Fate of Chemical Warfare Agents and Toxic Industrial Chemicals in Landfills: Supporting Information Shannon L. Bartelt-Hunt, Morton A. Barlaz *, Detlef R.U. Knappe, and Peter Kjeldsen *Corresponding Author. Department of Civil, Construction, and Environmental Engineering, Campus Box 7908, North Carolina State University, Raleigh, NC 27695-7908; Tel. (919) 515- 7676, Fax (919) 515-7908, [email protected]Summary: chemical agent classification, environmental fate of chemical agents, physical- chemical property data for additional TICs, CWAs and their hydrolysates, description of MOCLA and derivation of liner diffusion term, rationale for MOCLA input parameter selection, ranges of K H and log K ow for uncertainty analyses, effect of biodegradation and climate on contaminant fate.
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Fate of Chemical Warfare Agents and Toxic Industrial Chemicals in
Landfills Supporting Information
Shannon L Bartelt-Hunt Morton A Barlaz Detlef RU Knappe and Peter Kjeldsen
Corresponding Author Department of Civil Construction and Environmental Engineering
Campus Box 7908 North Carolina State University Raleigh NC 27695-7908 Tel (919) 515-
7676 Fax (919) 515-7908 barlazeosncsuedu
Summary chemical agent classification environmental fate of chemical agents physical-
chemical property data for additional TICs CWAs and their hydrolysates description of
MOCLA and derivation of liner diffusion term rationale for MOCLA input parameter selection
ranges of KH and log Kow for uncertainty analyses effect of biodegradation and climate on
contaminant fate
S2
Chemical Agent Classification Blister agents include sulfur mustard (HD) nitrogen mustard
(HN-2) lewisite (L) ethyldichloroarsine (ED) and phosgene oxime (CX) Exposure to these
agents damages the respiratory tract when inhaled and causes vomiting and diarrhea when
absorbed (1) Most blood agents are cyanide-containing compounds They poison the
cytochrome oxidase system resulting in a lack of cell respiration and the normal transfer of
oxygen from the blood to body tissues (2) Nerve agents are highly toxic with a lethal
concentration (LD50) of approximately 01 mgkg (3) The toxicity of nerve agents arises from
their ability to irreversibly inhibit acetylcholinesterase an enzyme involved in the proper
functioning of nerves and muscles (1) Nerve agents include tabun (GA) sarin (GB) soman
(GD) GE cyclohexyl sarin (GF) amiton (VG) VM and VX
Environmental Fate of Chemical Agents In landfills the behavior of organic contaminants is
influenced by the combined effects of biodegradation sorption transport in the gas andor liquid
phases (ie volatilization and leaching) and abiotic transformation such as hydrolysis (4-8)
Many CWAs hydrolyze in aqueous systems with half-lives on the order of minutes to days A
hydrolysis half-life of 85 min has been reported for HD in aqueous systems (9) however the
overall rate of HD disappearance is often limited by the slow rate of HD dissolution from a non-
aqueous phase into water Also hydrolysis products can coat the surface of HD droplets and
retard HD dissolution (10) Both its hydrophobicity and the formation of hydrolysis products
make non-aqueous-phase HD fairly persistent in the environment HD hydrolysis can occur via
two pathways that are dependent on water availability but the dominant products of either
pathway are thiodiglycol (TDG) and hydrochloric acid (10) Like HD the principal
environmental fate pathway of HN-2 is hydrolysis A hydrolysis half-life of 11 h has been
calculated for HN-2 at 25degC in a 667 acetone-water solution (11) The primary hydrolysate is
S3
the hydrochloride form of 2-(2-chloroethyl) methylamino ethanol which is highly toxic by the
oral route in rats and mice (10)
Hydrolysis rates of nerve agents are slower than those of HD or HN-2 with half-lives of 14-
28 h at pH 7 and 25degC 39 h at pH 75 and 25degC and 60 h at pH 6 and 25degC for GA GB and
GD respectively (10 12) The primary product of GA hydrolysis is phosphoric acid and the
primary product of GB and GD hydrolysis is methylphosphonic acid (MPA) (3 13) Hydrolysis
of VX is slower than that of the G-agents with a reported half-life of 17-42 d at 25degC and pH 7
(14) The hydrolysis products are pH-dependent but S-(2-diisopropylaminoethyl) methyl
phosphonothioate (EA2192) and ethanol are formed at pH 7 to 10 (3) EA2192 has
anticholinesterase activity that is similar to that of VX (10)
The rate of CWA hydrolysis is dependent on such factors as temperature pH and water
quality Hydrolysis rates increase with increasing temperature For example the rate of HD
hydrolysis at 70degC was 28 times that at 30degC (15) For GB at pH 7 hydrolysis half-lives of 2650
h and 39-41 h were reported at 0degC and 25degC respectively (14) The effect of pH on CWA
hydrolysis varies eg GD hydrolysis is acid-catalyzed with half-lives of 3 50 and 60 hr at pH 2
76 and 9 respectively (14) while VX hydrolysis is base-catalyzed with half-lives of 2400 17
and 002 d at pH 2-3 11 and 14 respectively (14) The hydrolysis rate of HD does not vary
between pH 5 and 10 (14) which covers the typical pH range for landfill leachate High chloride
ion concentrations can inhibit HD hydrolysis (16) an observation that is likely important in a
landfill environment because of the relatively high chloride concentrations in landfill leachates
(17) GA and GB hydrolysis rates were enhanced by the presence of dissolved oxygen and
cations such as Cu2+ Ca2+ Al3+ Mg2+ and Mn2+ (14)
S4
Sorption to organic waste constituents retards the transport of organic contaminants in
landfills Municipal solid waste (MSW) is ~50 cellulose 10-15 hemicellulose and 15-20
lignin (18 19) In addition MSW contains ~10 plastics In terms of elemental composition
MSW is about 50 organic carbon (18 19) therefore a large fraction of MSW represents a
sorbent for organic compounds For many MSW constituents sorption of neutral organic
contaminants can be described by a partitioning model (48) and the sorption capacity of an
organic MSW constituent increases with increasing sorbent hydrophobicity (8) and sorbate
octanol-water partition coefficient log Kow (4) For ionizable CWAs it was assumed that only
the neutral species sorbs appreciably for octanol-water systems this assumption is valid up to
several pH units above the pKa of organic acids (20)
Although biodegradation of CWAs is theoretically possible biodegradation of many CWAs
has not been observed due to their toxicity (10) Assuming that CWA-exposed building debris
will be decontaminated prior to disposal some anaerobic degradation may occur in landfills if
CWAs are present at low aqueous-phase concentrations It is more likely that biodegradation of
CWA hydrolysates will occur because CWAs hydrolyze rapidly and hydrolysates generally have
reduced toxicity relative to the original agents Only one study was identified that investigated
the anaerobic biodegradability of CWA hydrolysates Skylar et al (21) reported 42
degradation of TDG (HD hydrolysate) by an anaerobic sludge inoculum after 185 d The
addition of co-substrates (volatile fatty acids glucose) reduced the TDG half-life to less than 30
d
Physical-Chemical Data for additional CWAs Evaluation of the transport of a number of
additional CWAs was performed using MOCLA A complete list of all CWAs evaluated is
S5
presented in Table S1 Physical-chemical property data for CWAs and TICs not presented in
Table 2 of the manuscript are given in Table S2
S6
Description of MOCLA model and derivation of liner diffusion term
Box S1 Equations of the original MOCLA model
The total concentration of the chemical CT (g chemical m-3 landfill) at any time t is calculated with
⎟⎟⎠
⎞⎜⎜⎝
⎛sdotminus= t
RkCC
aTT exp0 (S1)
where CT0 is the initial total concentration of the chemical (g chemical m-3 landfill) at t=0
H
w
Ha KHK
Nqk λε++= (S2)
Ra is the retardation factor
aH
wococba K
KfR εερ+
+sdotsdot= (S3)
qa is the specific gas flow (see Box S2) N is the annual net precipitation (m yr-1) H is the depth of waste (m) KH is the dimensionless Henryrsquos Law constant foc is the fraction of organic carbon in the dry waste Koc is the distribution coefficient between solid organic carbon and water (see Box S2) λ is the first order transformation constant (yr-1) ρb is the dry bulk density of the dry waste in the landfill (tonne dry waste m-3 landfill) εw is the volumetric moisture content in the landfill (m3 water m-3 landfill) εa is the volumetric air content in the landfill (m3 air m-3 landfill)
The transport of chemicals via landfill gas (Fa) diffusion through the top cover (Fgd) and leachate (Fw) is calculated with the following equations
)(tCR
VqF Ta
aa sdot=
)()( tCRQtF T
a
Dgd sdot= )()( tC
RKNAtF T
aHw sdot= (S4) (S5) (S6)
where QD = VqD (see Box S2)
S7
Box S2 Additional MOCLA equations
The sum of the specific gas production rate and diffusional lsquoflowrsquo is combined into a specific gas flow qa
rsquo qa
rsquo = qa + qD (S7) where qa is the specific gas production rate (m-3 landfill gas m-3 waste yr-1) and qD the diffusional lsquoflowrsquo is calculated from
LV
ADq
SC
airSCaD 2
310
εε
= (S8)
Dair is the molecular diffusion coefficient of the chemical in air (m2 yr-1) εSC is the total porosity of the soil cover (m3 pore space m-3 soil cover) εaSC is the volumetric content of air in the soil cover (m3 air m-3 soil cover) L is the thickness of the soil cover (m) A is the surface area of the landfill (m2) V is the total volume of waste in the landfill (m3)
For neutral compounds Koc the distribution coefficient between solid organic carbon and water is calculated from
log Koc = 072log Kow+049 (S9) where Kow is the octanol-water distribution coefficient (dimensionless)
For organic bases (tertiary amines) Koc (pH) the pH-dependent distribution coefficient is calculated from (20)
Koc (pH) = (1-α) Koc (S10) where Koc is the distribution coefficient for the neutral compound and α the fraction of the non-dissociated (cationic) species is calculated from
α = 1(1+10(pH-pKa)) (S11)
S8
Box S3 Incorporation of liner diffusion term into MOCLA
In addition to the processes originally modeled by MOCLA a term was incorporated to evaluate diffusion through the composite liner The diffusive flux through the liner can be expressed by
xCDJ Diff partpart
= (S12)
where JDiff is the diffusive flux through the liner (g m-2 yr-1) D is the diffusion coefficient in the soil cover partCpartx is the concentration gradient (g m-4)
The diffusion coefficient (D) in eqn S12 is the effective diffusion coefficient for the composite geomembraneclay liner It was assumed that the geomembrane layer does not impede the diffusive flux through the composite liner as volatile organic compounds have been shown to penetrate geomembranes at an appreciable rate (22) Therefore the diffusion coefficient for the composite liner was represented by the effective diffusion coefficient for the clay layer Since clay liners are typically compacted at a moisture content less than saturation diffusion will occur through both the air-filled and water-filled pore spaces within the clay In a porous medium the effective diffusion coefficient for each phase (D
air or D
water) is calculated from the molecular diffusivity of the compound in air or water (Dair or Dwater) the total porosity of the clay liner (εL) and the air- or water-filled porosity of the liner (εaL or εwL) One commonly-used expression is the Millington equation which relates the effective diffusion coefficient to the molecular diffusion coefficient by (23)
2
333
L
Laairair DD
ε
ε= (S13)
and
2
333
L
Lwwaterwater DD
ε
ε= (S14)
S9
Box S3 (continued) Incorporation of liner diffusion term into MOCLA
Combining expressions S13 and S14 along with Henryrsquos Law results in the following equation for the diffusive flux through the liner (24)
x
CK
DDJ a
L
Lw
H
water
L
LaairDiff part
part⎟⎟⎠
⎞⎜⎜⎝
⎛+= 2
333
2
333
ε
ε
ε
ε (S15)
where Ca is equal to the gas-phase concentration of the contaminant If it is assumed that the concentration of the contaminant of interest in the aquifer beneath the liner is equal to zero then the sink due to diffusion through the composite liner may be written as
liner
a
L
Lw
H
water
L
LaairDiff L
CA
KD
DS ⎟⎟⎠
⎞⎜⎜⎝
⎛+= 2
333
2
333
ε
ε
ε
ε (S16)
where SDiff is the sink due to diffusion through the liner (g yr-1) Lliner is the thickness of the clay layer of the composite liner (m) SDiff can be simplified to SDiff = QD linerCa (S17) where
liner
effLinerD L
ADQ = (S18)
and
2
333
2
333
L
Lw
H
water
L
Laaireff K
DDD
ε
ε
ε
ε+= (S19)
Because literature values for εaSC and εaL were not available these terms were calculated as
)0max( scscbscSCa MCsdotminus= ρεε (S20) and
)0max( LLbLLa MCsdotminus= ρεε (S21) where εsc and εL are the total porosity of the soil cover and liner (m3 voids m-3 cover or liner) ρbSC and ρbL are the dry bulk density of the soil cover and liner (g soil m-3 cover or liner) MCSC and MCL are the gravimetric moisture content of the soil cover and liner ()
S10
Box S3 (continued) Incorporation of liner diffusion term into MOCLA
Including the diffusive flux term into the original MOCLA mass balance equation gives
( )diffwgdaT SSSSS
dtVCd
++++minus= λ)( (S22)
rearranging this expression gives
⎟⎟⎠
⎞⎜⎜⎝
⎛+++minus=
VQ
KHKNq
dtdC linerD
H
w
Ha
T λε (S23)
if qrsquo
D liner = QD liner V then a new expression for k can be written
linerD
H
w
Ha q
KHKNqk +++=
λε (S24)
Integrating each term on the right-hand side of eqn S22 gives the expressions for the fate routes The new expression for fate via liner diffusion is written as
))exp(1( t
RkqF
alinerDdiff minusminus= (S23)
S11
Methodology used to determine MOCLA input parameter values (physical parameters)
To evaluate the distribution and fate of chemicals in a landfill data for a number of input
parameters describing the landfill design and operation are required This section describes each
parameter and provides an explanation of how parameter values that could be applicable under
various disposal scenarios were determined
Dry bulk density of the waste ρb (T m-3) It is assumed that the building debris will be contained
for transport and burial and therefore will not be compacted after placement in the landfill
Therefore the wet bulk density of the building debris will likely be lower than the average value
of wet bulk density for compacted waste which is about 076 T m-3 The range of wet bulk
densities to be used in the bounding calculations was 042 to 070 T m-3 with an average value of
055 T m-3
The dry bulk density was determined from the wet bulk density and an estimate of the
gravimetric moisture content of the waste If the gravimetric moisture content (MC) of the waste
is assumed to be 10-20 (wet weight basis) then the dry bulk density can be calculated as
follows
Using a design basis of 1 m3 of refuse the total mass of waste is equal to 042 T which
corresponds to the low end of the range The mass of water in 1 m3 of refuse is equal to 042
times 020 (highest possible value of MC) or 0084 T The total mass of waste minus the mass of
water (042 - 0084) results in the mass of dry refuse which is 034 T Therefore the low value
of the range for dry bulk density is 034 T m-3 Similarly the high end of the range is 063 T m-3
The average value is 049 T m-3
Volumetric moisture content of the waste εw (m3 water m-3 LF) The possible values of
volumetric moisture content of the waste can be calculated from the ranges of the wet bulk
S12
density and the gravimetric moisture content assuming 1 m3 of waste The lowest value in the
range of volumetric moisture contents is calculated at 10 gravimetric moisture The mass of
water in 1 m3 of waste is 042 T (total mass) times 010 (mass of watertotal mass) which is 0042
T The density of water is 1 T m-3 so the volumetric moisture content is equal to 0042 m3 water
m-3 LF Similarly the highest value in the range is 014 m3 water m-3 LF which is equivalent to
070 T times 020 The average volumetric moisture content is 0091 m3 water m-3 LF
Volumetric gas content of the waste εa (m3 airm3 LF) A range of 010 to 040 was assumed for
the volumetric gas content of the waste There is very little data on measured values of the
effective porosity of waste Bendz et al (25) reported a measured value of 012 for a waste
sample from an operating MSW landfill Based on the range specified above the average value
for the volumetric gas content of the waste is 025
Fraction of organic carbon foc A range of 040 to 060 was used for the fraction of organic
carbon in the waste A value of 050 was reported for a sample of MSW (26) which will be used
as the average value in the bounding calculations
Height of the waste in the landfill H (m) The height of waste in the landfill is assumed to vary
between 183 and 61 m Based on this range the average height of waste in the landfill was 397
m
The final two terms required to describe the landfill infiltration and the gas production rate
are a function of the climate in which the landfill is located As a result two sets of values for
these parameters were used to represent an arid or a wet climate
Net precipitation N (myear) The net precipitation or infiltration was calculated based on data
reported in Camobreco et al (27) For the arid climate scenario data from sites with less than
05 m yr-1 of total precipitation were used while the data from sites with greater than or equal to
S13
05 m yr-1 were used for the wet climate scenario For each site the total precipitation was
multiplied by the percentage of precipitation that becomes leachate to determine the net
precipitation or infiltration Using this method infiltration for the arid climate was found to
range from 002 to 005 m yr-1 with an average value of 004 m yr-1 Infiltration for the wet
climate ranged from 004 to 032 m yr-1 with an average of 012 m yr-1 Although the data used
to generate these estimates encompassed a variety of different percentages of final cover it
should be noted that modeling a dry (fully capped) landfill is potentially a more realistic scenario
than a wet landfill since the building debris will likely be encapsulated and the greatest
likelihood for leakage from the containers will occur after the final cover has been placed when
infiltration is minimal
Gas production rate qa (m3 LFG m-3 LF yr-1) The landfill gas (LFG) production rate can be
described by the following equation (28)
qa=2WLoke-kt (S24)
where W is the mass of refuse Lo is a term representing the ultimate volume of methane gas
produced per unit of wet waste and k is a rate constant (yr-1) Equation S24 assumes a methane
concentration of 50 in LFG
The mass of refuse (W) is a function of the bulk density of the waste which as stated above
was assumed to vary from 042 to 070 T m-3 with an average value of 055 T m-3 Assuming 1
m3 of waste W will be equal to 055 T Lo was assumed to vary between 85 and 170 L methane
kg-1 wet waste The value of 170 L methane kg-1 wet waste is the default used in the New
Source Performance Standards of the Clean Air Act amendments (29) For the arid climate
scenario the rate constant (k) was set to 002 yr-1 For the wet climate scenario the rate constant
(k) was set to 005 yr-1 For the arid scenario qa was found to range from 19 to 37 m3 LFG m-3
S14
LF yr-1 with an average value of 28 m3 LFG m-3 LF yr-1 For the wet scenario qa was found to
range from 45 to 90 m3 LFG m-3 LF yr-1 with an average value of 675 m3 LFG m-3 LF yr-1
Thickness of cover L (m) The thickness of the landfill cover was set to 045 m which is the
minimum thickness specified by Subtitle D regulation for the thickness of the barrier layer (30)
This value was not varied in the bounding calculations
Total porosity of the soil cover εsc (dimensionless) The total porosity of the soil cover ranged
from 03 to 05 with an average value of 04 A total porosity between 03 and 05 is common for
a wide range of soil types
Gravimetric moisture content of soil cover (MCSC) The gravimetric moisture content of the soil
cover ranged from 103 to 308 (dry weight basis) with an average value of 200 based
published data (31)
Dry bulk density of the cover soil ρbSC (g cm-3) The dry bulk density of the soil cover ranged
from 13 to 20 g cm-3 with an average value of 17 g cm-3 based on published data (31) It
should be noted that the gravimetric moisture content and dry bulk density of the cover soil are
not used directly in MOCLA These parameters are used along with the porosity of the cover
soil to calculate the air-filled porosity of the cover soil which is an input parameter to MOCLA
Liner thickness Lliner (m) The thickness of the landfill liner was set to 06 m which is the
minimum thickness required by EPA Subtitle D regulation (30) The liner thickness was not
varied in the bounding calculations
Total porosity of the liner εL (dimensionless) The total porosity of the liner ranged from 03 to
05 with an average value of 04 A total porosity between 03 and 05 is common for a wide
range of soil types
S15
Gravimetric moisture content of the liner (MCL) Based on published data (31) the gravimetric
moisture content of the liner ranged from 103 to 308 with an average value of 200
Dry bulk density of the liner materials ρb L (g cm-3) Based on published data (31) the dry bulk
density of the liner ranged from 13 to 20 g cm-3 with an average value of 17 g cm-3 It should
be noted that the gravimetric moisture content and dry bulk density of the liner are not used
directly in MOCLA These parameters are used along with the porosity of the liner to calculate
the air-filled porosity of the liner which is an input parameter to MOCLA
S16
Table S1 List of Studied CWAs and TICs Military
Designation Common Name Chemical Formula CAS number Use
Carbon disulfide CS2 75-15-0 Toxic Industrial Chemical
Furan C4H4O 110-00-9 Toxic Industrial Chemical
HHD Mustard Gas C4H8Cl2S 505-60-2 Blister AgentVesicant
a Data compiled from the following sources (10 32-39) b Estimated with EPISuite v312 (40) c Hydrolysis rate estimated to be on the order of 10 min-1 at 20degC (41) d Hydrolysis half-life for ED estimated to be equal to that of L based on structural similarity e Half-life calculated based on 5 disappearance after 6 d (2) f Value estimated by averaging hydrolysis half-lives of GA GB and GD g Hydrolysis half-life estimated to be equal to that of VX based on structural similarity h Temperature not reported i Estimated using Wilke-Lee equation (42) j Estimated using Hayduk-Laudie equation (42) k pKa for CX estimated from a range of calculated pKa values for chloro-substituted oximes (43) l Estimated using Chem-Silico software package (44) m pKa for VG and VM estimated to be equivalent to that of VX MW is molecular weight bp is boiling point fp is freezing point KH is the Henryrsquos Law constant Kow is the octanol-water partition coefficient
S18Table S3 Henryrsquos law constant ranges for organic compounds originally modeled in MOCLA
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S2
Chemical Agent Classification Blister agents include sulfur mustard (HD) nitrogen mustard
(HN-2) lewisite (L) ethyldichloroarsine (ED) and phosgene oxime (CX) Exposure to these
agents damages the respiratory tract when inhaled and causes vomiting and diarrhea when
absorbed (1) Most blood agents are cyanide-containing compounds They poison the
cytochrome oxidase system resulting in a lack of cell respiration and the normal transfer of
oxygen from the blood to body tissues (2) Nerve agents are highly toxic with a lethal
concentration (LD50) of approximately 01 mgkg (3) The toxicity of nerve agents arises from
their ability to irreversibly inhibit acetylcholinesterase an enzyme involved in the proper
functioning of nerves and muscles (1) Nerve agents include tabun (GA) sarin (GB) soman
(GD) GE cyclohexyl sarin (GF) amiton (VG) VM and VX
Environmental Fate of Chemical Agents In landfills the behavior of organic contaminants is
influenced by the combined effects of biodegradation sorption transport in the gas andor liquid
phases (ie volatilization and leaching) and abiotic transformation such as hydrolysis (4-8)
Many CWAs hydrolyze in aqueous systems with half-lives on the order of minutes to days A
hydrolysis half-life of 85 min has been reported for HD in aqueous systems (9) however the
overall rate of HD disappearance is often limited by the slow rate of HD dissolution from a non-
aqueous phase into water Also hydrolysis products can coat the surface of HD droplets and
retard HD dissolution (10) Both its hydrophobicity and the formation of hydrolysis products
make non-aqueous-phase HD fairly persistent in the environment HD hydrolysis can occur via
two pathways that are dependent on water availability but the dominant products of either
pathway are thiodiglycol (TDG) and hydrochloric acid (10) Like HD the principal
environmental fate pathway of HN-2 is hydrolysis A hydrolysis half-life of 11 h has been
calculated for HN-2 at 25degC in a 667 acetone-water solution (11) The primary hydrolysate is
S3
the hydrochloride form of 2-(2-chloroethyl) methylamino ethanol which is highly toxic by the
oral route in rats and mice (10)
Hydrolysis rates of nerve agents are slower than those of HD or HN-2 with half-lives of 14-
28 h at pH 7 and 25degC 39 h at pH 75 and 25degC and 60 h at pH 6 and 25degC for GA GB and
GD respectively (10 12) The primary product of GA hydrolysis is phosphoric acid and the
primary product of GB and GD hydrolysis is methylphosphonic acid (MPA) (3 13) Hydrolysis
of VX is slower than that of the G-agents with a reported half-life of 17-42 d at 25degC and pH 7
(14) The hydrolysis products are pH-dependent but S-(2-diisopropylaminoethyl) methyl
phosphonothioate (EA2192) and ethanol are formed at pH 7 to 10 (3) EA2192 has
anticholinesterase activity that is similar to that of VX (10)
The rate of CWA hydrolysis is dependent on such factors as temperature pH and water
quality Hydrolysis rates increase with increasing temperature For example the rate of HD
hydrolysis at 70degC was 28 times that at 30degC (15) For GB at pH 7 hydrolysis half-lives of 2650
h and 39-41 h were reported at 0degC and 25degC respectively (14) The effect of pH on CWA
hydrolysis varies eg GD hydrolysis is acid-catalyzed with half-lives of 3 50 and 60 hr at pH 2
76 and 9 respectively (14) while VX hydrolysis is base-catalyzed with half-lives of 2400 17
and 002 d at pH 2-3 11 and 14 respectively (14) The hydrolysis rate of HD does not vary
between pH 5 and 10 (14) which covers the typical pH range for landfill leachate High chloride
ion concentrations can inhibit HD hydrolysis (16) an observation that is likely important in a
landfill environment because of the relatively high chloride concentrations in landfill leachates
(17) GA and GB hydrolysis rates were enhanced by the presence of dissolved oxygen and
cations such as Cu2+ Ca2+ Al3+ Mg2+ and Mn2+ (14)
S4
Sorption to organic waste constituents retards the transport of organic contaminants in
landfills Municipal solid waste (MSW) is ~50 cellulose 10-15 hemicellulose and 15-20
lignin (18 19) In addition MSW contains ~10 plastics In terms of elemental composition
MSW is about 50 organic carbon (18 19) therefore a large fraction of MSW represents a
sorbent for organic compounds For many MSW constituents sorption of neutral organic
contaminants can be described by a partitioning model (48) and the sorption capacity of an
organic MSW constituent increases with increasing sorbent hydrophobicity (8) and sorbate
octanol-water partition coefficient log Kow (4) For ionizable CWAs it was assumed that only
the neutral species sorbs appreciably for octanol-water systems this assumption is valid up to
several pH units above the pKa of organic acids (20)
Although biodegradation of CWAs is theoretically possible biodegradation of many CWAs
has not been observed due to their toxicity (10) Assuming that CWA-exposed building debris
will be decontaminated prior to disposal some anaerobic degradation may occur in landfills if
CWAs are present at low aqueous-phase concentrations It is more likely that biodegradation of
CWA hydrolysates will occur because CWAs hydrolyze rapidly and hydrolysates generally have
reduced toxicity relative to the original agents Only one study was identified that investigated
the anaerobic biodegradability of CWA hydrolysates Skylar et al (21) reported 42
degradation of TDG (HD hydrolysate) by an anaerobic sludge inoculum after 185 d The
addition of co-substrates (volatile fatty acids glucose) reduced the TDG half-life to less than 30
d
Physical-Chemical Data for additional CWAs Evaluation of the transport of a number of
additional CWAs was performed using MOCLA A complete list of all CWAs evaluated is
S5
presented in Table S1 Physical-chemical property data for CWAs and TICs not presented in
Table 2 of the manuscript are given in Table S2
S6
Description of MOCLA model and derivation of liner diffusion term
Box S1 Equations of the original MOCLA model
The total concentration of the chemical CT (g chemical m-3 landfill) at any time t is calculated with
⎟⎟⎠
⎞⎜⎜⎝
⎛sdotminus= t
RkCC
aTT exp0 (S1)
where CT0 is the initial total concentration of the chemical (g chemical m-3 landfill) at t=0
H
w
Ha KHK
Nqk λε++= (S2)
Ra is the retardation factor
aH
wococba K
KfR εερ+
+sdotsdot= (S3)
qa is the specific gas flow (see Box S2) N is the annual net precipitation (m yr-1) H is the depth of waste (m) KH is the dimensionless Henryrsquos Law constant foc is the fraction of organic carbon in the dry waste Koc is the distribution coefficient between solid organic carbon and water (see Box S2) λ is the first order transformation constant (yr-1) ρb is the dry bulk density of the dry waste in the landfill (tonne dry waste m-3 landfill) εw is the volumetric moisture content in the landfill (m3 water m-3 landfill) εa is the volumetric air content in the landfill (m3 air m-3 landfill)
The transport of chemicals via landfill gas (Fa) diffusion through the top cover (Fgd) and leachate (Fw) is calculated with the following equations
)(tCR
VqF Ta
aa sdot=
)()( tCRQtF T
a
Dgd sdot= )()( tC
RKNAtF T
aHw sdot= (S4) (S5) (S6)
where QD = VqD (see Box S2)
S7
Box S2 Additional MOCLA equations
The sum of the specific gas production rate and diffusional lsquoflowrsquo is combined into a specific gas flow qa
rsquo qa
rsquo = qa + qD (S7) where qa is the specific gas production rate (m-3 landfill gas m-3 waste yr-1) and qD the diffusional lsquoflowrsquo is calculated from
LV
ADq
SC
airSCaD 2
310
εε
= (S8)
Dair is the molecular diffusion coefficient of the chemical in air (m2 yr-1) εSC is the total porosity of the soil cover (m3 pore space m-3 soil cover) εaSC is the volumetric content of air in the soil cover (m3 air m-3 soil cover) L is the thickness of the soil cover (m) A is the surface area of the landfill (m2) V is the total volume of waste in the landfill (m3)
For neutral compounds Koc the distribution coefficient between solid organic carbon and water is calculated from
log Koc = 072log Kow+049 (S9) where Kow is the octanol-water distribution coefficient (dimensionless)
For organic bases (tertiary amines) Koc (pH) the pH-dependent distribution coefficient is calculated from (20)
Koc (pH) = (1-α) Koc (S10) where Koc is the distribution coefficient for the neutral compound and α the fraction of the non-dissociated (cationic) species is calculated from
α = 1(1+10(pH-pKa)) (S11)
S8
Box S3 Incorporation of liner diffusion term into MOCLA
In addition to the processes originally modeled by MOCLA a term was incorporated to evaluate diffusion through the composite liner The diffusive flux through the liner can be expressed by
xCDJ Diff partpart
= (S12)
where JDiff is the diffusive flux through the liner (g m-2 yr-1) D is the diffusion coefficient in the soil cover partCpartx is the concentration gradient (g m-4)
The diffusion coefficient (D) in eqn S12 is the effective diffusion coefficient for the composite geomembraneclay liner It was assumed that the geomembrane layer does not impede the diffusive flux through the composite liner as volatile organic compounds have been shown to penetrate geomembranes at an appreciable rate (22) Therefore the diffusion coefficient for the composite liner was represented by the effective diffusion coefficient for the clay layer Since clay liners are typically compacted at a moisture content less than saturation diffusion will occur through both the air-filled and water-filled pore spaces within the clay In a porous medium the effective diffusion coefficient for each phase (D
air or D
water) is calculated from the molecular diffusivity of the compound in air or water (Dair or Dwater) the total porosity of the clay liner (εL) and the air- or water-filled porosity of the liner (εaL or εwL) One commonly-used expression is the Millington equation which relates the effective diffusion coefficient to the molecular diffusion coefficient by (23)
2
333
L
Laairair DD
ε
ε= (S13)
and
2
333
L
Lwwaterwater DD
ε
ε= (S14)
S9
Box S3 (continued) Incorporation of liner diffusion term into MOCLA
Combining expressions S13 and S14 along with Henryrsquos Law results in the following equation for the diffusive flux through the liner (24)
x
CK
DDJ a
L
Lw
H
water
L
LaairDiff part
part⎟⎟⎠
⎞⎜⎜⎝
⎛+= 2
333
2
333
ε
ε
ε
ε (S15)
where Ca is equal to the gas-phase concentration of the contaminant If it is assumed that the concentration of the contaminant of interest in the aquifer beneath the liner is equal to zero then the sink due to diffusion through the composite liner may be written as
liner
a
L
Lw
H
water
L
LaairDiff L
CA
KD
DS ⎟⎟⎠
⎞⎜⎜⎝
⎛+= 2
333
2
333
ε
ε
ε
ε (S16)
where SDiff is the sink due to diffusion through the liner (g yr-1) Lliner is the thickness of the clay layer of the composite liner (m) SDiff can be simplified to SDiff = QD linerCa (S17) where
liner
effLinerD L
ADQ = (S18)
and
2
333
2
333
L
Lw
H
water
L
Laaireff K
DDD
ε
ε
ε
ε+= (S19)
Because literature values for εaSC and εaL were not available these terms were calculated as
)0max( scscbscSCa MCsdotminus= ρεε (S20) and
)0max( LLbLLa MCsdotminus= ρεε (S21) where εsc and εL are the total porosity of the soil cover and liner (m3 voids m-3 cover or liner) ρbSC and ρbL are the dry bulk density of the soil cover and liner (g soil m-3 cover or liner) MCSC and MCL are the gravimetric moisture content of the soil cover and liner ()
S10
Box S3 (continued) Incorporation of liner diffusion term into MOCLA
Including the diffusive flux term into the original MOCLA mass balance equation gives
( )diffwgdaT SSSSS
dtVCd
++++minus= λ)( (S22)
rearranging this expression gives
⎟⎟⎠
⎞⎜⎜⎝
⎛+++minus=
VQ
KHKNq
dtdC linerD
H
w
Ha
T λε (S23)
if qrsquo
D liner = QD liner V then a new expression for k can be written
linerD
H
w
Ha q
KHKNqk +++=
λε (S24)
Integrating each term on the right-hand side of eqn S22 gives the expressions for the fate routes The new expression for fate via liner diffusion is written as
))exp(1( t
RkqF
alinerDdiff minusminus= (S23)
S11
Methodology used to determine MOCLA input parameter values (physical parameters)
To evaluate the distribution and fate of chemicals in a landfill data for a number of input
parameters describing the landfill design and operation are required This section describes each
parameter and provides an explanation of how parameter values that could be applicable under
various disposal scenarios were determined
Dry bulk density of the waste ρb (T m-3) It is assumed that the building debris will be contained
for transport and burial and therefore will not be compacted after placement in the landfill
Therefore the wet bulk density of the building debris will likely be lower than the average value
of wet bulk density for compacted waste which is about 076 T m-3 The range of wet bulk
densities to be used in the bounding calculations was 042 to 070 T m-3 with an average value of
055 T m-3
The dry bulk density was determined from the wet bulk density and an estimate of the
gravimetric moisture content of the waste If the gravimetric moisture content (MC) of the waste
is assumed to be 10-20 (wet weight basis) then the dry bulk density can be calculated as
follows
Using a design basis of 1 m3 of refuse the total mass of waste is equal to 042 T which
corresponds to the low end of the range The mass of water in 1 m3 of refuse is equal to 042
times 020 (highest possible value of MC) or 0084 T The total mass of waste minus the mass of
water (042 - 0084) results in the mass of dry refuse which is 034 T Therefore the low value
of the range for dry bulk density is 034 T m-3 Similarly the high end of the range is 063 T m-3
The average value is 049 T m-3
Volumetric moisture content of the waste εw (m3 water m-3 LF) The possible values of
volumetric moisture content of the waste can be calculated from the ranges of the wet bulk
S12
density and the gravimetric moisture content assuming 1 m3 of waste The lowest value in the
range of volumetric moisture contents is calculated at 10 gravimetric moisture The mass of
water in 1 m3 of waste is 042 T (total mass) times 010 (mass of watertotal mass) which is 0042
T The density of water is 1 T m-3 so the volumetric moisture content is equal to 0042 m3 water
m-3 LF Similarly the highest value in the range is 014 m3 water m-3 LF which is equivalent to
070 T times 020 The average volumetric moisture content is 0091 m3 water m-3 LF
Volumetric gas content of the waste εa (m3 airm3 LF) A range of 010 to 040 was assumed for
the volumetric gas content of the waste There is very little data on measured values of the
effective porosity of waste Bendz et al (25) reported a measured value of 012 for a waste
sample from an operating MSW landfill Based on the range specified above the average value
for the volumetric gas content of the waste is 025
Fraction of organic carbon foc A range of 040 to 060 was used for the fraction of organic
carbon in the waste A value of 050 was reported for a sample of MSW (26) which will be used
as the average value in the bounding calculations
Height of the waste in the landfill H (m) The height of waste in the landfill is assumed to vary
between 183 and 61 m Based on this range the average height of waste in the landfill was 397
m
The final two terms required to describe the landfill infiltration and the gas production rate
are a function of the climate in which the landfill is located As a result two sets of values for
these parameters were used to represent an arid or a wet climate
Net precipitation N (myear) The net precipitation or infiltration was calculated based on data
reported in Camobreco et al (27) For the arid climate scenario data from sites with less than
05 m yr-1 of total precipitation were used while the data from sites with greater than or equal to
S13
05 m yr-1 were used for the wet climate scenario For each site the total precipitation was
multiplied by the percentage of precipitation that becomes leachate to determine the net
precipitation or infiltration Using this method infiltration for the arid climate was found to
range from 002 to 005 m yr-1 with an average value of 004 m yr-1 Infiltration for the wet
climate ranged from 004 to 032 m yr-1 with an average of 012 m yr-1 Although the data used
to generate these estimates encompassed a variety of different percentages of final cover it
should be noted that modeling a dry (fully capped) landfill is potentially a more realistic scenario
than a wet landfill since the building debris will likely be encapsulated and the greatest
likelihood for leakage from the containers will occur after the final cover has been placed when
infiltration is minimal
Gas production rate qa (m3 LFG m-3 LF yr-1) The landfill gas (LFG) production rate can be
described by the following equation (28)
qa=2WLoke-kt (S24)
where W is the mass of refuse Lo is a term representing the ultimate volume of methane gas
produced per unit of wet waste and k is a rate constant (yr-1) Equation S24 assumes a methane
concentration of 50 in LFG
The mass of refuse (W) is a function of the bulk density of the waste which as stated above
was assumed to vary from 042 to 070 T m-3 with an average value of 055 T m-3 Assuming 1
m3 of waste W will be equal to 055 T Lo was assumed to vary between 85 and 170 L methane
kg-1 wet waste The value of 170 L methane kg-1 wet waste is the default used in the New
Source Performance Standards of the Clean Air Act amendments (29) For the arid climate
scenario the rate constant (k) was set to 002 yr-1 For the wet climate scenario the rate constant
(k) was set to 005 yr-1 For the arid scenario qa was found to range from 19 to 37 m3 LFG m-3
S14
LF yr-1 with an average value of 28 m3 LFG m-3 LF yr-1 For the wet scenario qa was found to
range from 45 to 90 m3 LFG m-3 LF yr-1 with an average value of 675 m3 LFG m-3 LF yr-1
Thickness of cover L (m) The thickness of the landfill cover was set to 045 m which is the
minimum thickness specified by Subtitle D regulation for the thickness of the barrier layer (30)
This value was not varied in the bounding calculations
Total porosity of the soil cover εsc (dimensionless) The total porosity of the soil cover ranged
from 03 to 05 with an average value of 04 A total porosity between 03 and 05 is common for
a wide range of soil types
Gravimetric moisture content of soil cover (MCSC) The gravimetric moisture content of the soil
cover ranged from 103 to 308 (dry weight basis) with an average value of 200 based
published data (31)
Dry bulk density of the cover soil ρbSC (g cm-3) The dry bulk density of the soil cover ranged
from 13 to 20 g cm-3 with an average value of 17 g cm-3 based on published data (31) It
should be noted that the gravimetric moisture content and dry bulk density of the cover soil are
not used directly in MOCLA These parameters are used along with the porosity of the cover
soil to calculate the air-filled porosity of the cover soil which is an input parameter to MOCLA
Liner thickness Lliner (m) The thickness of the landfill liner was set to 06 m which is the
minimum thickness required by EPA Subtitle D regulation (30) The liner thickness was not
varied in the bounding calculations
Total porosity of the liner εL (dimensionless) The total porosity of the liner ranged from 03 to
05 with an average value of 04 A total porosity between 03 and 05 is common for a wide
range of soil types
S15
Gravimetric moisture content of the liner (MCL) Based on published data (31) the gravimetric
moisture content of the liner ranged from 103 to 308 with an average value of 200
Dry bulk density of the liner materials ρb L (g cm-3) Based on published data (31) the dry bulk
density of the liner ranged from 13 to 20 g cm-3 with an average value of 17 g cm-3 It should
be noted that the gravimetric moisture content and dry bulk density of the liner are not used
directly in MOCLA These parameters are used along with the porosity of the liner to calculate
the air-filled porosity of the liner which is an input parameter to MOCLA
S16
Table S1 List of Studied CWAs and TICs Military
Designation Common Name Chemical Formula CAS number Use
Carbon disulfide CS2 75-15-0 Toxic Industrial Chemical
Furan C4H4O 110-00-9 Toxic Industrial Chemical
HHD Mustard Gas C4H8Cl2S 505-60-2 Blister AgentVesicant
a Data compiled from the following sources (10 32-39) b Estimated with EPISuite v312 (40) c Hydrolysis rate estimated to be on the order of 10 min-1 at 20degC (41) d Hydrolysis half-life for ED estimated to be equal to that of L based on structural similarity e Half-life calculated based on 5 disappearance after 6 d (2) f Value estimated by averaging hydrolysis half-lives of GA GB and GD g Hydrolysis half-life estimated to be equal to that of VX based on structural similarity h Temperature not reported i Estimated using Wilke-Lee equation (42) j Estimated using Hayduk-Laudie equation (42) k pKa for CX estimated from a range of calculated pKa values for chloro-substituted oximes (43) l Estimated using Chem-Silico software package (44) m pKa for VG and VM estimated to be equivalent to that of VX MW is molecular weight bp is boiling point fp is freezing point KH is the Henryrsquos Law constant Kow is the octanol-water partition coefficient
S18Table S3 Henryrsquos law constant ranges for organic compounds originally modeled in MOCLA
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S3
the hydrochloride form of 2-(2-chloroethyl) methylamino ethanol which is highly toxic by the
oral route in rats and mice (10)
Hydrolysis rates of nerve agents are slower than those of HD or HN-2 with half-lives of 14-
28 h at pH 7 and 25degC 39 h at pH 75 and 25degC and 60 h at pH 6 and 25degC for GA GB and
GD respectively (10 12) The primary product of GA hydrolysis is phosphoric acid and the
primary product of GB and GD hydrolysis is methylphosphonic acid (MPA) (3 13) Hydrolysis
of VX is slower than that of the G-agents with a reported half-life of 17-42 d at 25degC and pH 7
(14) The hydrolysis products are pH-dependent but S-(2-diisopropylaminoethyl) methyl
phosphonothioate (EA2192) and ethanol are formed at pH 7 to 10 (3) EA2192 has
anticholinesterase activity that is similar to that of VX (10)
The rate of CWA hydrolysis is dependent on such factors as temperature pH and water
quality Hydrolysis rates increase with increasing temperature For example the rate of HD
hydrolysis at 70degC was 28 times that at 30degC (15) For GB at pH 7 hydrolysis half-lives of 2650
h and 39-41 h were reported at 0degC and 25degC respectively (14) The effect of pH on CWA
hydrolysis varies eg GD hydrolysis is acid-catalyzed with half-lives of 3 50 and 60 hr at pH 2
76 and 9 respectively (14) while VX hydrolysis is base-catalyzed with half-lives of 2400 17
and 002 d at pH 2-3 11 and 14 respectively (14) The hydrolysis rate of HD does not vary
between pH 5 and 10 (14) which covers the typical pH range for landfill leachate High chloride
ion concentrations can inhibit HD hydrolysis (16) an observation that is likely important in a
landfill environment because of the relatively high chloride concentrations in landfill leachates
(17) GA and GB hydrolysis rates were enhanced by the presence of dissolved oxygen and
cations such as Cu2+ Ca2+ Al3+ Mg2+ and Mn2+ (14)
S4
Sorption to organic waste constituents retards the transport of organic contaminants in
landfills Municipal solid waste (MSW) is ~50 cellulose 10-15 hemicellulose and 15-20
lignin (18 19) In addition MSW contains ~10 plastics In terms of elemental composition
MSW is about 50 organic carbon (18 19) therefore a large fraction of MSW represents a
sorbent for organic compounds For many MSW constituents sorption of neutral organic
contaminants can be described by a partitioning model (48) and the sorption capacity of an
organic MSW constituent increases with increasing sorbent hydrophobicity (8) and sorbate
octanol-water partition coefficient log Kow (4) For ionizable CWAs it was assumed that only
the neutral species sorbs appreciably for octanol-water systems this assumption is valid up to
several pH units above the pKa of organic acids (20)
Although biodegradation of CWAs is theoretically possible biodegradation of many CWAs
has not been observed due to their toxicity (10) Assuming that CWA-exposed building debris
will be decontaminated prior to disposal some anaerobic degradation may occur in landfills if
CWAs are present at low aqueous-phase concentrations It is more likely that biodegradation of
CWA hydrolysates will occur because CWAs hydrolyze rapidly and hydrolysates generally have
reduced toxicity relative to the original agents Only one study was identified that investigated
the anaerobic biodegradability of CWA hydrolysates Skylar et al (21) reported 42
degradation of TDG (HD hydrolysate) by an anaerobic sludge inoculum after 185 d The
addition of co-substrates (volatile fatty acids glucose) reduced the TDG half-life to less than 30
d
Physical-Chemical Data for additional CWAs Evaluation of the transport of a number of
additional CWAs was performed using MOCLA A complete list of all CWAs evaluated is
S5
presented in Table S1 Physical-chemical property data for CWAs and TICs not presented in
Table 2 of the manuscript are given in Table S2
S6
Description of MOCLA model and derivation of liner diffusion term
Box S1 Equations of the original MOCLA model
The total concentration of the chemical CT (g chemical m-3 landfill) at any time t is calculated with
⎟⎟⎠
⎞⎜⎜⎝
⎛sdotminus= t
RkCC
aTT exp0 (S1)
where CT0 is the initial total concentration of the chemical (g chemical m-3 landfill) at t=0
H
w
Ha KHK
Nqk λε++= (S2)
Ra is the retardation factor
aH
wococba K
KfR εερ+
+sdotsdot= (S3)
qa is the specific gas flow (see Box S2) N is the annual net precipitation (m yr-1) H is the depth of waste (m) KH is the dimensionless Henryrsquos Law constant foc is the fraction of organic carbon in the dry waste Koc is the distribution coefficient between solid organic carbon and water (see Box S2) λ is the first order transformation constant (yr-1) ρb is the dry bulk density of the dry waste in the landfill (tonne dry waste m-3 landfill) εw is the volumetric moisture content in the landfill (m3 water m-3 landfill) εa is the volumetric air content in the landfill (m3 air m-3 landfill)
The transport of chemicals via landfill gas (Fa) diffusion through the top cover (Fgd) and leachate (Fw) is calculated with the following equations
)(tCR
VqF Ta
aa sdot=
)()( tCRQtF T
a
Dgd sdot= )()( tC
RKNAtF T
aHw sdot= (S4) (S5) (S6)
where QD = VqD (see Box S2)
S7
Box S2 Additional MOCLA equations
The sum of the specific gas production rate and diffusional lsquoflowrsquo is combined into a specific gas flow qa
rsquo qa
rsquo = qa + qD (S7) where qa is the specific gas production rate (m-3 landfill gas m-3 waste yr-1) and qD the diffusional lsquoflowrsquo is calculated from
LV
ADq
SC
airSCaD 2
310
εε
= (S8)
Dair is the molecular diffusion coefficient of the chemical in air (m2 yr-1) εSC is the total porosity of the soil cover (m3 pore space m-3 soil cover) εaSC is the volumetric content of air in the soil cover (m3 air m-3 soil cover) L is the thickness of the soil cover (m) A is the surface area of the landfill (m2) V is the total volume of waste in the landfill (m3)
For neutral compounds Koc the distribution coefficient between solid organic carbon and water is calculated from
log Koc = 072log Kow+049 (S9) where Kow is the octanol-water distribution coefficient (dimensionless)
For organic bases (tertiary amines) Koc (pH) the pH-dependent distribution coefficient is calculated from (20)
Koc (pH) = (1-α) Koc (S10) where Koc is the distribution coefficient for the neutral compound and α the fraction of the non-dissociated (cationic) species is calculated from
α = 1(1+10(pH-pKa)) (S11)
S8
Box S3 Incorporation of liner diffusion term into MOCLA
In addition to the processes originally modeled by MOCLA a term was incorporated to evaluate diffusion through the composite liner The diffusive flux through the liner can be expressed by
xCDJ Diff partpart
= (S12)
where JDiff is the diffusive flux through the liner (g m-2 yr-1) D is the diffusion coefficient in the soil cover partCpartx is the concentration gradient (g m-4)
The diffusion coefficient (D) in eqn S12 is the effective diffusion coefficient for the composite geomembraneclay liner It was assumed that the geomembrane layer does not impede the diffusive flux through the composite liner as volatile organic compounds have been shown to penetrate geomembranes at an appreciable rate (22) Therefore the diffusion coefficient for the composite liner was represented by the effective diffusion coefficient for the clay layer Since clay liners are typically compacted at a moisture content less than saturation diffusion will occur through both the air-filled and water-filled pore spaces within the clay In a porous medium the effective diffusion coefficient for each phase (D
air or D
water) is calculated from the molecular diffusivity of the compound in air or water (Dair or Dwater) the total porosity of the clay liner (εL) and the air- or water-filled porosity of the liner (εaL or εwL) One commonly-used expression is the Millington equation which relates the effective diffusion coefficient to the molecular diffusion coefficient by (23)
2
333
L
Laairair DD
ε
ε= (S13)
and
2
333
L
Lwwaterwater DD
ε
ε= (S14)
S9
Box S3 (continued) Incorporation of liner diffusion term into MOCLA
Combining expressions S13 and S14 along with Henryrsquos Law results in the following equation for the diffusive flux through the liner (24)
x
CK
DDJ a
L
Lw
H
water
L
LaairDiff part
part⎟⎟⎠
⎞⎜⎜⎝
⎛+= 2
333
2
333
ε
ε
ε
ε (S15)
where Ca is equal to the gas-phase concentration of the contaminant If it is assumed that the concentration of the contaminant of interest in the aquifer beneath the liner is equal to zero then the sink due to diffusion through the composite liner may be written as
liner
a
L
Lw
H
water
L
LaairDiff L
CA
KD
DS ⎟⎟⎠
⎞⎜⎜⎝
⎛+= 2
333
2
333
ε
ε
ε
ε (S16)
where SDiff is the sink due to diffusion through the liner (g yr-1) Lliner is the thickness of the clay layer of the composite liner (m) SDiff can be simplified to SDiff = QD linerCa (S17) where
liner
effLinerD L
ADQ = (S18)
and
2
333
2
333
L
Lw
H
water
L
Laaireff K
DDD
ε
ε
ε
ε+= (S19)
Because literature values for εaSC and εaL were not available these terms were calculated as
)0max( scscbscSCa MCsdotminus= ρεε (S20) and
)0max( LLbLLa MCsdotminus= ρεε (S21) where εsc and εL are the total porosity of the soil cover and liner (m3 voids m-3 cover or liner) ρbSC and ρbL are the dry bulk density of the soil cover and liner (g soil m-3 cover or liner) MCSC and MCL are the gravimetric moisture content of the soil cover and liner ()
S10
Box S3 (continued) Incorporation of liner diffusion term into MOCLA
Including the diffusive flux term into the original MOCLA mass balance equation gives
( )diffwgdaT SSSSS
dtVCd
++++minus= λ)( (S22)
rearranging this expression gives
⎟⎟⎠
⎞⎜⎜⎝
⎛+++minus=
VQ
KHKNq
dtdC linerD
H
w
Ha
T λε (S23)
if qrsquo
D liner = QD liner V then a new expression for k can be written
linerD
H
w
Ha q
KHKNqk +++=
λε (S24)
Integrating each term on the right-hand side of eqn S22 gives the expressions for the fate routes The new expression for fate via liner diffusion is written as
))exp(1( t
RkqF
alinerDdiff minusminus= (S23)
S11
Methodology used to determine MOCLA input parameter values (physical parameters)
To evaluate the distribution and fate of chemicals in a landfill data for a number of input
parameters describing the landfill design and operation are required This section describes each
parameter and provides an explanation of how parameter values that could be applicable under
various disposal scenarios were determined
Dry bulk density of the waste ρb (T m-3) It is assumed that the building debris will be contained
for transport and burial and therefore will not be compacted after placement in the landfill
Therefore the wet bulk density of the building debris will likely be lower than the average value
of wet bulk density for compacted waste which is about 076 T m-3 The range of wet bulk
densities to be used in the bounding calculations was 042 to 070 T m-3 with an average value of
055 T m-3
The dry bulk density was determined from the wet bulk density and an estimate of the
gravimetric moisture content of the waste If the gravimetric moisture content (MC) of the waste
is assumed to be 10-20 (wet weight basis) then the dry bulk density can be calculated as
follows
Using a design basis of 1 m3 of refuse the total mass of waste is equal to 042 T which
corresponds to the low end of the range The mass of water in 1 m3 of refuse is equal to 042
times 020 (highest possible value of MC) or 0084 T The total mass of waste minus the mass of
water (042 - 0084) results in the mass of dry refuse which is 034 T Therefore the low value
of the range for dry bulk density is 034 T m-3 Similarly the high end of the range is 063 T m-3
The average value is 049 T m-3
Volumetric moisture content of the waste εw (m3 water m-3 LF) The possible values of
volumetric moisture content of the waste can be calculated from the ranges of the wet bulk
S12
density and the gravimetric moisture content assuming 1 m3 of waste The lowest value in the
range of volumetric moisture contents is calculated at 10 gravimetric moisture The mass of
water in 1 m3 of waste is 042 T (total mass) times 010 (mass of watertotal mass) which is 0042
T The density of water is 1 T m-3 so the volumetric moisture content is equal to 0042 m3 water
m-3 LF Similarly the highest value in the range is 014 m3 water m-3 LF which is equivalent to
070 T times 020 The average volumetric moisture content is 0091 m3 water m-3 LF
Volumetric gas content of the waste εa (m3 airm3 LF) A range of 010 to 040 was assumed for
the volumetric gas content of the waste There is very little data on measured values of the
effective porosity of waste Bendz et al (25) reported a measured value of 012 for a waste
sample from an operating MSW landfill Based on the range specified above the average value
for the volumetric gas content of the waste is 025
Fraction of organic carbon foc A range of 040 to 060 was used for the fraction of organic
carbon in the waste A value of 050 was reported for a sample of MSW (26) which will be used
as the average value in the bounding calculations
Height of the waste in the landfill H (m) The height of waste in the landfill is assumed to vary
between 183 and 61 m Based on this range the average height of waste in the landfill was 397
m
The final two terms required to describe the landfill infiltration and the gas production rate
are a function of the climate in which the landfill is located As a result two sets of values for
these parameters were used to represent an arid or a wet climate
Net precipitation N (myear) The net precipitation or infiltration was calculated based on data
reported in Camobreco et al (27) For the arid climate scenario data from sites with less than
05 m yr-1 of total precipitation were used while the data from sites with greater than or equal to
S13
05 m yr-1 were used for the wet climate scenario For each site the total precipitation was
multiplied by the percentage of precipitation that becomes leachate to determine the net
precipitation or infiltration Using this method infiltration for the arid climate was found to
range from 002 to 005 m yr-1 with an average value of 004 m yr-1 Infiltration for the wet
climate ranged from 004 to 032 m yr-1 with an average of 012 m yr-1 Although the data used
to generate these estimates encompassed a variety of different percentages of final cover it
should be noted that modeling a dry (fully capped) landfill is potentially a more realistic scenario
than a wet landfill since the building debris will likely be encapsulated and the greatest
likelihood for leakage from the containers will occur after the final cover has been placed when
infiltration is minimal
Gas production rate qa (m3 LFG m-3 LF yr-1) The landfill gas (LFG) production rate can be
described by the following equation (28)
qa=2WLoke-kt (S24)
where W is the mass of refuse Lo is a term representing the ultimate volume of methane gas
produced per unit of wet waste and k is a rate constant (yr-1) Equation S24 assumes a methane
concentration of 50 in LFG
The mass of refuse (W) is a function of the bulk density of the waste which as stated above
was assumed to vary from 042 to 070 T m-3 with an average value of 055 T m-3 Assuming 1
m3 of waste W will be equal to 055 T Lo was assumed to vary between 85 and 170 L methane
kg-1 wet waste The value of 170 L methane kg-1 wet waste is the default used in the New
Source Performance Standards of the Clean Air Act amendments (29) For the arid climate
scenario the rate constant (k) was set to 002 yr-1 For the wet climate scenario the rate constant
(k) was set to 005 yr-1 For the arid scenario qa was found to range from 19 to 37 m3 LFG m-3
S14
LF yr-1 with an average value of 28 m3 LFG m-3 LF yr-1 For the wet scenario qa was found to
range from 45 to 90 m3 LFG m-3 LF yr-1 with an average value of 675 m3 LFG m-3 LF yr-1
Thickness of cover L (m) The thickness of the landfill cover was set to 045 m which is the
minimum thickness specified by Subtitle D regulation for the thickness of the barrier layer (30)
This value was not varied in the bounding calculations
Total porosity of the soil cover εsc (dimensionless) The total porosity of the soil cover ranged
from 03 to 05 with an average value of 04 A total porosity between 03 and 05 is common for
a wide range of soil types
Gravimetric moisture content of soil cover (MCSC) The gravimetric moisture content of the soil
cover ranged from 103 to 308 (dry weight basis) with an average value of 200 based
published data (31)
Dry bulk density of the cover soil ρbSC (g cm-3) The dry bulk density of the soil cover ranged
from 13 to 20 g cm-3 with an average value of 17 g cm-3 based on published data (31) It
should be noted that the gravimetric moisture content and dry bulk density of the cover soil are
not used directly in MOCLA These parameters are used along with the porosity of the cover
soil to calculate the air-filled porosity of the cover soil which is an input parameter to MOCLA
Liner thickness Lliner (m) The thickness of the landfill liner was set to 06 m which is the
minimum thickness required by EPA Subtitle D regulation (30) The liner thickness was not
varied in the bounding calculations
Total porosity of the liner εL (dimensionless) The total porosity of the liner ranged from 03 to
05 with an average value of 04 A total porosity between 03 and 05 is common for a wide
range of soil types
S15
Gravimetric moisture content of the liner (MCL) Based on published data (31) the gravimetric
moisture content of the liner ranged from 103 to 308 with an average value of 200
Dry bulk density of the liner materials ρb L (g cm-3) Based on published data (31) the dry bulk
density of the liner ranged from 13 to 20 g cm-3 with an average value of 17 g cm-3 It should
be noted that the gravimetric moisture content and dry bulk density of the liner are not used
directly in MOCLA These parameters are used along with the porosity of the liner to calculate
the air-filled porosity of the liner which is an input parameter to MOCLA
S16
Table S1 List of Studied CWAs and TICs Military
Designation Common Name Chemical Formula CAS number Use
Carbon disulfide CS2 75-15-0 Toxic Industrial Chemical
Furan C4H4O 110-00-9 Toxic Industrial Chemical
HHD Mustard Gas C4H8Cl2S 505-60-2 Blister AgentVesicant
a Data compiled from the following sources (10 32-39) b Estimated with EPISuite v312 (40) c Hydrolysis rate estimated to be on the order of 10 min-1 at 20degC (41) d Hydrolysis half-life for ED estimated to be equal to that of L based on structural similarity e Half-life calculated based on 5 disappearance after 6 d (2) f Value estimated by averaging hydrolysis half-lives of GA GB and GD g Hydrolysis half-life estimated to be equal to that of VX based on structural similarity h Temperature not reported i Estimated using Wilke-Lee equation (42) j Estimated using Hayduk-Laudie equation (42) k pKa for CX estimated from a range of calculated pKa values for chloro-substituted oximes (43) l Estimated using Chem-Silico software package (44) m pKa for VG and VM estimated to be equivalent to that of VX MW is molecular weight bp is boiling point fp is freezing point KH is the Henryrsquos Law constant Kow is the octanol-water partition coefficient
S18Table S3 Henryrsquos law constant ranges for organic compounds originally modeled in MOCLA
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S4
Sorption to organic waste constituents retards the transport of organic contaminants in
landfills Municipal solid waste (MSW) is ~50 cellulose 10-15 hemicellulose and 15-20
lignin (18 19) In addition MSW contains ~10 plastics In terms of elemental composition
MSW is about 50 organic carbon (18 19) therefore a large fraction of MSW represents a
sorbent for organic compounds For many MSW constituents sorption of neutral organic
contaminants can be described by a partitioning model (48) and the sorption capacity of an
organic MSW constituent increases with increasing sorbent hydrophobicity (8) and sorbate
octanol-water partition coefficient log Kow (4) For ionizable CWAs it was assumed that only
the neutral species sorbs appreciably for octanol-water systems this assumption is valid up to
several pH units above the pKa of organic acids (20)
Although biodegradation of CWAs is theoretically possible biodegradation of many CWAs
has not been observed due to their toxicity (10) Assuming that CWA-exposed building debris
will be decontaminated prior to disposal some anaerobic degradation may occur in landfills if
CWAs are present at low aqueous-phase concentrations It is more likely that biodegradation of
CWA hydrolysates will occur because CWAs hydrolyze rapidly and hydrolysates generally have
reduced toxicity relative to the original agents Only one study was identified that investigated
the anaerobic biodegradability of CWA hydrolysates Skylar et al (21) reported 42
degradation of TDG (HD hydrolysate) by an anaerobic sludge inoculum after 185 d The
addition of co-substrates (volatile fatty acids glucose) reduced the TDG half-life to less than 30
d
Physical-Chemical Data for additional CWAs Evaluation of the transport of a number of
additional CWAs was performed using MOCLA A complete list of all CWAs evaluated is
S5
presented in Table S1 Physical-chemical property data for CWAs and TICs not presented in
Table 2 of the manuscript are given in Table S2
S6
Description of MOCLA model and derivation of liner diffusion term
Box S1 Equations of the original MOCLA model
The total concentration of the chemical CT (g chemical m-3 landfill) at any time t is calculated with
⎟⎟⎠
⎞⎜⎜⎝
⎛sdotminus= t
RkCC
aTT exp0 (S1)
where CT0 is the initial total concentration of the chemical (g chemical m-3 landfill) at t=0
H
w
Ha KHK
Nqk λε++= (S2)
Ra is the retardation factor
aH
wococba K
KfR εερ+
+sdotsdot= (S3)
qa is the specific gas flow (see Box S2) N is the annual net precipitation (m yr-1) H is the depth of waste (m) KH is the dimensionless Henryrsquos Law constant foc is the fraction of organic carbon in the dry waste Koc is the distribution coefficient between solid organic carbon and water (see Box S2) λ is the first order transformation constant (yr-1) ρb is the dry bulk density of the dry waste in the landfill (tonne dry waste m-3 landfill) εw is the volumetric moisture content in the landfill (m3 water m-3 landfill) εa is the volumetric air content in the landfill (m3 air m-3 landfill)
The transport of chemicals via landfill gas (Fa) diffusion through the top cover (Fgd) and leachate (Fw) is calculated with the following equations
)(tCR
VqF Ta
aa sdot=
)()( tCRQtF T
a
Dgd sdot= )()( tC
RKNAtF T
aHw sdot= (S4) (S5) (S6)
where QD = VqD (see Box S2)
S7
Box S2 Additional MOCLA equations
The sum of the specific gas production rate and diffusional lsquoflowrsquo is combined into a specific gas flow qa
rsquo qa
rsquo = qa + qD (S7) where qa is the specific gas production rate (m-3 landfill gas m-3 waste yr-1) and qD the diffusional lsquoflowrsquo is calculated from
LV
ADq
SC
airSCaD 2
310
εε
= (S8)
Dair is the molecular diffusion coefficient of the chemical in air (m2 yr-1) εSC is the total porosity of the soil cover (m3 pore space m-3 soil cover) εaSC is the volumetric content of air in the soil cover (m3 air m-3 soil cover) L is the thickness of the soil cover (m) A is the surface area of the landfill (m2) V is the total volume of waste in the landfill (m3)
For neutral compounds Koc the distribution coefficient between solid organic carbon and water is calculated from
log Koc = 072log Kow+049 (S9) where Kow is the octanol-water distribution coefficient (dimensionless)
For organic bases (tertiary amines) Koc (pH) the pH-dependent distribution coefficient is calculated from (20)
Koc (pH) = (1-α) Koc (S10) where Koc is the distribution coefficient for the neutral compound and α the fraction of the non-dissociated (cationic) species is calculated from
α = 1(1+10(pH-pKa)) (S11)
S8
Box S3 Incorporation of liner diffusion term into MOCLA
In addition to the processes originally modeled by MOCLA a term was incorporated to evaluate diffusion through the composite liner The diffusive flux through the liner can be expressed by
xCDJ Diff partpart
= (S12)
where JDiff is the diffusive flux through the liner (g m-2 yr-1) D is the diffusion coefficient in the soil cover partCpartx is the concentration gradient (g m-4)
The diffusion coefficient (D) in eqn S12 is the effective diffusion coefficient for the composite geomembraneclay liner It was assumed that the geomembrane layer does not impede the diffusive flux through the composite liner as volatile organic compounds have been shown to penetrate geomembranes at an appreciable rate (22) Therefore the diffusion coefficient for the composite liner was represented by the effective diffusion coefficient for the clay layer Since clay liners are typically compacted at a moisture content less than saturation diffusion will occur through both the air-filled and water-filled pore spaces within the clay In a porous medium the effective diffusion coefficient for each phase (D
air or D
water) is calculated from the molecular diffusivity of the compound in air or water (Dair or Dwater) the total porosity of the clay liner (εL) and the air- or water-filled porosity of the liner (εaL or εwL) One commonly-used expression is the Millington equation which relates the effective diffusion coefficient to the molecular diffusion coefficient by (23)
2
333
L
Laairair DD
ε
ε= (S13)
and
2
333
L
Lwwaterwater DD
ε
ε= (S14)
S9
Box S3 (continued) Incorporation of liner diffusion term into MOCLA
Combining expressions S13 and S14 along with Henryrsquos Law results in the following equation for the diffusive flux through the liner (24)
x
CK
DDJ a
L
Lw
H
water
L
LaairDiff part
part⎟⎟⎠
⎞⎜⎜⎝
⎛+= 2
333
2
333
ε
ε
ε
ε (S15)
where Ca is equal to the gas-phase concentration of the contaminant If it is assumed that the concentration of the contaminant of interest in the aquifer beneath the liner is equal to zero then the sink due to diffusion through the composite liner may be written as
liner
a
L
Lw
H
water
L
LaairDiff L
CA
KD
DS ⎟⎟⎠
⎞⎜⎜⎝
⎛+= 2
333
2
333
ε
ε
ε
ε (S16)
where SDiff is the sink due to diffusion through the liner (g yr-1) Lliner is the thickness of the clay layer of the composite liner (m) SDiff can be simplified to SDiff = QD linerCa (S17) where
liner
effLinerD L
ADQ = (S18)
and
2
333
2
333
L
Lw
H
water
L
Laaireff K
DDD
ε
ε
ε
ε+= (S19)
Because literature values for εaSC and εaL were not available these terms were calculated as
)0max( scscbscSCa MCsdotminus= ρεε (S20) and
)0max( LLbLLa MCsdotminus= ρεε (S21) where εsc and εL are the total porosity of the soil cover and liner (m3 voids m-3 cover or liner) ρbSC and ρbL are the dry bulk density of the soil cover and liner (g soil m-3 cover or liner) MCSC and MCL are the gravimetric moisture content of the soil cover and liner ()
S10
Box S3 (continued) Incorporation of liner diffusion term into MOCLA
Including the diffusive flux term into the original MOCLA mass balance equation gives
( )diffwgdaT SSSSS
dtVCd
++++minus= λ)( (S22)
rearranging this expression gives
⎟⎟⎠
⎞⎜⎜⎝
⎛+++minus=
VQ
KHKNq
dtdC linerD
H
w
Ha
T λε (S23)
if qrsquo
D liner = QD liner V then a new expression for k can be written
linerD
H
w
Ha q
KHKNqk +++=
λε (S24)
Integrating each term on the right-hand side of eqn S22 gives the expressions for the fate routes The new expression for fate via liner diffusion is written as
))exp(1( t
RkqF
alinerDdiff minusminus= (S23)
S11
Methodology used to determine MOCLA input parameter values (physical parameters)
To evaluate the distribution and fate of chemicals in a landfill data for a number of input
parameters describing the landfill design and operation are required This section describes each
parameter and provides an explanation of how parameter values that could be applicable under
various disposal scenarios were determined
Dry bulk density of the waste ρb (T m-3) It is assumed that the building debris will be contained
for transport and burial and therefore will not be compacted after placement in the landfill
Therefore the wet bulk density of the building debris will likely be lower than the average value
of wet bulk density for compacted waste which is about 076 T m-3 The range of wet bulk
densities to be used in the bounding calculations was 042 to 070 T m-3 with an average value of
055 T m-3
The dry bulk density was determined from the wet bulk density and an estimate of the
gravimetric moisture content of the waste If the gravimetric moisture content (MC) of the waste
is assumed to be 10-20 (wet weight basis) then the dry bulk density can be calculated as
follows
Using a design basis of 1 m3 of refuse the total mass of waste is equal to 042 T which
corresponds to the low end of the range The mass of water in 1 m3 of refuse is equal to 042
times 020 (highest possible value of MC) or 0084 T The total mass of waste minus the mass of
water (042 - 0084) results in the mass of dry refuse which is 034 T Therefore the low value
of the range for dry bulk density is 034 T m-3 Similarly the high end of the range is 063 T m-3
The average value is 049 T m-3
Volumetric moisture content of the waste εw (m3 water m-3 LF) The possible values of
volumetric moisture content of the waste can be calculated from the ranges of the wet bulk
S12
density and the gravimetric moisture content assuming 1 m3 of waste The lowest value in the
range of volumetric moisture contents is calculated at 10 gravimetric moisture The mass of
water in 1 m3 of waste is 042 T (total mass) times 010 (mass of watertotal mass) which is 0042
T The density of water is 1 T m-3 so the volumetric moisture content is equal to 0042 m3 water
m-3 LF Similarly the highest value in the range is 014 m3 water m-3 LF which is equivalent to
070 T times 020 The average volumetric moisture content is 0091 m3 water m-3 LF
Volumetric gas content of the waste εa (m3 airm3 LF) A range of 010 to 040 was assumed for
the volumetric gas content of the waste There is very little data on measured values of the
effective porosity of waste Bendz et al (25) reported a measured value of 012 for a waste
sample from an operating MSW landfill Based on the range specified above the average value
for the volumetric gas content of the waste is 025
Fraction of organic carbon foc A range of 040 to 060 was used for the fraction of organic
carbon in the waste A value of 050 was reported for a sample of MSW (26) which will be used
as the average value in the bounding calculations
Height of the waste in the landfill H (m) The height of waste in the landfill is assumed to vary
between 183 and 61 m Based on this range the average height of waste in the landfill was 397
m
The final two terms required to describe the landfill infiltration and the gas production rate
are a function of the climate in which the landfill is located As a result two sets of values for
these parameters were used to represent an arid or a wet climate
Net precipitation N (myear) The net precipitation or infiltration was calculated based on data
reported in Camobreco et al (27) For the arid climate scenario data from sites with less than
05 m yr-1 of total precipitation were used while the data from sites with greater than or equal to
S13
05 m yr-1 were used for the wet climate scenario For each site the total precipitation was
multiplied by the percentage of precipitation that becomes leachate to determine the net
precipitation or infiltration Using this method infiltration for the arid climate was found to
range from 002 to 005 m yr-1 with an average value of 004 m yr-1 Infiltration for the wet
climate ranged from 004 to 032 m yr-1 with an average of 012 m yr-1 Although the data used
to generate these estimates encompassed a variety of different percentages of final cover it
should be noted that modeling a dry (fully capped) landfill is potentially a more realistic scenario
than a wet landfill since the building debris will likely be encapsulated and the greatest
likelihood for leakage from the containers will occur after the final cover has been placed when
infiltration is minimal
Gas production rate qa (m3 LFG m-3 LF yr-1) The landfill gas (LFG) production rate can be
described by the following equation (28)
qa=2WLoke-kt (S24)
where W is the mass of refuse Lo is a term representing the ultimate volume of methane gas
produced per unit of wet waste and k is a rate constant (yr-1) Equation S24 assumes a methane
concentration of 50 in LFG
The mass of refuse (W) is a function of the bulk density of the waste which as stated above
was assumed to vary from 042 to 070 T m-3 with an average value of 055 T m-3 Assuming 1
m3 of waste W will be equal to 055 T Lo was assumed to vary between 85 and 170 L methane
kg-1 wet waste The value of 170 L methane kg-1 wet waste is the default used in the New
Source Performance Standards of the Clean Air Act amendments (29) For the arid climate
scenario the rate constant (k) was set to 002 yr-1 For the wet climate scenario the rate constant
(k) was set to 005 yr-1 For the arid scenario qa was found to range from 19 to 37 m3 LFG m-3
S14
LF yr-1 with an average value of 28 m3 LFG m-3 LF yr-1 For the wet scenario qa was found to
range from 45 to 90 m3 LFG m-3 LF yr-1 with an average value of 675 m3 LFG m-3 LF yr-1
Thickness of cover L (m) The thickness of the landfill cover was set to 045 m which is the
minimum thickness specified by Subtitle D regulation for the thickness of the barrier layer (30)
This value was not varied in the bounding calculations
Total porosity of the soil cover εsc (dimensionless) The total porosity of the soil cover ranged
from 03 to 05 with an average value of 04 A total porosity between 03 and 05 is common for
a wide range of soil types
Gravimetric moisture content of soil cover (MCSC) The gravimetric moisture content of the soil
cover ranged from 103 to 308 (dry weight basis) with an average value of 200 based
published data (31)
Dry bulk density of the cover soil ρbSC (g cm-3) The dry bulk density of the soil cover ranged
from 13 to 20 g cm-3 with an average value of 17 g cm-3 based on published data (31) It
should be noted that the gravimetric moisture content and dry bulk density of the cover soil are
not used directly in MOCLA These parameters are used along with the porosity of the cover
soil to calculate the air-filled porosity of the cover soil which is an input parameter to MOCLA
Liner thickness Lliner (m) The thickness of the landfill liner was set to 06 m which is the
minimum thickness required by EPA Subtitle D regulation (30) The liner thickness was not
varied in the bounding calculations
Total porosity of the liner εL (dimensionless) The total porosity of the liner ranged from 03 to
05 with an average value of 04 A total porosity between 03 and 05 is common for a wide
range of soil types
S15
Gravimetric moisture content of the liner (MCL) Based on published data (31) the gravimetric
moisture content of the liner ranged from 103 to 308 with an average value of 200
Dry bulk density of the liner materials ρb L (g cm-3) Based on published data (31) the dry bulk
density of the liner ranged from 13 to 20 g cm-3 with an average value of 17 g cm-3 It should
be noted that the gravimetric moisture content and dry bulk density of the liner are not used
directly in MOCLA These parameters are used along with the porosity of the liner to calculate
the air-filled porosity of the liner which is an input parameter to MOCLA
S16
Table S1 List of Studied CWAs and TICs Military
Designation Common Name Chemical Formula CAS number Use
Carbon disulfide CS2 75-15-0 Toxic Industrial Chemical
Furan C4H4O 110-00-9 Toxic Industrial Chemical
HHD Mustard Gas C4H8Cl2S 505-60-2 Blister AgentVesicant
a Data compiled from the following sources (10 32-39) b Estimated with EPISuite v312 (40) c Hydrolysis rate estimated to be on the order of 10 min-1 at 20degC (41) d Hydrolysis half-life for ED estimated to be equal to that of L based on structural similarity e Half-life calculated based on 5 disappearance after 6 d (2) f Value estimated by averaging hydrolysis half-lives of GA GB and GD g Hydrolysis half-life estimated to be equal to that of VX based on structural similarity h Temperature not reported i Estimated using Wilke-Lee equation (42) j Estimated using Hayduk-Laudie equation (42) k pKa for CX estimated from a range of calculated pKa values for chloro-substituted oximes (43) l Estimated using Chem-Silico software package (44) m pKa for VG and VM estimated to be equivalent to that of VX MW is molecular weight bp is boiling point fp is freezing point KH is the Henryrsquos Law constant Kow is the octanol-water partition coefficient
S18Table S3 Henryrsquos law constant ranges for organic compounds originally modeled in MOCLA
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S5
presented in Table S1 Physical-chemical property data for CWAs and TICs not presented in
Table 2 of the manuscript are given in Table S2
S6
Description of MOCLA model and derivation of liner diffusion term
Box S1 Equations of the original MOCLA model
The total concentration of the chemical CT (g chemical m-3 landfill) at any time t is calculated with
⎟⎟⎠
⎞⎜⎜⎝
⎛sdotminus= t
RkCC
aTT exp0 (S1)
where CT0 is the initial total concentration of the chemical (g chemical m-3 landfill) at t=0
H
w
Ha KHK
Nqk λε++= (S2)
Ra is the retardation factor
aH
wococba K
KfR εερ+
+sdotsdot= (S3)
qa is the specific gas flow (see Box S2) N is the annual net precipitation (m yr-1) H is the depth of waste (m) KH is the dimensionless Henryrsquos Law constant foc is the fraction of organic carbon in the dry waste Koc is the distribution coefficient between solid organic carbon and water (see Box S2) λ is the first order transformation constant (yr-1) ρb is the dry bulk density of the dry waste in the landfill (tonne dry waste m-3 landfill) εw is the volumetric moisture content in the landfill (m3 water m-3 landfill) εa is the volumetric air content in the landfill (m3 air m-3 landfill)
The transport of chemicals via landfill gas (Fa) diffusion through the top cover (Fgd) and leachate (Fw) is calculated with the following equations
)(tCR
VqF Ta
aa sdot=
)()( tCRQtF T
a
Dgd sdot= )()( tC
RKNAtF T
aHw sdot= (S4) (S5) (S6)
where QD = VqD (see Box S2)
S7
Box S2 Additional MOCLA equations
The sum of the specific gas production rate and diffusional lsquoflowrsquo is combined into a specific gas flow qa
rsquo qa
rsquo = qa + qD (S7) where qa is the specific gas production rate (m-3 landfill gas m-3 waste yr-1) and qD the diffusional lsquoflowrsquo is calculated from
LV
ADq
SC
airSCaD 2
310
εε
= (S8)
Dair is the molecular diffusion coefficient of the chemical in air (m2 yr-1) εSC is the total porosity of the soil cover (m3 pore space m-3 soil cover) εaSC is the volumetric content of air in the soil cover (m3 air m-3 soil cover) L is the thickness of the soil cover (m) A is the surface area of the landfill (m2) V is the total volume of waste in the landfill (m3)
For neutral compounds Koc the distribution coefficient between solid organic carbon and water is calculated from
log Koc = 072log Kow+049 (S9) where Kow is the octanol-water distribution coefficient (dimensionless)
For organic bases (tertiary amines) Koc (pH) the pH-dependent distribution coefficient is calculated from (20)
Koc (pH) = (1-α) Koc (S10) where Koc is the distribution coefficient for the neutral compound and α the fraction of the non-dissociated (cationic) species is calculated from
α = 1(1+10(pH-pKa)) (S11)
S8
Box S3 Incorporation of liner diffusion term into MOCLA
In addition to the processes originally modeled by MOCLA a term was incorporated to evaluate diffusion through the composite liner The diffusive flux through the liner can be expressed by
xCDJ Diff partpart
= (S12)
where JDiff is the diffusive flux through the liner (g m-2 yr-1) D is the diffusion coefficient in the soil cover partCpartx is the concentration gradient (g m-4)
The diffusion coefficient (D) in eqn S12 is the effective diffusion coefficient for the composite geomembraneclay liner It was assumed that the geomembrane layer does not impede the diffusive flux through the composite liner as volatile organic compounds have been shown to penetrate geomembranes at an appreciable rate (22) Therefore the diffusion coefficient for the composite liner was represented by the effective diffusion coefficient for the clay layer Since clay liners are typically compacted at a moisture content less than saturation diffusion will occur through both the air-filled and water-filled pore spaces within the clay In a porous medium the effective diffusion coefficient for each phase (D
air or D
water) is calculated from the molecular diffusivity of the compound in air or water (Dair or Dwater) the total porosity of the clay liner (εL) and the air- or water-filled porosity of the liner (εaL or εwL) One commonly-used expression is the Millington equation which relates the effective diffusion coefficient to the molecular diffusion coefficient by (23)
2
333
L
Laairair DD
ε
ε= (S13)
and
2
333
L
Lwwaterwater DD
ε
ε= (S14)
S9
Box S3 (continued) Incorporation of liner diffusion term into MOCLA
Combining expressions S13 and S14 along with Henryrsquos Law results in the following equation for the diffusive flux through the liner (24)
x
CK
DDJ a
L
Lw
H
water
L
LaairDiff part
part⎟⎟⎠
⎞⎜⎜⎝
⎛+= 2
333
2
333
ε
ε
ε
ε (S15)
where Ca is equal to the gas-phase concentration of the contaminant If it is assumed that the concentration of the contaminant of interest in the aquifer beneath the liner is equal to zero then the sink due to diffusion through the composite liner may be written as
liner
a
L
Lw
H
water
L
LaairDiff L
CA
KD
DS ⎟⎟⎠
⎞⎜⎜⎝
⎛+= 2
333
2
333
ε
ε
ε
ε (S16)
where SDiff is the sink due to diffusion through the liner (g yr-1) Lliner is the thickness of the clay layer of the composite liner (m) SDiff can be simplified to SDiff = QD linerCa (S17) where
liner
effLinerD L
ADQ = (S18)
and
2
333
2
333
L
Lw
H
water
L
Laaireff K
DDD
ε
ε
ε
ε+= (S19)
Because literature values for εaSC and εaL were not available these terms were calculated as
)0max( scscbscSCa MCsdotminus= ρεε (S20) and
)0max( LLbLLa MCsdotminus= ρεε (S21) where εsc and εL are the total porosity of the soil cover and liner (m3 voids m-3 cover or liner) ρbSC and ρbL are the dry bulk density of the soil cover and liner (g soil m-3 cover or liner) MCSC and MCL are the gravimetric moisture content of the soil cover and liner ()
S10
Box S3 (continued) Incorporation of liner diffusion term into MOCLA
Including the diffusive flux term into the original MOCLA mass balance equation gives
( )diffwgdaT SSSSS
dtVCd
++++minus= λ)( (S22)
rearranging this expression gives
⎟⎟⎠
⎞⎜⎜⎝
⎛+++minus=
VQ
KHKNq
dtdC linerD
H
w
Ha
T λε (S23)
if qrsquo
D liner = QD liner V then a new expression for k can be written
linerD
H
w
Ha q
KHKNqk +++=
λε (S24)
Integrating each term on the right-hand side of eqn S22 gives the expressions for the fate routes The new expression for fate via liner diffusion is written as
))exp(1( t
RkqF
alinerDdiff minusminus= (S23)
S11
Methodology used to determine MOCLA input parameter values (physical parameters)
To evaluate the distribution and fate of chemicals in a landfill data for a number of input
parameters describing the landfill design and operation are required This section describes each
parameter and provides an explanation of how parameter values that could be applicable under
various disposal scenarios were determined
Dry bulk density of the waste ρb (T m-3) It is assumed that the building debris will be contained
for transport and burial and therefore will not be compacted after placement in the landfill
Therefore the wet bulk density of the building debris will likely be lower than the average value
of wet bulk density for compacted waste which is about 076 T m-3 The range of wet bulk
densities to be used in the bounding calculations was 042 to 070 T m-3 with an average value of
055 T m-3
The dry bulk density was determined from the wet bulk density and an estimate of the
gravimetric moisture content of the waste If the gravimetric moisture content (MC) of the waste
is assumed to be 10-20 (wet weight basis) then the dry bulk density can be calculated as
follows
Using a design basis of 1 m3 of refuse the total mass of waste is equal to 042 T which
corresponds to the low end of the range The mass of water in 1 m3 of refuse is equal to 042
times 020 (highest possible value of MC) or 0084 T The total mass of waste minus the mass of
water (042 - 0084) results in the mass of dry refuse which is 034 T Therefore the low value
of the range for dry bulk density is 034 T m-3 Similarly the high end of the range is 063 T m-3
The average value is 049 T m-3
Volumetric moisture content of the waste εw (m3 water m-3 LF) The possible values of
volumetric moisture content of the waste can be calculated from the ranges of the wet bulk
S12
density and the gravimetric moisture content assuming 1 m3 of waste The lowest value in the
range of volumetric moisture contents is calculated at 10 gravimetric moisture The mass of
water in 1 m3 of waste is 042 T (total mass) times 010 (mass of watertotal mass) which is 0042
T The density of water is 1 T m-3 so the volumetric moisture content is equal to 0042 m3 water
m-3 LF Similarly the highest value in the range is 014 m3 water m-3 LF which is equivalent to
070 T times 020 The average volumetric moisture content is 0091 m3 water m-3 LF
Volumetric gas content of the waste εa (m3 airm3 LF) A range of 010 to 040 was assumed for
the volumetric gas content of the waste There is very little data on measured values of the
effective porosity of waste Bendz et al (25) reported a measured value of 012 for a waste
sample from an operating MSW landfill Based on the range specified above the average value
for the volumetric gas content of the waste is 025
Fraction of organic carbon foc A range of 040 to 060 was used for the fraction of organic
carbon in the waste A value of 050 was reported for a sample of MSW (26) which will be used
as the average value in the bounding calculations
Height of the waste in the landfill H (m) The height of waste in the landfill is assumed to vary
between 183 and 61 m Based on this range the average height of waste in the landfill was 397
m
The final two terms required to describe the landfill infiltration and the gas production rate
are a function of the climate in which the landfill is located As a result two sets of values for
these parameters were used to represent an arid or a wet climate
Net precipitation N (myear) The net precipitation or infiltration was calculated based on data
reported in Camobreco et al (27) For the arid climate scenario data from sites with less than
05 m yr-1 of total precipitation were used while the data from sites with greater than or equal to
S13
05 m yr-1 were used for the wet climate scenario For each site the total precipitation was
multiplied by the percentage of precipitation that becomes leachate to determine the net
precipitation or infiltration Using this method infiltration for the arid climate was found to
range from 002 to 005 m yr-1 with an average value of 004 m yr-1 Infiltration for the wet
climate ranged from 004 to 032 m yr-1 with an average of 012 m yr-1 Although the data used
to generate these estimates encompassed a variety of different percentages of final cover it
should be noted that modeling a dry (fully capped) landfill is potentially a more realistic scenario
than a wet landfill since the building debris will likely be encapsulated and the greatest
likelihood for leakage from the containers will occur after the final cover has been placed when
infiltration is minimal
Gas production rate qa (m3 LFG m-3 LF yr-1) The landfill gas (LFG) production rate can be
described by the following equation (28)
qa=2WLoke-kt (S24)
where W is the mass of refuse Lo is a term representing the ultimate volume of methane gas
produced per unit of wet waste and k is a rate constant (yr-1) Equation S24 assumes a methane
concentration of 50 in LFG
The mass of refuse (W) is a function of the bulk density of the waste which as stated above
was assumed to vary from 042 to 070 T m-3 with an average value of 055 T m-3 Assuming 1
m3 of waste W will be equal to 055 T Lo was assumed to vary between 85 and 170 L methane
kg-1 wet waste The value of 170 L methane kg-1 wet waste is the default used in the New
Source Performance Standards of the Clean Air Act amendments (29) For the arid climate
scenario the rate constant (k) was set to 002 yr-1 For the wet climate scenario the rate constant
(k) was set to 005 yr-1 For the arid scenario qa was found to range from 19 to 37 m3 LFG m-3
S14
LF yr-1 with an average value of 28 m3 LFG m-3 LF yr-1 For the wet scenario qa was found to
range from 45 to 90 m3 LFG m-3 LF yr-1 with an average value of 675 m3 LFG m-3 LF yr-1
Thickness of cover L (m) The thickness of the landfill cover was set to 045 m which is the
minimum thickness specified by Subtitle D regulation for the thickness of the barrier layer (30)
This value was not varied in the bounding calculations
Total porosity of the soil cover εsc (dimensionless) The total porosity of the soil cover ranged
from 03 to 05 with an average value of 04 A total porosity between 03 and 05 is common for
a wide range of soil types
Gravimetric moisture content of soil cover (MCSC) The gravimetric moisture content of the soil
cover ranged from 103 to 308 (dry weight basis) with an average value of 200 based
published data (31)
Dry bulk density of the cover soil ρbSC (g cm-3) The dry bulk density of the soil cover ranged
from 13 to 20 g cm-3 with an average value of 17 g cm-3 based on published data (31) It
should be noted that the gravimetric moisture content and dry bulk density of the cover soil are
not used directly in MOCLA These parameters are used along with the porosity of the cover
soil to calculate the air-filled porosity of the cover soil which is an input parameter to MOCLA
Liner thickness Lliner (m) The thickness of the landfill liner was set to 06 m which is the
minimum thickness required by EPA Subtitle D regulation (30) The liner thickness was not
varied in the bounding calculations
Total porosity of the liner εL (dimensionless) The total porosity of the liner ranged from 03 to
05 with an average value of 04 A total porosity between 03 and 05 is common for a wide
range of soil types
S15
Gravimetric moisture content of the liner (MCL) Based on published data (31) the gravimetric
moisture content of the liner ranged from 103 to 308 with an average value of 200
Dry bulk density of the liner materials ρb L (g cm-3) Based on published data (31) the dry bulk
density of the liner ranged from 13 to 20 g cm-3 with an average value of 17 g cm-3 It should
be noted that the gravimetric moisture content and dry bulk density of the liner are not used
directly in MOCLA These parameters are used along with the porosity of the liner to calculate
the air-filled porosity of the liner which is an input parameter to MOCLA
S16
Table S1 List of Studied CWAs and TICs Military
Designation Common Name Chemical Formula CAS number Use
Carbon disulfide CS2 75-15-0 Toxic Industrial Chemical
Furan C4H4O 110-00-9 Toxic Industrial Chemical
HHD Mustard Gas C4H8Cl2S 505-60-2 Blister AgentVesicant
a Data compiled from the following sources (10 32-39) b Estimated with EPISuite v312 (40) c Hydrolysis rate estimated to be on the order of 10 min-1 at 20degC (41) d Hydrolysis half-life for ED estimated to be equal to that of L based on structural similarity e Half-life calculated based on 5 disappearance after 6 d (2) f Value estimated by averaging hydrolysis half-lives of GA GB and GD g Hydrolysis half-life estimated to be equal to that of VX based on structural similarity h Temperature not reported i Estimated using Wilke-Lee equation (42) j Estimated using Hayduk-Laudie equation (42) k pKa for CX estimated from a range of calculated pKa values for chloro-substituted oximes (43) l Estimated using Chem-Silico software package (44) m pKa for VG and VM estimated to be equivalent to that of VX MW is molecular weight bp is boiling point fp is freezing point KH is the Henryrsquos Law constant Kow is the octanol-water partition coefficient
S18Table S3 Henryrsquos law constant ranges for organic compounds originally modeled in MOCLA
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S6
Description of MOCLA model and derivation of liner diffusion term
Box S1 Equations of the original MOCLA model
The total concentration of the chemical CT (g chemical m-3 landfill) at any time t is calculated with
⎟⎟⎠
⎞⎜⎜⎝
⎛sdotminus= t
RkCC
aTT exp0 (S1)
where CT0 is the initial total concentration of the chemical (g chemical m-3 landfill) at t=0
H
w
Ha KHK
Nqk λε++= (S2)
Ra is the retardation factor
aH
wococba K
KfR εερ+
+sdotsdot= (S3)
qa is the specific gas flow (see Box S2) N is the annual net precipitation (m yr-1) H is the depth of waste (m) KH is the dimensionless Henryrsquos Law constant foc is the fraction of organic carbon in the dry waste Koc is the distribution coefficient between solid organic carbon and water (see Box S2) λ is the first order transformation constant (yr-1) ρb is the dry bulk density of the dry waste in the landfill (tonne dry waste m-3 landfill) εw is the volumetric moisture content in the landfill (m3 water m-3 landfill) εa is the volumetric air content in the landfill (m3 air m-3 landfill)
The transport of chemicals via landfill gas (Fa) diffusion through the top cover (Fgd) and leachate (Fw) is calculated with the following equations
)(tCR
VqF Ta
aa sdot=
)()( tCRQtF T
a
Dgd sdot= )()( tC
RKNAtF T
aHw sdot= (S4) (S5) (S6)
where QD = VqD (see Box S2)
S7
Box S2 Additional MOCLA equations
The sum of the specific gas production rate and diffusional lsquoflowrsquo is combined into a specific gas flow qa
rsquo qa
rsquo = qa + qD (S7) where qa is the specific gas production rate (m-3 landfill gas m-3 waste yr-1) and qD the diffusional lsquoflowrsquo is calculated from
LV
ADq
SC
airSCaD 2
310
εε
= (S8)
Dair is the molecular diffusion coefficient of the chemical in air (m2 yr-1) εSC is the total porosity of the soil cover (m3 pore space m-3 soil cover) εaSC is the volumetric content of air in the soil cover (m3 air m-3 soil cover) L is the thickness of the soil cover (m) A is the surface area of the landfill (m2) V is the total volume of waste in the landfill (m3)
For neutral compounds Koc the distribution coefficient between solid organic carbon and water is calculated from
log Koc = 072log Kow+049 (S9) where Kow is the octanol-water distribution coefficient (dimensionless)
For organic bases (tertiary amines) Koc (pH) the pH-dependent distribution coefficient is calculated from (20)
Koc (pH) = (1-α) Koc (S10) where Koc is the distribution coefficient for the neutral compound and α the fraction of the non-dissociated (cationic) species is calculated from
α = 1(1+10(pH-pKa)) (S11)
S8
Box S3 Incorporation of liner diffusion term into MOCLA
In addition to the processes originally modeled by MOCLA a term was incorporated to evaluate diffusion through the composite liner The diffusive flux through the liner can be expressed by
xCDJ Diff partpart
= (S12)
where JDiff is the diffusive flux through the liner (g m-2 yr-1) D is the diffusion coefficient in the soil cover partCpartx is the concentration gradient (g m-4)
The diffusion coefficient (D) in eqn S12 is the effective diffusion coefficient for the composite geomembraneclay liner It was assumed that the geomembrane layer does not impede the diffusive flux through the composite liner as volatile organic compounds have been shown to penetrate geomembranes at an appreciable rate (22) Therefore the diffusion coefficient for the composite liner was represented by the effective diffusion coefficient for the clay layer Since clay liners are typically compacted at a moisture content less than saturation diffusion will occur through both the air-filled and water-filled pore spaces within the clay In a porous medium the effective diffusion coefficient for each phase (D
air or D
water) is calculated from the molecular diffusivity of the compound in air or water (Dair or Dwater) the total porosity of the clay liner (εL) and the air- or water-filled porosity of the liner (εaL or εwL) One commonly-used expression is the Millington equation which relates the effective diffusion coefficient to the molecular diffusion coefficient by (23)
2
333
L
Laairair DD
ε
ε= (S13)
and
2
333
L
Lwwaterwater DD
ε
ε= (S14)
S9
Box S3 (continued) Incorporation of liner diffusion term into MOCLA
Combining expressions S13 and S14 along with Henryrsquos Law results in the following equation for the diffusive flux through the liner (24)
x
CK
DDJ a
L
Lw
H
water
L
LaairDiff part
part⎟⎟⎠
⎞⎜⎜⎝
⎛+= 2
333
2
333
ε
ε
ε
ε (S15)
where Ca is equal to the gas-phase concentration of the contaminant If it is assumed that the concentration of the contaminant of interest in the aquifer beneath the liner is equal to zero then the sink due to diffusion through the composite liner may be written as
liner
a
L
Lw
H
water
L
LaairDiff L
CA
KD
DS ⎟⎟⎠
⎞⎜⎜⎝
⎛+= 2
333
2
333
ε
ε
ε
ε (S16)
where SDiff is the sink due to diffusion through the liner (g yr-1) Lliner is the thickness of the clay layer of the composite liner (m) SDiff can be simplified to SDiff = QD linerCa (S17) where
liner
effLinerD L
ADQ = (S18)
and
2
333
2
333
L
Lw
H
water
L
Laaireff K
DDD
ε
ε
ε
ε+= (S19)
Because literature values for εaSC and εaL were not available these terms were calculated as
)0max( scscbscSCa MCsdotminus= ρεε (S20) and
)0max( LLbLLa MCsdotminus= ρεε (S21) where εsc and εL are the total porosity of the soil cover and liner (m3 voids m-3 cover or liner) ρbSC and ρbL are the dry bulk density of the soil cover and liner (g soil m-3 cover or liner) MCSC and MCL are the gravimetric moisture content of the soil cover and liner ()
S10
Box S3 (continued) Incorporation of liner diffusion term into MOCLA
Including the diffusive flux term into the original MOCLA mass balance equation gives
( )diffwgdaT SSSSS
dtVCd
++++minus= λ)( (S22)
rearranging this expression gives
⎟⎟⎠
⎞⎜⎜⎝
⎛+++minus=
VQ
KHKNq
dtdC linerD
H
w
Ha
T λε (S23)
if qrsquo
D liner = QD liner V then a new expression for k can be written
linerD
H
w
Ha q
KHKNqk +++=
λε (S24)
Integrating each term on the right-hand side of eqn S22 gives the expressions for the fate routes The new expression for fate via liner diffusion is written as
))exp(1( t
RkqF
alinerDdiff minusminus= (S23)
S11
Methodology used to determine MOCLA input parameter values (physical parameters)
To evaluate the distribution and fate of chemicals in a landfill data for a number of input
parameters describing the landfill design and operation are required This section describes each
parameter and provides an explanation of how parameter values that could be applicable under
various disposal scenarios were determined
Dry bulk density of the waste ρb (T m-3) It is assumed that the building debris will be contained
for transport and burial and therefore will not be compacted after placement in the landfill
Therefore the wet bulk density of the building debris will likely be lower than the average value
of wet bulk density for compacted waste which is about 076 T m-3 The range of wet bulk
densities to be used in the bounding calculations was 042 to 070 T m-3 with an average value of
055 T m-3
The dry bulk density was determined from the wet bulk density and an estimate of the
gravimetric moisture content of the waste If the gravimetric moisture content (MC) of the waste
is assumed to be 10-20 (wet weight basis) then the dry bulk density can be calculated as
follows
Using a design basis of 1 m3 of refuse the total mass of waste is equal to 042 T which
corresponds to the low end of the range The mass of water in 1 m3 of refuse is equal to 042
times 020 (highest possible value of MC) or 0084 T The total mass of waste minus the mass of
water (042 - 0084) results in the mass of dry refuse which is 034 T Therefore the low value
of the range for dry bulk density is 034 T m-3 Similarly the high end of the range is 063 T m-3
The average value is 049 T m-3
Volumetric moisture content of the waste εw (m3 water m-3 LF) The possible values of
volumetric moisture content of the waste can be calculated from the ranges of the wet bulk
S12
density and the gravimetric moisture content assuming 1 m3 of waste The lowest value in the
range of volumetric moisture contents is calculated at 10 gravimetric moisture The mass of
water in 1 m3 of waste is 042 T (total mass) times 010 (mass of watertotal mass) which is 0042
T The density of water is 1 T m-3 so the volumetric moisture content is equal to 0042 m3 water
m-3 LF Similarly the highest value in the range is 014 m3 water m-3 LF which is equivalent to
070 T times 020 The average volumetric moisture content is 0091 m3 water m-3 LF
Volumetric gas content of the waste εa (m3 airm3 LF) A range of 010 to 040 was assumed for
the volumetric gas content of the waste There is very little data on measured values of the
effective porosity of waste Bendz et al (25) reported a measured value of 012 for a waste
sample from an operating MSW landfill Based on the range specified above the average value
for the volumetric gas content of the waste is 025
Fraction of organic carbon foc A range of 040 to 060 was used for the fraction of organic
carbon in the waste A value of 050 was reported for a sample of MSW (26) which will be used
as the average value in the bounding calculations
Height of the waste in the landfill H (m) The height of waste in the landfill is assumed to vary
between 183 and 61 m Based on this range the average height of waste in the landfill was 397
m
The final two terms required to describe the landfill infiltration and the gas production rate
are a function of the climate in which the landfill is located As a result two sets of values for
these parameters were used to represent an arid or a wet climate
Net precipitation N (myear) The net precipitation or infiltration was calculated based on data
reported in Camobreco et al (27) For the arid climate scenario data from sites with less than
05 m yr-1 of total precipitation were used while the data from sites with greater than or equal to
S13
05 m yr-1 were used for the wet climate scenario For each site the total precipitation was
multiplied by the percentage of precipitation that becomes leachate to determine the net
precipitation or infiltration Using this method infiltration for the arid climate was found to
range from 002 to 005 m yr-1 with an average value of 004 m yr-1 Infiltration for the wet
climate ranged from 004 to 032 m yr-1 with an average of 012 m yr-1 Although the data used
to generate these estimates encompassed a variety of different percentages of final cover it
should be noted that modeling a dry (fully capped) landfill is potentially a more realistic scenario
than a wet landfill since the building debris will likely be encapsulated and the greatest
likelihood for leakage from the containers will occur after the final cover has been placed when
infiltration is minimal
Gas production rate qa (m3 LFG m-3 LF yr-1) The landfill gas (LFG) production rate can be
described by the following equation (28)
qa=2WLoke-kt (S24)
where W is the mass of refuse Lo is a term representing the ultimate volume of methane gas
produced per unit of wet waste and k is a rate constant (yr-1) Equation S24 assumes a methane
concentration of 50 in LFG
The mass of refuse (W) is a function of the bulk density of the waste which as stated above
was assumed to vary from 042 to 070 T m-3 with an average value of 055 T m-3 Assuming 1
m3 of waste W will be equal to 055 T Lo was assumed to vary between 85 and 170 L methane
kg-1 wet waste The value of 170 L methane kg-1 wet waste is the default used in the New
Source Performance Standards of the Clean Air Act amendments (29) For the arid climate
scenario the rate constant (k) was set to 002 yr-1 For the wet climate scenario the rate constant
(k) was set to 005 yr-1 For the arid scenario qa was found to range from 19 to 37 m3 LFG m-3
S14
LF yr-1 with an average value of 28 m3 LFG m-3 LF yr-1 For the wet scenario qa was found to
range from 45 to 90 m3 LFG m-3 LF yr-1 with an average value of 675 m3 LFG m-3 LF yr-1
Thickness of cover L (m) The thickness of the landfill cover was set to 045 m which is the
minimum thickness specified by Subtitle D regulation for the thickness of the barrier layer (30)
This value was not varied in the bounding calculations
Total porosity of the soil cover εsc (dimensionless) The total porosity of the soil cover ranged
from 03 to 05 with an average value of 04 A total porosity between 03 and 05 is common for
a wide range of soil types
Gravimetric moisture content of soil cover (MCSC) The gravimetric moisture content of the soil
cover ranged from 103 to 308 (dry weight basis) with an average value of 200 based
published data (31)
Dry bulk density of the cover soil ρbSC (g cm-3) The dry bulk density of the soil cover ranged
from 13 to 20 g cm-3 with an average value of 17 g cm-3 based on published data (31) It
should be noted that the gravimetric moisture content and dry bulk density of the cover soil are
not used directly in MOCLA These parameters are used along with the porosity of the cover
soil to calculate the air-filled porosity of the cover soil which is an input parameter to MOCLA
Liner thickness Lliner (m) The thickness of the landfill liner was set to 06 m which is the
minimum thickness required by EPA Subtitle D regulation (30) The liner thickness was not
varied in the bounding calculations
Total porosity of the liner εL (dimensionless) The total porosity of the liner ranged from 03 to
05 with an average value of 04 A total porosity between 03 and 05 is common for a wide
range of soil types
S15
Gravimetric moisture content of the liner (MCL) Based on published data (31) the gravimetric
moisture content of the liner ranged from 103 to 308 with an average value of 200
Dry bulk density of the liner materials ρb L (g cm-3) Based on published data (31) the dry bulk
density of the liner ranged from 13 to 20 g cm-3 with an average value of 17 g cm-3 It should
be noted that the gravimetric moisture content and dry bulk density of the liner are not used
directly in MOCLA These parameters are used along with the porosity of the liner to calculate
the air-filled porosity of the liner which is an input parameter to MOCLA
S16
Table S1 List of Studied CWAs and TICs Military
Designation Common Name Chemical Formula CAS number Use
Carbon disulfide CS2 75-15-0 Toxic Industrial Chemical
Furan C4H4O 110-00-9 Toxic Industrial Chemical
HHD Mustard Gas C4H8Cl2S 505-60-2 Blister AgentVesicant
a Data compiled from the following sources (10 32-39) b Estimated with EPISuite v312 (40) c Hydrolysis rate estimated to be on the order of 10 min-1 at 20degC (41) d Hydrolysis half-life for ED estimated to be equal to that of L based on structural similarity e Half-life calculated based on 5 disappearance after 6 d (2) f Value estimated by averaging hydrolysis half-lives of GA GB and GD g Hydrolysis half-life estimated to be equal to that of VX based on structural similarity h Temperature not reported i Estimated using Wilke-Lee equation (42) j Estimated using Hayduk-Laudie equation (42) k pKa for CX estimated from a range of calculated pKa values for chloro-substituted oximes (43) l Estimated using Chem-Silico software package (44) m pKa for VG and VM estimated to be equivalent to that of VX MW is molecular weight bp is boiling point fp is freezing point KH is the Henryrsquos Law constant Kow is the octanol-water partition coefficient
S18Table S3 Henryrsquos law constant ranges for organic compounds originally modeled in MOCLA
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S7
Box S2 Additional MOCLA equations
The sum of the specific gas production rate and diffusional lsquoflowrsquo is combined into a specific gas flow qa
rsquo qa
rsquo = qa + qD (S7) where qa is the specific gas production rate (m-3 landfill gas m-3 waste yr-1) and qD the diffusional lsquoflowrsquo is calculated from
LV
ADq
SC
airSCaD 2
310
εε
= (S8)
Dair is the molecular diffusion coefficient of the chemical in air (m2 yr-1) εSC is the total porosity of the soil cover (m3 pore space m-3 soil cover) εaSC is the volumetric content of air in the soil cover (m3 air m-3 soil cover) L is the thickness of the soil cover (m) A is the surface area of the landfill (m2) V is the total volume of waste in the landfill (m3)
For neutral compounds Koc the distribution coefficient between solid organic carbon and water is calculated from
log Koc = 072log Kow+049 (S9) where Kow is the octanol-water distribution coefficient (dimensionless)
For organic bases (tertiary amines) Koc (pH) the pH-dependent distribution coefficient is calculated from (20)
Koc (pH) = (1-α) Koc (S10) where Koc is the distribution coefficient for the neutral compound and α the fraction of the non-dissociated (cationic) species is calculated from
α = 1(1+10(pH-pKa)) (S11)
S8
Box S3 Incorporation of liner diffusion term into MOCLA
In addition to the processes originally modeled by MOCLA a term was incorporated to evaluate diffusion through the composite liner The diffusive flux through the liner can be expressed by
xCDJ Diff partpart
= (S12)
where JDiff is the diffusive flux through the liner (g m-2 yr-1) D is the diffusion coefficient in the soil cover partCpartx is the concentration gradient (g m-4)
The diffusion coefficient (D) in eqn S12 is the effective diffusion coefficient for the composite geomembraneclay liner It was assumed that the geomembrane layer does not impede the diffusive flux through the composite liner as volatile organic compounds have been shown to penetrate geomembranes at an appreciable rate (22) Therefore the diffusion coefficient for the composite liner was represented by the effective diffusion coefficient for the clay layer Since clay liners are typically compacted at a moisture content less than saturation diffusion will occur through both the air-filled and water-filled pore spaces within the clay In a porous medium the effective diffusion coefficient for each phase (D
air or D
water) is calculated from the molecular diffusivity of the compound in air or water (Dair or Dwater) the total porosity of the clay liner (εL) and the air- or water-filled porosity of the liner (εaL or εwL) One commonly-used expression is the Millington equation which relates the effective diffusion coefficient to the molecular diffusion coefficient by (23)
2
333
L
Laairair DD
ε
ε= (S13)
and
2
333
L
Lwwaterwater DD
ε
ε= (S14)
S9
Box S3 (continued) Incorporation of liner diffusion term into MOCLA
Combining expressions S13 and S14 along with Henryrsquos Law results in the following equation for the diffusive flux through the liner (24)
x
CK
DDJ a
L
Lw
H
water
L
LaairDiff part
part⎟⎟⎠
⎞⎜⎜⎝
⎛+= 2
333
2
333
ε
ε
ε
ε (S15)
where Ca is equal to the gas-phase concentration of the contaminant If it is assumed that the concentration of the contaminant of interest in the aquifer beneath the liner is equal to zero then the sink due to diffusion through the composite liner may be written as
liner
a
L
Lw
H
water
L
LaairDiff L
CA
KD
DS ⎟⎟⎠
⎞⎜⎜⎝
⎛+= 2
333
2
333
ε
ε
ε
ε (S16)
where SDiff is the sink due to diffusion through the liner (g yr-1) Lliner is the thickness of the clay layer of the composite liner (m) SDiff can be simplified to SDiff = QD linerCa (S17) where
liner
effLinerD L
ADQ = (S18)
and
2
333
2
333
L
Lw
H
water
L
Laaireff K
DDD
ε
ε
ε
ε+= (S19)
Because literature values for εaSC and εaL were not available these terms were calculated as
)0max( scscbscSCa MCsdotminus= ρεε (S20) and
)0max( LLbLLa MCsdotminus= ρεε (S21) where εsc and εL are the total porosity of the soil cover and liner (m3 voids m-3 cover or liner) ρbSC and ρbL are the dry bulk density of the soil cover and liner (g soil m-3 cover or liner) MCSC and MCL are the gravimetric moisture content of the soil cover and liner ()
S10
Box S3 (continued) Incorporation of liner diffusion term into MOCLA
Including the diffusive flux term into the original MOCLA mass balance equation gives
( )diffwgdaT SSSSS
dtVCd
++++minus= λ)( (S22)
rearranging this expression gives
⎟⎟⎠
⎞⎜⎜⎝
⎛+++minus=
VQ
KHKNq
dtdC linerD
H
w
Ha
T λε (S23)
if qrsquo
D liner = QD liner V then a new expression for k can be written
linerD
H
w
Ha q
KHKNqk +++=
λε (S24)
Integrating each term on the right-hand side of eqn S22 gives the expressions for the fate routes The new expression for fate via liner diffusion is written as
))exp(1( t
RkqF
alinerDdiff minusminus= (S23)
S11
Methodology used to determine MOCLA input parameter values (physical parameters)
To evaluate the distribution and fate of chemicals in a landfill data for a number of input
parameters describing the landfill design and operation are required This section describes each
parameter and provides an explanation of how parameter values that could be applicable under
various disposal scenarios were determined
Dry bulk density of the waste ρb (T m-3) It is assumed that the building debris will be contained
for transport and burial and therefore will not be compacted after placement in the landfill
Therefore the wet bulk density of the building debris will likely be lower than the average value
of wet bulk density for compacted waste which is about 076 T m-3 The range of wet bulk
densities to be used in the bounding calculations was 042 to 070 T m-3 with an average value of
055 T m-3
The dry bulk density was determined from the wet bulk density and an estimate of the
gravimetric moisture content of the waste If the gravimetric moisture content (MC) of the waste
is assumed to be 10-20 (wet weight basis) then the dry bulk density can be calculated as
follows
Using a design basis of 1 m3 of refuse the total mass of waste is equal to 042 T which
corresponds to the low end of the range The mass of water in 1 m3 of refuse is equal to 042
times 020 (highest possible value of MC) or 0084 T The total mass of waste minus the mass of
water (042 - 0084) results in the mass of dry refuse which is 034 T Therefore the low value
of the range for dry bulk density is 034 T m-3 Similarly the high end of the range is 063 T m-3
The average value is 049 T m-3
Volumetric moisture content of the waste εw (m3 water m-3 LF) The possible values of
volumetric moisture content of the waste can be calculated from the ranges of the wet bulk
S12
density and the gravimetric moisture content assuming 1 m3 of waste The lowest value in the
range of volumetric moisture contents is calculated at 10 gravimetric moisture The mass of
water in 1 m3 of waste is 042 T (total mass) times 010 (mass of watertotal mass) which is 0042
T The density of water is 1 T m-3 so the volumetric moisture content is equal to 0042 m3 water
m-3 LF Similarly the highest value in the range is 014 m3 water m-3 LF which is equivalent to
070 T times 020 The average volumetric moisture content is 0091 m3 water m-3 LF
Volumetric gas content of the waste εa (m3 airm3 LF) A range of 010 to 040 was assumed for
the volumetric gas content of the waste There is very little data on measured values of the
effective porosity of waste Bendz et al (25) reported a measured value of 012 for a waste
sample from an operating MSW landfill Based on the range specified above the average value
for the volumetric gas content of the waste is 025
Fraction of organic carbon foc A range of 040 to 060 was used for the fraction of organic
carbon in the waste A value of 050 was reported for a sample of MSW (26) which will be used
as the average value in the bounding calculations
Height of the waste in the landfill H (m) The height of waste in the landfill is assumed to vary
between 183 and 61 m Based on this range the average height of waste in the landfill was 397
m
The final two terms required to describe the landfill infiltration and the gas production rate
are a function of the climate in which the landfill is located As a result two sets of values for
these parameters were used to represent an arid or a wet climate
Net precipitation N (myear) The net precipitation or infiltration was calculated based on data
reported in Camobreco et al (27) For the arid climate scenario data from sites with less than
05 m yr-1 of total precipitation were used while the data from sites with greater than or equal to
S13
05 m yr-1 were used for the wet climate scenario For each site the total precipitation was
multiplied by the percentage of precipitation that becomes leachate to determine the net
precipitation or infiltration Using this method infiltration for the arid climate was found to
range from 002 to 005 m yr-1 with an average value of 004 m yr-1 Infiltration for the wet
climate ranged from 004 to 032 m yr-1 with an average of 012 m yr-1 Although the data used
to generate these estimates encompassed a variety of different percentages of final cover it
should be noted that modeling a dry (fully capped) landfill is potentially a more realistic scenario
than a wet landfill since the building debris will likely be encapsulated and the greatest
likelihood for leakage from the containers will occur after the final cover has been placed when
infiltration is minimal
Gas production rate qa (m3 LFG m-3 LF yr-1) The landfill gas (LFG) production rate can be
described by the following equation (28)
qa=2WLoke-kt (S24)
where W is the mass of refuse Lo is a term representing the ultimate volume of methane gas
produced per unit of wet waste and k is a rate constant (yr-1) Equation S24 assumes a methane
concentration of 50 in LFG
The mass of refuse (W) is a function of the bulk density of the waste which as stated above
was assumed to vary from 042 to 070 T m-3 with an average value of 055 T m-3 Assuming 1
m3 of waste W will be equal to 055 T Lo was assumed to vary between 85 and 170 L methane
kg-1 wet waste The value of 170 L methane kg-1 wet waste is the default used in the New
Source Performance Standards of the Clean Air Act amendments (29) For the arid climate
scenario the rate constant (k) was set to 002 yr-1 For the wet climate scenario the rate constant
(k) was set to 005 yr-1 For the arid scenario qa was found to range from 19 to 37 m3 LFG m-3
S14
LF yr-1 with an average value of 28 m3 LFG m-3 LF yr-1 For the wet scenario qa was found to
range from 45 to 90 m3 LFG m-3 LF yr-1 with an average value of 675 m3 LFG m-3 LF yr-1
Thickness of cover L (m) The thickness of the landfill cover was set to 045 m which is the
minimum thickness specified by Subtitle D regulation for the thickness of the barrier layer (30)
This value was not varied in the bounding calculations
Total porosity of the soil cover εsc (dimensionless) The total porosity of the soil cover ranged
from 03 to 05 with an average value of 04 A total porosity between 03 and 05 is common for
a wide range of soil types
Gravimetric moisture content of soil cover (MCSC) The gravimetric moisture content of the soil
cover ranged from 103 to 308 (dry weight basis) with an average value of 200 based
published data (31)
Dry bulk density of the cover soil ρbSC (g cm-3) The dry bulk density of the soil cover ranged
from 13 to 20 g cm-3 with an average value of 17 g cm-3 based on published data (31) It
should be noted that the gravimetric moisture content and dry bulk density of the cover soil are
not used directly in MOCLA These parameters are used along with the porosity of the cover
soil to calculate the air-filled porosity of the cover soil which is an input parameter to MOCLA
Liner thickness Lliner (m) The thickness of the landfill liner was set to 06 m which is the
minimum thickness required by EPA Subtitle D regulation (30) The liner thickness was not
varied in the bounding calculations
Total porosity of the liner εL (dimensionless) The total porosity of the liner ranged from 03 to
05 with an average value of 04 A total porosity between 03 and 05 is common for a wide
range of soil types
S15
Gravimetric moisture content of the liner (MCL) Based on published data (31) the gravimetric
moisture content of the liner ranged from 103 to 308 with an average value of 200
Dry bulk density of the liner materials ρb L (g cm-3) Based on published data (31) the dry bulk
density of the liner ranged from 13 to 20 g cm-3 with an average value of 17 g cm-3 It should
be noted that the gravimetric moisture content and dry bulk density of the liner are not used
directly in MOCLA These parameters are used along with the porosity of the liner to calculate
the air-filled porosity of the liner which is an input parameter to MOCLA
S16
Table S1 List of Studied CWAs and TICs Military
Designation Common Name Chemical Formula CAS number Use
Carbon disulfide CS2 75-15-0 Toxic Industrial Chemical
Furan C4H4O 110-00-9 Toxic Industrial Chemical
HHD Mustard Gas C4H8Cl2S 505-60-2 Blister AgentVesicant
a Data compiled from the following sources (10 32-39) b Estimated with EPISuite v312 (40) c Hydrolysis rate estimated to be on the order of 10 min-1 at 20degC (41) d Hydrolysis half-life for ED estimated to be equal to that of L based on structural similarity e Half-life calculated based on 5 disappearance after 6 d (2) f Value estimated by averaging hydrolysis half-lives of GA GB and GD g Hydrolysis half-life estimated to be equal to that of VX based on structural similarity h Temperature not reported i Estimated using Wilke-Lee equation (42) j Estimated using Hayduk-Laudie equation (42) k pKa for CX estimated from a range of calculated pKa values for chloro-substituted oximes (43) l Estimated using Chem-Silico software package (44) m pKa for VG and VM estimated to be equivalent to that of VX MW is molecular weight bp is boiling point fp is freezing point KH is the Henryrsquos Law constant Kow is the octanol-water partition coefficient
S18Table S3 Henryrsquos law constant ranges for organic compounds originally modeled in MOCLA
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S8
Box S3 Incorporation of liner diffusion term into MOCLA
In addition to the processes originally modeled by MOCLA a term was incorporated to evaluate diffusion through the composite liner The diffusive flux through the liner can be expressed by
xCDJ Diff partpart
= (S12)
where JDiff is the diffusive flux through the liner (g m-2 yr-1) D is the diffusion coefficient in the soil cover partCpartx is the concentration gradient (g m-4)
The diffusion coefficient (D) in eqn S12 is the effective diffusion coefficient for the composite geomembraneclay liner It was assumed that the geomembrane layer does not impede the diffusive flux through the composite liner as volatile organic compounds have been shown to penetrate geomembranes at an appreciable rate (22) Therefore the diffusion coefficient for the composite liner was represented by the effective diffusion coefficient for the clay layer Since clay liners are typically compacted at a moisture content less than saturation diffusion will occur through both the air-filled and water-filled pore spaces within the clay In a porous medium the effective diffusion coefficient for each phase (D
air or D
water) is calculated from the molecular diffusivity of the compound in air or water (Dair or Dwater) the total porosity of the clay liner (εL) and the air- or water-filled porosity of the liner (εaL or εwL) One commonly-used expression is the Millington equation which relates the effective diffusion coefficient to the molecular diffusion coefficient by (23)
2
333
L
Laairair DD
ε
ε= (S13)
and
2
333
L
Lwwaterwater DD
ε
ε= (S14)
S9
Box S3 (continued) Incorporation of liner diffusion term into MOCLA
Combining expressions S13 and S14 along with Henryrsquos Law results in the following equation for the diffusive flux through the liner (24)
x
CK
DDJ a
L
Lw
H
water
L
LaairDiff part
part⎟⎟⎠
⎞⎜⎜⎝
⎛+= 2
333
2
333
ε
ε
ε
ε (S15)
where Ca is equal to the gas-phase concentration of the contaminant If it is assumed that the concentration of the contaminant of interest in the aquifer beneath the liner is equal to zero then the sink due to diffusion through the composite liner may be written as
liner
a
L
Lw
H
water
L
LaairDiff L
CA
KD
DS ⎟⎟⎠
⎞⎜⎜⎝
⎛+= 2
333
2
333
ε
ε
ε
ε (S16)
where SDiff is the sink due to diffusion through the liner (g yr-1) Lliner is the thickness of the clay layer of the composite liner (m) SDiff can be simplified to SDiff = QD linerCa (S17) where
liner
effLinerD L
ADQ = (S18)
and
2
333
2
333
L
Lw
H
water
L
Laaireff K
DDD
ε
ε
ε
ε+= (S19)
Because literature values for εaSC and εaL were not available these terms were calculated as
)0max( scscbscSCa MCsdotminus= ρεε (S20) and
)0max( LLbLLa MCsdotminus= ρεε (S21) where εsc and εL are the total porosity of the soil cover and liner (m3 voids m-3 cover or liner) ρbSC and ρbL are the dry bulk density of the soil cover and liner (g soil m-3 cover or liner) MCSC and MCL are the gravimetric moisture content of the soil cover and liner ()
S10
Box S3 (continued) Incorporation of liner diffusion term into MOCLA
Including the diffusive flux term into the original MOCLA mass balance equation gives
( )diffwgdaT SSSSS
dtVCd
++++minus= λ)( (S22)
rearranging this expression gives
⎟⎟⎠
⎞⎜⎜⎝
⎛+++minus=
VQ
KHKNq
dtdC linerD
H
w
Ha
T λε (S23)
if qrsquo
D liner = QD liner V then a new expression for k can be written
linerD
H
w
Ha q
KHKNqk +++=
λε (S24)
Integrating each term on the right-hand side of eqn S22 gives the expressions for the fate routes The new expression for fate via liner diffusion is written as
))exp(1( t
RkqF
alinerDdiff minusminus= (S23)
S11
Methodology used to determine MOCLA input parameter values (physical parameters)
To evaluate the distribution and fate of chemicals in a landfill data for a number of input
parameters describing the landfill design and operation are required This section describes each
parameter and provides an explanation of how parameter values that could be applicable under
various disposal scenarios were determined
Dry bulk density of the waste ρb (T m-3) It is assumed that the building debris will be contained
for transport and burial and therefore will not be compacted after placement in the landfill
Therefore the wet bulk density of the building debris will likely be lower than the average value
of wet bulk density for compacted waste which is about 076 T m-3 The range of wet bulk
densities to be used in the bounding calculations was 042 to 070 T m-3 with an average value of
055 T m-3
The dry bulk density was determined from the wet bulk density and an estimate of the
gravimetric moisture content of the waste If the gravimetric moisture content (MC) of the waste
is assumed to be 10-20 (wet weight basis) then the dry bulk density can be calculated as
follows
Using a design basis of 1 m3 of refuse the total mass of waste is equal to 042 T which
corresponds to the low end of the range The mass of water in 1 m3 of refuse is equal to 042
times 020 (highest possible value of MC) or 0084 T The total mass of waste minus the mass of
water (042 - 0084) results in the mass of dry refuse which is 034 T Therefore the low value
of the range for dry bulk density is 034 T m-3 Similarly the high end of the range is 063 T m-3
The average value is 049 T m-3
Volumetric moisture content of the waste εw (m3 water m-3 LF) The possible values of
volumetric moisture content of the waste can be calculated from the ranges of the wet bulk
S12
density and the gravimetric moisture content assuming 1 m3 of waste The lowest value in the
range of volumetric moisture contents is calculated at 10 gravimetric moisture The mass of
water in 1 m3 of waste is 042 T (total mass) times 010 (mass of watertotal mass) which is 0042
T The density of water is 1 T m-3 so the volumetric moisture content is equal to 0042 m3 water
m-3 LF Similarly the highest value in the range is 014 m3 water m-3 LF which is equivalent to
070 T times 020 The average volumetric moisture content is 0091 m3 water m-3 LF
Volumetric gas content of the waste εa (m3 airm3 LF) A range of 010 to 040 was assumed for
the volumetric gas content of the waste There is very little data on measured values of the
effective porosity of waste Bendz et al (25) reported a measured value of 012 for a waste
sample from an operating MSW landfill Based on the range specified above the average value
for the volumetric gas content of the waste is 025
Fraction of organic carbon foc A range of 040 to 060 was used for the fraction of organic
carbon in the waste A value of 050 was reported for a sample of MSW (26) which will be used
as the average value in the bounding calculations
Height of the waste in the landfill H (m) The height of waste in the landfill is assumed to vary
between 183 and 61 m Based on this range the average height of waste in the landfill was 397
m
The final two terms required to describe the landfill infiltration and the gas production rate
are a function of the climate in which the landfill is located As a result two sets of values for
these parameters were used to represent an arid or a wet climate
Net precipitation N (myear) The net precipitation or infiltration was calculated based on data
reported in Camobreco et al (27) For the arid climate scenario data from sites with less than
05 m yr-1 of total precipitation were used while the data from sites with greater than or equal to
S13
05 m yr-1 were used for the wet climate scenario For each site the total precipitation was
multiplied by the percentage of precipitation that becomes leachate to determine the net
precipitation or infiltration Using this method infiltration for the arid climate was found to
range from 002 to 005 m yr-1 with an average value of 004 m yr-1 Infiltration for the wet
climate ranged from 004 to 032 m yr-1 with an average of 012 m yr-1 Although the data used
to generate these estimates encompassed a variety of different percentages of final cover it
should be noted that modeling a dry (fully capped) landfill is potentially a more realistic scenario
than a wet landfill since the building debris will likely be encapsulated and the greatest
likelihood for leakage from the containers will occur after the final cover has been placed when
infiltration is minimal
Gas production rate qa (m3 LFG m-3 LF yr-1) The landfill gas (LFG) production rate can be
described by the following equation (28)
qa=2WLoke-kt (S24)
where W is the mass of refuse Lo is a term representing the ultimate volume of methane gas
produced per unit of wet waste and k is a rate constant (yr-1) Equation S24 assumes a methane
concentration of 50 in LFG
The mass of refuse (W) is a function of the bulk density of the waste which as stated above
was assumed to vary from 042 to 070 T m-3 with an average value of 055 T m-3 Assuming 1
m3 of waste W will be equal to 055 T Lo was assumed to vary between 85 and 170 L methane
kg-1 wet waste The value of 170 L methane kg-1 wet waste is the default used in the New
Source Performance Standards of the Clean Air Act amendments (29) For the arid climate
scenario the rate constant (k) was set to 002 yr-1 For the wet climate scenario the rate constant
(k) was set to 005 yr-1 For the arid scenario qa was found to range from 19 to 37 m3 LFG m-3
S14
LF yr-1 with an average value of 28 m3 LFG m-3 LF yr-1 For the wet scenario qa was found to
range from 45 to 90 m3 LFG m-3 LF yr-1 with an average value of 675 m3 LFG m-3 LF yr-1
Thickness of cover L (m) The thickness of the landfill cover was set to 045 m which is the
minimum thickness specified by Subtitle D regulation for the thickness of the barrier layer (30)
This value was not varied in the bounding calculations
Total porosity of the soil cover εsc (dimensionless) The total porosity of the soil cover ranged
from 03 to 05 with an average value of 04 A total porosity between 03 and 05 is common for
a wide range of soil types
Gravimetric moisture content of soil cover (MCSC) The gravimetric moisture content of the soil
cover ranged from 103 to 308 (dry weight basis) with an average value of 200 based
published data (31)
Dry bulk density of the cover soil ρbSC (g cm-3) The dry bulk density of the soil cover ranged
from 13 to 20 g cm-3 with an average value of 17 g cm-3 based on published data (31) It
should be noted that the gravimetric moisture content and dry bulk density of the cover soil are
not used directly in MOCLA These parameters are used along with the porosity of the cover
soil to calculate the air-filled porosity of the cover soil which is an input parameter to MOCLA
Liner thickness Lliner (m) The thickness of the landfill liner was set to 06 m which is the
minimum thickness required by EPA Subtitle D regulation (30) The liner thickness was not
varied in the bounding calculations
Total porosity of the liner εL (dimensionless) The total porosity of the liner ranged from 03 to
05 with an average value of 04 A total porosity between 03 and 05 is common for a wide
range of soil types
S15
Gravimetric moisture content of the liner (MCL) Based on published data (31) the gravimetric
moisture content of the liner ranged from 103 to 308 with an average value of 200
Dry bulk density of the liner materials ρb L (g cm-3) Based on published data (31) the dry bulk
density of the liner ranged from 13 to 20 g cm-3 with an average value of 17 g cm-3 It should
be noted that the gravimetric moisture content and dry bulk density of the liner are not used
directly in MOCLA These parameters are used along with the porosity of the liner to calculate
the air-filled porosity of the liner which is an input parameter to MOCLA
S16
Table S1 List of Studied CWAs and TICs Military
Designation Common Name Chemical Formula CAS number Use
Carbon disulfide CS2 75-15-0 Toxic Industrial Chemical
Furan C4H4O 110-00-9 Toxic Industrial Chemical
HHD Mustard Gas C4H8Cl2S 505-60-2 Blister AgentVesicant
a Data compiled from the following sources (10 32-39) b Estimated with EPISuite v312 (40) c Hydrolysis rate estimated to be on the order of 10 min-1 at 20degC (41) d Hydrolysis half-life for ED estimated to be equal to that of L based on structural similarity e Half-life calculated based on 5 disappearance after 6 d (2) f Value estimated by averaging hydrolysis half-lives of GA GB and GD g Hydrolysis half-life estimated to be equal to that of VX based on structural similarity h Temperature not reported i Estimated using Wilke-Lee equation (42) j Estimated using Hayduk-Laudie equation (42) k pKa for CX estimated from a range of calculated pKa values for chloro-substituted oximes (43) l Estimated using Chem-Silico software package (44) m pKa for VG and VM estimated to be equivalent to that of VX MW is molecular weight bp is boiling point fp is freezing point KH is the Henryrsquos Law constant Kow is the octanol-water partition coefficient
S18Table S3 Henryrsquos law constant ranges for organic compounds originally modeled in MOCLA
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S9
Box S3 (continued) Incorporation of liner diffusion term into MOCLA
Combining expressions S13 and S14 along with Henryrsquos Law results in the following equation for the diffusive flux through the liner (24)
x
CK
DDJ a
L
Lw
H
water
L
LaairDiff part
part⎟⎟⎠
⎞⎜⎜⎝
⎛+= 2
333
2
333
ε
ε
ε
ε (S15)
where Ca is equal to the gas-phase concentration of the contaminant If it is assumed that the concentration of the contaminant of interest in the aquifer beneath the liner is equal to zero then the sink due to diffusion through the composite liner may be written as
liner
a
L
Lw
H
water
L
LaairDiff L
CA
KD
DS ⎟⎟⎠
⎞⎜⎜⎝
⎛+= 2
333
2
333
ε
ε
ε
ε (S16)
where SDiff is the sink due to diffusion through the liner (g yr-1) Lliner is the thickness of the clay layer of the composite liner (m) SDiff can be simplified to SDiff = QD linerCa (S17) where
liner
effLinerD L
ADQ = (S18)
and
2
333
2
333
L
Lw
H
water
L
Laaireff K
DDD
ε
ε
ε
ε+= (S19)
Because literature values for εaSC and εaL were not available these terms were calculated as
)0max( scscbscSCa MCsdotminus= ρεε (S20) and
)0max( LLbLLa MCsdotminus= ρεε (S21) where εsc and εL are the total porosity of the soil cover and liner (m3 voids m-3 cover or liner) ρbSC and ρbL are the dry bulk density of the soil cover and liner (g soil m-3 cover or liner) MCSC and MCL are the gravimetric moisture content of the soil cover and liner ()
S10
Box S3 (continued) Incorporation of liner diffusion term into MOCLA
Including the diffusive flux term into the original MOCLA mass balance equation gives
( )diffwgdaT SSSSS
dtVCd
++++minus= λ)( (S22)
rearranging this expression gives
⎟⎟⎠
⎞⎜⎜⎝
⎛+++minus=
VQ
KHKNq
dtdC linerD
H
w
Ha
T λε (S23)
if qrsquo
D liner = QD liner V then a new expression for k can be written
linerD
H
w
Ha q
KHKNqk +++=
λε (S24)
Integrating each term on the right-hand side of eqn S22 gives the expressions for the fate routes The new expression for fate via liner diffusion is written as
))exp(1( t
RkqF
alinerDdiff minusminus= (S23)
S11
Methodology used to determine MOCLA input parameter values (physical parameters)
To evaluate the distribution and fate of chemicals in a landfill data for a number of input
parameters describing the landfill design and operation are required This section describes each
parameter and provides an explanation of how parameter values that could be applicable under
various disposal scenarios were determined
Dry bulk density of the waste ρb (T m-3) It is assumed that the building debris will be contained
for transport and burial and therefore will not be compacted after placement in the landfill
Therefore the wet bulk density of the building debris will likely be lower than the average value
of wet bulk density for compacted waste which is about 076 T m-3 The range of wet bulk
densities to be used in the bounding calculations was 042 to 070 T m-3 with an average value of
055 T m-3
The dry bulk density was determined from the wet bulk density and an estimate of the
gravimetric moisture content of the waste If the gravimetric moisture content (MC) of the waste
is assumed to be 10-20 (wet weight basis) then the dry bulk density can be calculated as
follows
Using a design basis of 1 m3 of refuse the total mass of waste is equal to 042 T which
corresponds to the low end of the range The mass of water in 1 m3 of refuse is equal to 042
times 020 (highest possible value of MC) or 0084 T The total mass of waste minus the mass of
water (042 - 0084) results in the mass of dry refuse which is 034 T Therefore the low value
of the range for dry bulk density is 034 T m-3 Similarly the high end of the range is 063 T m-3
The average value is 049 T m-3
Volumetric moisture content of the waste εw (m3 water m-3 LF) The possible values of
volumetric moisture content of the waste can be calculated from the ranges of the wet bulk
S12
density and the gravimetric moisture content assuming 1 m3 of waste The lowest value in the
range of volumetric moisture contents is calculated at 10 gravimetric moisture The mass of
water in 1 m3 of waste is 042 T (total mass) times 010 (mass of watertotal mass) which is 0042
T The density of water is 1 T m-3 so the volumetric moisture content is equal to 0042 m3 water
m-3 LF Similarly the highest value in the range is 014 m3 water m-3 LF which is equivalent to
070 T times 020 The average volumetric moisture content is 0091 m3 water m-3 LF
Volumetric gas content of the waste εa (m3 airm3 LF) A range of 010 to 040 was assumed for
the volumetric gas content of the waste There is very little data on measured values of the
effective porosity of waste Bendz et al (25) reported a measured value of 012 for a waste
sample from an operating MSW landfill Based on the range specified above the average value
for the volumetric gas content of the waste is 025
Fraction of organic carbon foc A range of 040 to 060 was used for the fraction of organic
carbon in the waste A value of 050 was reported for a sample of MSW (26) which will be used
as the average value in the bounding calculations
Height of the waste in the landfill H (m) The height of waste in the landfill is assumed to vary
between 183 and 61 m Based on this range the average height of waste in the landfill was 397
m
The final two terms required to describe the landfill infiltration and the gas production rate
are a function of the climate in which the landfill is located As a result two sets of values for
these parameters were used to represent an arid or a wet climate
Net precipitation N (myear) The net precipitation or infiltration was calculated based on data
reported in Camobreco et al (27) For the arid climate scenario data from sites with less than
05 m yr-1 of total precipitation were used while the data from sites with greater than or equal to
S13
05 m yr-1 were used for the wet climate scenario For each site the total precipitation was
multiplied by the percentage of precipitation that becomes leachate to determine the net
precipitation or infiltration Using this method infiltration for the arid climate was found to
range from 002 to 005 m yr-1 with an average value of 004 m yr-1 Infiltration for the wet
climate ranged from 004 to 032 m yr-1 with an average of 012 m yr-1 Although the data used
to generate these estimates encompassed a variety of different percentages of final cover it
should be noted that modeling a dry (fully capped) landfill is potentially a more realistic scenario
than a wet landfill since the building debris will likely be encapsulated and the greatest
likelihood for leakage from the containers will occur after the final cover has been placed when
infiltration is minimal
Gas production rate qa (m3 LFG m-3 LF yr-1) The landfill gas (LFG) production rate can be
described by the following equation (28)
qa=2WLoke-kt (S24)
where W is the mass of refuse Lo is a term representing the ultimate volume of methane gas
produced per unit of wet waste and k is a rate constant (yr-1) Equation S24 assumes a methane
concentration of 50 in LFG
The mass of refuse (W) is a function of the bulk density of the waste which as stated above
was assumed to vary from 042 to 070 T m-3 with an average value of 055 T m-3 Assuming 1
m3 of waste W will be equal to 055 T Lo was assumed to vary between 85 and 170 L methane
kg-1 wet waste The value of 170 L methane kg-1 wet waste is the default used in the New
Source Performance Standards of the Clean Air Act amendments (29) For the arid climate
scenario the rate constant (k) was set to 002 yr-1 For the wet climate scenario the rate constant
(k) was set to 005 yr-1 For the arid scenario qa was found to range from 19 to 37 m3 LFG m-3
S14
LF yr-1 with an average value of 28 m3 LFG m-3 LF yr-1 For the wet scenario qa was found to
range from 45 to 90 m3 LFG m-3 LF yr-1 with an average value of 675 m3 LFG m-3 LF yr-1
Thickness of cover L (m) The thickness of the landfill cover was set to 045 m which is the
minimum thickness specified by Subtitle D regulation for the thickness of the barrier layer (30)
This value was not varied in the bounding calculations
Total porosity of the soil cover εsc (dimensionless) The total porosity of the soil cover ranged
from 03 to 05 with an average value of 04 A total porosity between 03 and 05 is common for
a wide range of soil types
Gravimetric moisture content of soil cover (MCSC) The gravimetric moisture content of the soil
cover ranged from 103 to 308 (dry weight basis) with an average value of 200 based
published data (31)
Dry bulk density of the cover soil ρbSC (g cm-3) The dry bulk density of the soil cover ranged
from 13 to 20 g cm-3 with an average value of 17 g cm-3 based on published data (31) It
should be noted that the gravimetric moisture content and dry bulk density of the cover soil are
not used directly in MOCLA These parameters are used along with the porosity of the cover
soil to calculate the air-filled porosity of the cover soil which is an input parameter to MOCLA
Liner thickness Lliner (m) The thickness of the landfill liner was set to 06 m which is the
minimum thickness required by EPA Subtitle D regulation (30) The liner thickness was not
varied in the bounding calculations
Total porosity of the liner εL (dimensionless) The total porosity of the liner ranged from 03 to
05 with an average value of 04 A total porosity between 03 and 05 is common for a wide
range of soil types
S15
Gravimetric moisture content of the liner (MCL) Based on published data (31) the gravimetric
moisture content of the liner ranged from 103 to 308 with an average value of 200
Dry bulk density of the liner materials ρb L (g cm-3) Based on published data (31) the dry bulk
density of the liner ranged from 13 to 20 g cm-3 with an average value of 17 g cm-3 It should
be noted that the gravimetric moisture content and dry bulk density of the liner are not used
directly in MOCLA These parameters are used along with the porosity of the liner to calculate
the air-filled porosity of the liner which is an input parameter to MOCLA
S16
Table S1 List of Studied CWAs and TICs Military
Designation Common Name Chemical Formula CAS number Use
Carbon disulfide CS2 75-15-0 Toxic Industrial Chemical
Furan C4H4O 110-00-9 Toxic Industrial Chemical
HHD Mustard Gas C4H8Cl2S 505-60-2 Blister AgentVesicant
a Data compiled from the following sources (10 32-39) b Estimated with EPISuite v312 (40) c Hydrolysis rate estimated to be on the order of 10 min-1 at 20degC (41) d Hydrolysis half-life for ED estimated to be equal to that of L based on structural similarity e Half-life calculated based on 5 disappearance after 6 d (2) f Value estimated by averaging hydrolysis half-lives of GA GB and GD g Hydrolysis half-life estimated to be equal to that of VX based on structural similarity h Temperature not reported i Estimated using Wilke-Lee equation (42) j Estimated using Hayduk-Laudie equation (42) k pKa for CX estimated from a range of calculated pKa values for chloro-substituted oximes (43) l Estimated using Chem-Silico software package (44) m pKa for VG and VM estimated to be equivalent to that of VX MW is molecular weight bp is boiling point fp is freezing point KH is the Henryrsquos Law constant Kow is the octanol-water partition coefficient
S18Table S3 Henryrsquos law constant ranges for organic compounds originally modeled in MOCLA
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S10
Box S3 (continued) Incorporation of liner diffusion term into MOCLA
Including the diffusive flux term into the original MOCLA mass balance equation gives
( )diffwgdaT SSSSS
dtVCd
++++minus= λ)( (S22)
rearranging this expression gives
⎟⎟⎠
⎞⎜⎜⎝
⎛+++minus=
VQ
KHKNq
dtdC linerD
H
w
Ha
T λε (S23)
if qrsquo
D liner = QD liner V then a new expression for k can be written
linerD
H
w
Ha q
KHKNqk +++=
λε (S24)
Integrating each term on the right-hand side of eqn S22 gives the expressions for the fate routes The new expression for fate via liner diffusion is written as
))exp(1( t
RkqF
alinerDdiff minusminus= (S23)
S11
Methodology used to determine MOCLA input parameter values (physical parameters)
To evaluate the distribution and fate of chemicals in a landfill data for a number of input
parameters describing the landfill design and operation are required This section describes each
parameter and provides an explanation of how parameter values that could be applicable under
various disposal scenarios were determined
Dry bulk density of the waste ρb (T m-3) It is assumed that the building debris will be contained
for transport and burial and therefore will not be compacted after placement in the landfill
Therefore the wet bulk density of the building debris will likely be lower than the average value
of wet bulk density for compacted waste which is about 076 T m-3 The range of wet bulk
densities to be used in the bounding calculations was 042 to 070 T m-3 with an average value of
055 T m-3
The dry bulk density was determined from the wet bulk density and an estimate of the
gravimetric moisture content of the waste If the gravimetric moisture content (MC) of the waste
is assumed to be 10-20 (wet weight basis) then the dry bulk density can be calculated as
follows
Using a design basis of 1 m3 of refuse the total mass of waste is equal to 042 T which
corresponds to the low end of the range The mass of water in 1 m3 of refuse is equal to 042
times 020 (highest possible value of MC) or 0084 T The total mass of waste minus the mass of
water (042 - 0084) results in the mass of dry refuse which is 034 T Therefore the low value
of the range for dry bulk density is 034 T m-3 Similarly the high end of the range is 063 T m-3
The average value is 049 T m-3
Volumetric moisture content of the waste εw (m3 water m-3 LF) The possible values of
volumetric moisture content of the waste can be calculated from the ranges of the wet bulk
S12
density and the gravimetric moisture content assuming 1 m3 of waste The lowest value in the
range of volumetric moisture contents is calculated at 10 gravimetric moisture The mass of
water in 1 m3 of waste is 042 T (total mass) times 010 (mass of watertotal mass) which is 0042
T The density of water is 1 T m-3 so the volumetric moisture content is equal to 0042 m3 water
m-3 LF Similarly the highest value in the range is 014 m3 water m-3 LF which is equivalent to
070 T times 020 The average volumetric moisture content is 0091 m3 water m-3 LF
Volumetric gas content of the waste εa (m3 airm3 LF) A range of 010 to 040 was assumed for
the volumetric gas content of the waste There is very little data on measured values of the
effective porosity of waste Bendz et al (25) reported a measured value of 012 for a waste
sample from an operating MSW landfill Based on the range specified above the average value
for the volumetric gas content of the waste is 025
Fraction of organic carbon foc A range of 040 to 060 was used for the fraction of organic
carbon in the waste A value of 050 was reported for a sample of MSW (26) which will be used
as the average value in the bounding calculations
Height of the waste in the landfill H (m) The height of waste in the landfill is assumed to vary
between 183 and 61 m Based on this range the average height of waste in the landfill was 397
m
The final two terms required to describe the landfill infiltration and the gas production rate
are a function of the climate in which the landfill is located As a result two sets of values for
these parameters were used to represent an arid or a wet climate
Net precipitation N (myear) The net precipitation or infiltration was calculated based on data
reported in Camobreco et al (27) For the arid climate scenario data from sites with less than
05 m yr-1 of total precipitation were used while the data from sites with greater than or equal to
S13
05 m yr-1 were used for the wet climate scenario For each site the total precipitation was
multiplied by the percentage of precipitation that becomes leachate to determine the net
precipitation or infiltration Using this method infiltration for the arid climate was found to
range from 002 to 005 m yr-1 with an average value of 004 m yr-1 Infiltration for the wet
climate ranged from 004 to 032 m yr-1 with an average of 012 m yr-1 Although the data used
to generate these estimates encompassed a variety of different percentages of final cover it
should be noted that modeling a dry (fully capped) landfill is potentially a more realistic scenario
than a wet landfill since the building debris will likely be encapsulated and the greatest
likelihood for leakage from the containers will occur after the final cover has been placed when
infiltration is minimal
Gas production rate qa (m3 LFG m-3 LF yr-1) The landfill gas (LFG) production rate can be
described by the following equation (28)
qa=2WLoke-kt (S24)
where W is the mass of refuse Lo is a term representing the ultimate volume of methane gas
produced per unit of wet waste and k is a rate constant (yr-1) Equation S24 assumes a methane
concentration of 50 in LFG
The mass of refuse (W) is a function of the bulk density of the waste which as stated above
was assumed to vary from 042 to 070 T m-3 with an average value of 055 T m-3 Assuming 1
m3 of waste W will be equal to 055 T Lo was assumed to vary between 85 and 170 L methane
kg-1 wet waste The value of 170 L methane kg-1 wet waste is the default used in the New
Source Performance Standards of the Clean Air Act amendments (29) For the arid climate
scenario the rate constant (k) was set to 002 yr-1 For the wet climate scenario the rate constant
(k) was set to 005 yr-1 For the arid scenario qa was found to range from 19 to 37 m3 LFG m-3
S14
LF yr-1 with an average value of 28 m3 LFG m-3 LF yr-1 For the wet scenario qa was found to
range from 45 to 90 m3 LFG m-3 LF yr-1 with an average value of 675 m3 LFG m-3 LF yr-1
Thickness of cover L (m) The thickness of the landfill cover was set to 045 m which is the
minimum thickness specified by Subtitle D regulation for the thickness of the barrier layer (30)
This value was not varied in the bounding calculations
Total porosity of the soil cover εsc (dimensionless) The total porosity of the soil cover ranged
from 03 to 05 with an average value of 04 A total porosity between 03 and 05 is common for
a wide range of soil types
Gravimetric moisture content of soil cover (MCSC) The gravimetric moisture content of the soil
cover ranged from 103 to 308 (dry weight basis) with an average value of 200 based
published data (31)
Dry bulk density of the cover soil ρbSC (g cm-3) The dry bulk density of the soil cover ranged
from 13 to 20 g cm-3 with an average value of 17 g cm-3 based on published data (31) It
should be noted that the gravimetric moisture content and dry bulk density of the cover soil are
not used directly in MOCLA These parameters are used along with the porosity of the cover
soil to calculate the air-filled porosity of the cover soil which is an input parameter to MOCLA
Liner thickness Lliner (m) The thickness of the landfill liner was set to 06 m which is the
minimum thickness required by EPA Subtitle D regulation (30) The liner thickness was not
varied in the bounding calculations
Total porosity of the liner εL (dimensionless) The total porosity of the liner ranged from 03 to
05 with an average value of 04 A total porosity between 03 and 05 is common for a wide
range of soil types
S15
Gravimetric moisture content of the liner (MCL) Based on published data (31) the gravimetric
moisture content of the liner ranged from 103 to 308 with an average value of 200
Dry bulk density of the liner materials ρb L (g cm-3) Based on published data (31) the dry bulk
density of the liner ranged from 13 to 20 g cm-3 with an average value of 17 g cm-3 It should
be noted that the gravimetric moisture content and dry bulk density of the liner are not used
directly in MOCLA These parameters are used along with the porosity of the liner to calculate
the air-filled porosity of the liner which is an input parameter to MOCLA
S16
Table S1 List of Studied CWAs and TICs Military
Designation Common Name Chemical Formula CAS number Use
Carbon disulfide CS2 75-15-0 Toxic Industrial Chemical
Furan C4H4O 110-00-9 Toxic Industrial Chemical
HHD Mustard Gas C4H8Cl2S 505-60-2 Blister AgentVesicant
a Data compiled from the following sources (10 32-39) b Estimated with EPISuite v312 (40) c Hydrolysis rate estimated to be on the order of 10 min-1 at 20degC (41) d Hydrolysis half-life for ED estimated to be equal to that of L based on structural similarity e Half-life calculated based on 5 disappearance after 6 d (2) f Value estimated by averaging hydrolysis half-lives of GA GB and GD g Hydrolysis half-life estimated to be equal to that of VX based on structural similarity h Temperature not reported i Estimated using Wilke-Lee equation (42) j Estimated using Hayduk-Laudie equation (42) k pKa for CX estimated from a range of calculated pKa values for chloro-substituted oximes (43) l Estimated using Chem-Silico software package (44) m pKa for VG and VM estimated to be equivalent to that of VX MW is molecular weight bp is boiling point fp is freezing point KH is the Henryrsquos Law constant Kow is the octanol-water partition coefficient
S18Table S3 Henryrsquos law constant ranges for organic compounds originally modeled in MOCLA
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S11
Methodology used to determine MOCLA input parameter values (physical parameters)
To evaluate the distribution and fate of chemicals in a landfill data for a number of input
parameters describing the landfill design and operation are required This section describes each
parameter and provides an explanation of how parameter values that could be applicable under
various disposal scenarios were determined
Dry bulk density of the waste ρb (T m-3) It is assumed that the building debris will be contained
for transport and burial and therefore will not be compacted after placement in the landfill
Therefore the wet bulk density of the building debris will likely be lower than the average value
of wet bulk density for compacted waste which is about 076 T m-3 The range of wet bulk
densities to be used in the bounding calculations was 042 to 070 T m-3 with an average value of
055 T m-3
The dry bulk density was determined from the wet bulk density and an estimate of the
gravimetric moisture content of the waste If the gravimetric moisture content (MC) of the waste
is assumed to be 10-20 (wet weight basis) then the dry bulk density can be calculated as
follows
Using a design basis of 1 m3 of refuse the total mass of waste is equal to 042 T which
corresponds to the low end of the range The mass of water in 1 m3 of refuse is equal to 042
times 020 (highest possible value of MC) or 0084 T The total mass of waste minus the mass of
water (042 - 0084) results in the mass of dry refuse which is 034 T Therefore the low value
of the range for dry bulk density is 034 T m-3 Similarly the high end of the range is 063 T m-3
The average value is 049 T m-3
Volumetric moisture content of the waste εw (m3 water m-3 LF) The possible values of
volumetric moisture content of the waste can be calculated from the ranges of the wet bulk
S12
density and the gravimetric moisture content assuming 1 m3 of waste The lowest value in the
range of volumetric moisture contents is calculated at 10 gravimetric moisture The mass of
water in 1 m3 of waste is 042 T (total mass) times 010 (mass of watertotal mass) which is 0042
T The density of water is 1 T m-3 so the volumetric moisture content is equal to 0042 m3 water
m-3 LF Similarly the highest value in the range is 014 m3 water m-3 LF which is equivalent to
070 T times 020 The average volumetric moisture content is 0091 m3 water m-3 LF
Volumetric gas content of the waste εa (m3 airm3 LF) A range of 010 to 040 was assumed for
the volumetric gas content of the waste There is very little data on measured values of the
effective porosity of waste Bendz et al (25) reported a measured value of 012 for a waste
sample from an operating MSW landfill Based on the range specified above the average value
for the volumetric gas content of the waste is 025
Fraction of organic carbon foc A range of 040 to 060 was used for the fraction of organic
carbon in the waste A value of 050 was reported for a sample of MSW (26) which will be used
as the average value in the bounding calculations
Height of the waste in the landfill H (m) The height of waste in the landfill is assumed to vary
between 183 and 61 m Based on this range the average height of waste in the landfill was 397
m
The final two terms required to describe the landfill infiltration and the gas production rate
are a function of the climate in which the landfill is located As a result two sets of values for
these parameters were used to represent an arid or a wet climate
Net precipitation N (myear) The net precipitation or infiltration was calculated based on data
reported in Camobreco et al (27) For the arid climate scenario data from sites with less than
05 m yr-1 of total precipitation were used while the data from sites with greater than or equal to
S13
05 m yr-1 were used for the wet climate scenario For each site the total precipitation was
multiplied by the percentage of precipitation that becomes leachate to determine the net
precipitation or infiltration Using this method infiltration for the arid climate was found to
range from 002 to 005 m yr-1 with an average value of 004 m yr-1 Infiltration for the wet
climate ranged from 004 to 032 m yr-1 with an average of 012 m yr-1 Although the data used
to generate these estimates encompassed a variety of different percentages of final cover it
should be noted that modeling a dry (fully capped) landfill is potentially a more realistic scenario
than a wet landfill since the building debris will likely be encapsulated and the greatest
likelihood for leakage from the containers will occur after the final cover has been placed when
infiltration is minimal
Gas production rate qa (m3 LFG m-3 LF yr-1) The landfill gas (LFG) production rate can be
described by the following equation (28)
qa=2WLoke-kt (S24)
where W is the mass of refuse Lo is a term representing the ultimate volume of methane gas
produced per unit of wet waste and k is a rate constant (yr-1) Equation S24 assumes a methane
concentration of 50 in LFG
The mass of refuse (W) is a function of the bulk density of the waste which as stated above
was assumed to vary from 042 to 070 T m-3 with an average value of 055 T m-3 Assuming 1
m3 of waste W will be equal to 055 T Lo was assumed to vary between 85 and 170 L methane
kg-1 wet waste The value of 170 L methane kg-1 wet waste is the default used in the New
Source Performance Standards of the Clean Air Act amendments (29) For the arid climate
scenario the rate constant (k) was set to 002 yr-1 For the wet climate scenario the rate constant
(k) was set to 005 yr-1 For the arid scenario qa was found to range from 19 to 37 m3 LFG m-3
S14
LF yr-1 with an average value of 28 m3 LFG m-3 LF yr-1 For the wet scenario qa was found to
range from 45 to 90 m3 LFG m-3 LF yr-1 with an average value of 675 m3 LFG m-3 LF yr-1
Thickness of cover L (m) The thickness of the landfill cover was set to 045 m which is the
minimum thickness specified by Subtitle D regulation for the thickness of the barrier layer (30)
This value was not varied in the bounding calculations
Total porosity of the soil cover εsc (dimensionless) The total porosity of the soil cover ranged
from 03 to 05 with an average value of 04 A total porosity between 03 and 05 is common for
a wide range of soil types
Gravimetric moisture content of soil cover (MCSC) The gravimetric moisture content of the soil
cover ranged from 103 to 308 (dry weight basis) with an average value of 200 based
published data (31)
Dry bulk density of the cover soil ρbSC (g cm-3) The dry bulk density of the soil cover ranged
from 13 to 20 g cm-3 with an average value of 17 g cm-3 based on published data (31) It
should be noted that the gravimetric moisture content and dry bulk density of the cover soil are
not used directly in MOCLA These parameters are used along with the porosity of the cover
soil to calculate the air-filled porosity of the cover soil which is an input parameter to MOCLA
Liner thickness Lliner (m) The thickness of the landfill liner was set to 06 m which is the
minimum thickness required by EPA Subtitle D regulation (30) The liner thickness was not
varied in the bounding calculations
Total porosity of the liner εL (dimensionless) The total porosity of the liner ranged from 03 to
05 with an average value of 04 A total porosity between 03 and 05 is common for a wide
range of soil types
S15
Gravimetric moisture content of the liner (MCL) Based on published data (31) the gravimetric
moisture content of the liner ranged from 103 to 308 with an average value of 200
Dry bulk density of the liner materials ρb L (g cm-3) Based on published data (31) the dry bulk
density of the liner ranged from 13 to 20 g cm-3 with an average value of 17 g cm-3 It should
be noted that the gravimetric moisture content and dry bulk density of the liner are not used
directly in MOCLA These parameters are used along with the porosity of the liner to calculate
the air-filled porosity of the liner which is an input parameter to MOCLA
S16
Table S1 List of Studied CWAs and TICs Military
Designation Common Name Chemical Formula CAS number Use
Carbon disulfide CS2 75-15-0 Toxic Industrial Chemical
Furan C4H4O 110-00-9 Toxic Industrial Chemical
HHD Mustard Gas C4H8Cl2S 505-60-2 Blister AgentVesicant
a Data compiled from the following sources (10 32-39) b Estimated with EPISuite v312 (40) c Hydrolysis rate estimated to be on the order of 10 min-1 at 20degC (41) d Hydrolysis half-life for ED estimated to be equal to that of L based on structural similarity e Half-life calculated based on 5 disappearance after 6 d (2) f Value estimated by averaging hydrolysis half-lives of GA GB and GD g Hydrolysis half-life estimated to be equal to that of VX based on structural similarity h Temperature not reported i Estimated using Wilke-Lee equation (42) j Estimated using Hayduk-Laudie equation (42) k pKa for CX estimated from a range of calculated pKa values for chloro-substituted oximes (43) l Estimated using Chem-Silico software package (44) m pKa for VG and VM estimated to be equivalent to that of VX MW is molecular weight bp is boiling point fp is freezing point KH is the Henryrsquos Law constant Kow is the octanol-water partition coefficient
S18Table S3 Henryrsquos law constant ranges for organic compounds originally modeled in MOCLA
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S12
density and the gravimetric moisture content assuming 1 m3 of waste The lowest value in the
range of volumetric moisture contents is calculated at 10 gravimetric moisture The mass of
water in 1 m3 of waste is 042 T (total mass) times 010 (mass of watertotal mass) which is 0042
T The density of water is 1 T m-3 so the volumetric moisture content is equal to 0042 m3 water
m-3 LF Similarly the highest value in the range is 014 m3 water m-3 LF which is equivalent to
070 T times 020 The average volumetric moisture content is 0091 m3 water m-3 LF
Volumetric gas content of the waste εa (m3 airm3 LF) A range of 010 to 040 was assumed for
the volumetric gas content of the waste There is very little data on measured values of the
effective porosity of waste Bendz et al (25) reported a measured value of 012 for a waste
sample from an operating MSW landfill Based on the range specified above the average value
for the volumetric gas content of the waste is 025
Fraction of organic carbon foc A range of 040 to 060 was used for the fraction of organic
carbon in the waste A value of 050 was reported for a sample of MSW (26) which will be used
as the average value in the bounding calculations
Height of the waste in the landfill H (m) The height of waste in the landfill is assumed to vary
between 183 and 61 m Based on this range the average height of waste in the landfill was 397
m
The final two terms required to describe the landfill infiltration and the gas production rate
are a function of the climate in which the landfill is located As a result two sets of values for
these parameters were used to represent an arid or a wet climate
Net precipitation N (myear) The net precipitation or infiltration was calculated based on data
reported in Camobreco et al (27) For the arid climate scenario data from sites with less than
05 m yr-1 of total precipitation were used while the data from sites with greater than or equal to
S13
05 m yr-1 were used for the wet climate scenario For each site the total precipitation was
multiplied by the percentage of precipitation that becomes leachate to determine the net
precipitation or infiltration Using this method infiltration for the arid climate was found to
range from 002 to 005 m yr-1 with an average value of 004 m yr-1 Infiltration for the wet
climate ranged from 004 to 032 m yr-1 with an average of 012 m yr-1 Although the data used
to generate these estimates encompassed a variety of different percentages of final cover it
should be noted that modeling a dry (fully capped) landfill is potentially a more realistic scenario
than a wet landfill since the building debris will likely be encapsulated and the greatest
likelihood for leakage from the containers will occur after the final cover has been placed when
infiltration is minimal
Gas production rate qa (m3 LFG m-3 LF yr-1) The landfill gas (LFG) production rate can be
described by the following equation (28)
qa=2WLoke-kt (S24)
where W is the mass of refuse Lo is a term representing the ultimate volume of methane gas
produced per unit of wet waste and k is a rate constant (yr-1) Equation S24 assumes a methane
concentration of 50 in LFG
The mass of refuse (W) is a function of the bulk density of the waste which as stated above
was assumed to vary from 042 to 070 T m-3 with an average value of 055 T m-3 Assuming 1
m3 of waste W will be equal to 055 T Lo was assumed to vary between 85 and 170 L methane
kg-1 wet waste The value of 170 L methane kg-1 wet waste is the default used in the New
Source Performance Standards of the Clean Air Act amendments (29) For the arid climate
scenario the rate constant (k) was set to 002 yr-1 For the wet climate scenario the rate constant
(k) was set to 005 yr-1 For the arid scenario qa was found to range from 19 to 37 m3 LFG m-3
S14
LF yr-1 with an average value of 28 m3 LFG m-3 LF yr-1 For the wet scenario qa was found to
range from 45 to 90 m3 LFG m-3 LF yr-1 with an average value of 675 m3 LFG m-3 LF yr-1
Thickness of cover L (m) The thickness of the landfill cover was set to 045 m which is the
minimum thickness specified by Subtitle D regulation for the thickness of the barrier layer (30)
This value was not varied in the bounding calculations
Total porosity of the soil cover εsc (dimensionless) The total porosity of the soil cover ranged
from 03 to 05 with an average value of 04 A total porosity between 03 and 05 is common for
a wide range of soil types
Gravimetric moisture content of soil cover (MCSC) The gravimetric moisture content of the soil
cover ranged from 103 to 308 (dry weight basis) with an average value of 200 based
published data (31)
Dry bulk density of the cover soil ρbSC (g cm-3) The dry bulk density of the soil cover ranged
from 13 to 20 g cm-3 with an average value of 17 g cm-3 based on published data (31) It
should be noted that the gravimetric moisture content and dry bulk density of the cover soil are
not used directly in MOCLA These parameters are used along with the porosity of the cover
soil to calculate the air-filled porosity of the cover soil which is an input parameter to MOCLA
Liner thickness Lliner (m) The thickness of the landfill liner was set to 06 m which is the
minimum thickness required by EPA Subtitle D regulation (30) The liner thickness was not
varied in the bounding calculations
Total porosity of the liner εL (dimensionless) The total porosity of the liner ranged from 03 to
05 with an average value of 04 A total porosity between 03 and 05 is common for a wide
range of soil types
S15
Gravimetric moisture content of the liner (MCL) Based on published data (31) the gravimetric
moisture content of the liner ranged from 103 to 308 with an average value of 200
Dry bulk density of the liner materials ρb L (g cm-3) Based on published data (31) the dry bulk
density of the liner ranged from 13 to 20 g cm-3 with an average value of 17 g cm-3 It should
be noted that the gravimetric moisture content and dry bulk density of the liner are not used
directly in MOCLA These parameters are used along with the porosity of the liner to calculate
the air-filled porosity of the liner which is an input parameter to MOCLA
S16
Table S1 List of Studied CWAs and TICs Military
Designation Common Name Chemical Formula CAS number Use
Carbon disulfide CS2 75-15-0 Toxic Industrial Chemical
Furan C4H4O 110-00-9 Toxic Industrial Chemical
HHD Mustard Gas C4H8Cl2S 505-60-2 Blister AgentVesicant
a Data compiled from the following sources (10 32-39) b Estimated with EPISuite v312 (40) c Hydrolysis rate estimated to be on the order of 10 min-1 at 20degC (41) d Hydrolysis half-life for ED estimated to be equal to that of L based on structural similarity e Half-life calculated based on 5 disappearance after 6 d (2) f Value estimated by averaging hydrolysis half-lives of GA GB and GD g Hydrolysis half-life estimated to be equal to that of VX based on structural similarity h Temperature not reported i Estimated using Wilke-Lee equation (42) j Estimated using Hayduk-Laudie equation (42) k pKa for CX estimated from a range of calculated pKa values for chloro-substituted oximes (43) l Estimated using Chem-Silico software package (44) m pKa for VG and VM estimated to be equivalent to that of VX MW is molecular weight bp is boiling point fp is freezing point KH is the Henryrsquos Law constant Kow is the octanol-water partition coefficient
S18Table S3 Henryrsquos law constant ranges for organic compounds originally modeled in MOCLA
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S13
05 m yr-1 were used for the wet climate scenario For each site the total precipitation was
multiplied by the percentage of precipitation that becomes leachate to determine the net
precipitation or infiltration Using this method infiltration for the arid climate was found to
range from 002 to 005 m yr-1 with an average value of 004 m yr-1 Infiltration for the wet
climate ranged from 004 to 032 m yr-1 with an average of 012 m yr-1 Although the data used
to generate these estimates encompassed a variety of different percentages of final cover it
should be noted that modeling a dry (fully capped) landfill is potentially a more realistic scenario
than a wet landfill since the building debris will likely be encapsulated and the greatest
likelihood for leakage from the containers will occur after the final cover has been placed when
infiltration is minimal
Gas production rate qa (m3 LFG m-3 LF yr-1) The landfill gas (LFG) production rate can be
described by the following equation (28)
qa=2WLoke-kt (S24)
where W is the mass of refuse Lo is a term representing the ultimate volume of methane gas
produced per unit of wet waste and k is a rate constant (yr-1) Equation S24 assumes a methane
concentration of 50 in LFG
The mass of refuse (W) is a function of the bulk density of the waste which as stated above
was assumed to vary from 042 to 070 T m-3 with an average value of 055 T m-3 Assuming 1
m3 of waste W will be equal to 055 T Lo was assumed to vary between 85 and 170 L methane
kg-1 wet waste The value of 170 L methane kg-1 wet waste is the default used in the New
Source Performance Standards of the Clean Air Act amendments (29) For the arid climate
scenario the rate constant (k) was set to 002 yr-1 For the wet climate scenario the rate constant
(k) was set to 005 yr-1 For the arid scenario qa was found to range from 19 to 37 m3 LFG m-3
S14
LF yr-1 with an average value of 28 m3 LFG m-3 LF yr-1 For the wet scenario qa was found to
range from 45 to 90 m3 LFG m-3 LF yr-1 with an average value of 675 m3 LFG m-3 LF yr-1
Thickness of cover L (m) The thickness of the landfill cover was set to 045 m which is the
minimum thickness specified by Subtitle D regulation for the thickness of the barrier layer (30)
This value was not varied in the bounding calculations
Total porosity of the soil cover εsc (dimensionless) The total porosity of the soil cover ranged
from 03 to 05 with an average value of 04 A total porosity between 03 and 05 is common for
a wide range of soil types
Gravimetric moisture content of soil cover (MCSC) The gravimetric moisture content of the soil
cover ranged from 103 to 308 (dry weight basis) with an average value of 200 based
published data (31)
Dry bulk density of the cover soil ρbSC (g cm-3) The dry bulk density of the soil cover ranged
from 13 to 20 g cm-3 with an average value of 17 g cm-3 based on published data (31) It
should be noted that the gravimetric moisture content and dry bulk density of the cover soil are
not used directly in MOCLA These parameters are used along with the porosity of the cover
soil to calculate the air-filled porosity of the cover soil which is an input parameter to MOCLA
Liner thickness Lliner (m) The thickness of the landfill liner was set to 06 m which is the
minimum thickness required by EPA Subtitle D regulation (30) The liner thickness was not
varied in the bounding calculations
Total porosity of the liner εL (dimensionless) The total porosity of the liner ranged from 03 to
05 with an average value of 04 A total porosity between 03 and 05 is common for a wide
range of soil types
S15
Gravimetric moisture content of the liner (MCL) Based on published data (31) the gravimetric
moisture content of the liner ranged from 103 to 308 with an average value of 200
Dry bulk density of the liner materials ρb L (g cm-3) Based on published data (31) the dry bulk
density of the liner ranged from 13 to 20 g cm-3 with an average value of 17 g cm-3 It should
be noted that the gravimetric moisture content and dry bulk density of the liner are not used
directly in MOCLA These parameters are used along with the porosity of the liner to calculate
the air-filled porosity of the liner which is an input parameter to MOCLA
S16
Table S1 List of Studied CWAs and TICs Military
Designation Common Name Chemical Formula CAS number Use
Carbon disulfide CS2 75-15-0 Toxic Industrial Chemical
Furan C4H4O 110-00-9 Toxic Industrial Chemical
HHD Mustard Gas C4H8Cl2S 505-60-2 Blister AgentVesicant
a Data compiled from the following sources (10 32-39) b Estimated with EPISuite v312 (40) c Hydrolysis rate estimated to be on the order of 10 min-1 at 20degC (41) d Hydrolysis half-life for ED estimated to be equal to that of L based on structural similarity e Half-life calculated based on 5 disappearance after 6 d (2) f Value estimated by averaging hydrolysis half-lives of GA GB and GD g Hydrolysis half-life estimated to be equal to that of VX based on structural similarity h Temperature not reported i Estimated using Wilke-Lee equation (42) j Estimated using Hayduk-Laudie equation (42) k pKa for CX estimated from a range of calculated pKa values for chloro-substituted oximes (43) l Estimated using Chem-Silico software package (44) m pKa for VG and VM estimated to be equivalent to that of VX MW is molecular weight bp is boiling point fp is freezing point KH is the Henryrsquos Law constant Kow is the octanol-water partition coefficient
S18Table S3 Henryrsquos law constant ranges for organic compounds originally modeled in MOCLA
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S14
LF yr-1 with an average value of 28 m3 LFG m-3 LF yr-1 For the wet scenario qa was found to
range from 45 to 90 m3 LFG m-3 LF yr-1 with an average value of 675 m3 LFG m-3 LF yr-1
Thickness of cover L (m) The thickness of the landfill cover was set to 045 m which is the
minimum thickness specified by Subtitle D regulation for the thickness of the barrier layer (30)
This value was not varied in the bounding calculations
Total porosity of the soil cover εsc (dimensionless) The total porosity of the soil cover ranged
from 03 to 05 with an average value of 04 A total porosity between 03 and 05 is common for
a wide range of soil types
Gravimetric moisture content of soil cover (MCSC) The gravimetric moisture content of the soil
cover ranged from 103 to 308 (dry weight basis) with an average value of 200 based
published data (31)
Dry bulk density of the cover soil ρbSC (g cm-3) The dry bulk density of the soil cover ranged
from 13 to 20 g cm-3 with an average value of 17 g cm-3 based on published data (31) It
should be noted that the gravimetric moisture content and dry bulk density of the cover soil are
not used directly in MOCLA These parameters are used along with the porosity of the cover
soil to calculate the air-filled porosity of the cover soil which is an input parameter to MOCLA
Liner thickness Lliner (m) The thickness of the landfill liner was set to 06 m which is the
minimum thickness required by EPA Subtitle D regulation (30) The liner thickness was not
varied in the bounding calculations
Total porosity of the liner εL (dimensionless) The total porosity of the liner ranged from 03 to
05 with an average value of 04 A total porosity between 03 and 05 is common for a wide
range of soil types
S15
Gravimetric moisture content of the liner (MCL) Based on published data (31) the gravimetric
moisture content of the liner ranged from 103 to 308 with an average value of 200
Dry bulk density of the liner materials ρb L (g cm-3) Based on published data (31) the dry bulk
density of the liner ranged from 13 to 20 g cm-3 with an average value of 17 g cm-3 It should
be noted that the gravimetric moisture content and dry bulk density of the liner are not used
directly in MOCLA These parameters are used along with the porosity of the liner to calculate
the air-filled porosity of the liner which is an input parameter to MOCLA
S16
Table S1 List of Studied CWAs and TICs Military
Designation Common Name Chemical Formula CAS number Use
Carbon disulfide CS2 75-15-0 Toxic Industrial Chemical
Furan C4H4O 110-00-9 Toxic Industrial Chemical
HHD Mustard Gas C4H8Cl2S 505-60-2 Blister AgentVesicant
a Data compiled from the following sources (10 32-39) b Estimated with EPISuite v312 (40) c Hydrolysis rate estimated to be on the order of 10 min-1 at 20degC (41) d Hydrolysis half-life for ED estimated to be equal to that of L based on structural similarity e Half-life calculated based on 5 disappearance after 6 d (2) f Value estimated by averaging hydrolysis half-lives of GA GB and GD g Hydrolysis half-life estimated to be equal to that of VX based on structural similarity h Temperature not reported i Estimated using Wilke-Lee equation (42) j Estimated using Hayduk-Laudie equation (42) k pKa for CX estimated from a range of calculated pKa values for chloro-substituted oximes (43) l Estimated using Chem-Silico software package (44) m pKa for VG and VM estimated to be equivalent to that of VX MW is molecular weight bp is boiling point fp is freezing point KH is the Henryrsquos Law constant Kow is the octanol-water partition coefficient
S18Table S3 Henryrsquos law constant ranges for organic compounds originally modeled in MOCLA
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S15
Gravimetric moisture content of the liner (MCL) Based on published data (31) the gravimetric
moisture content of the liner ranged from 103 to 308 with an average value of 200
Dry bulk density of the liner materials ρb L (g cm-3) Based on published data (31) the dry bulk
density of the liner ranged from 13 to 20 g cm-3 with an average value of 17 g cm-3 It should
be noted that the gravimetric moisture content and dry bulk density of the liner are not used
directly in MOCLA These parameters are used along with the porosity of the liner to calculate
the air-filled porosity of the liner which is an input parameter to MOCLA
S16
Table S1 List of Studied CWAs and TICs Military
Designation Common Name Chemical Formula CAS number Use
Carbon disulfide CS2 75-15-0 Toxic Industrial Chemical
Furan C4H4O 110-00-9 Toxic Industrial Chemical
HHD Mustard Gas C4H8Cl2S 505-60-2 Blister AgentVesicant
a Data compiled from the following sources (10 32-39) b Estimated with EPISuite v312 (40) c Hydrolysis rate estimated to be on the order of 10 min-1 at 20degC (41) d Hydrolysis half-life for ED estimated to be equal to that of L based on structural similarity e Half-life calculated based on 5 disappearance after 6 d (2) f Value estimated by averaging hydrolysis half-lives of GA GB and GD g Hydrolysis half-life estimated to be equal to that of VX based on structural similarity h Temperature not reported i Estimated using Wilke-Lee equation (42) j Estimated using Hayduk-Laudie equation (42) k pKa for CX estimated from a range of calculated pKa values for chloro-substituted oximes (43) l Estimated using Chem-Silico software package (44) m pKa for VG and VM estimated to be equivalent to that of VX MW is molecular weight bp is boiling point fp is freezing point KH is the Henryrsquos Law constant Kow is the octanol-water partition coefficient
S18Table S3 Henryrsquos law constant ranges for organic compounds originally modeled in MOCLA
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S16
Table S1 List of Studied CWAs and TICs Military
Designation Common Name Chemical Formula CAS number Use
Carbon disulfide CS2 75-15-0 Toxic Industrial Chemical
Furan C4H4O 110-00-9 Toxic Industrial Chemical
HHD Mustard Gas C4H8Cl2S 505-60-2 Blister AgentVesicant
a Data compiled from the following sources (10 32-39) b Estimated with EPISuite v312 (40) c Hydrolysis rate estimated to be on the order of 10 min-1 at 20degC (41) d Hydrolysis half-life for ED estimated to be equal to that of L based on structural similarity e Half-life calculated based on 5 disappearance after 6 d (2) f Value estimated by averaging hydrolysis half-lives of GA GB and GD g Hydrolysis half-life estimated to be equal to that of VX based on structural similarity h Temperature not reported i Estimated using Wilke-Lee equation (42) j Estimated using Hayduk-Laudie equation (42) k pKa for CX estimated from a range of calculated pKa values for chloro-substituted oximes (43) l Estimated using Chem-Silico software package (44) m pKa for VG and VM estimated to be equivalent to that of VX MW is molecular weight bp is boiling point fp is freezing point KH is the Henryrsquos Law constant Kow is the octanol-water partition coefficient
S18Table S3 Henryrsquos law constant ranges for organic compounds originally modeled in MOCLA
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S17 Table S2 Physical-chemical property data for additional CWAs the riot-control agent CS and carbon disulfidea
Chemical Carbon disulfide
Lewisite (L)
Ethyldichloro- arsine (ED)
Phosgene oxime (CX)
Tabun (GA) GE GF VG VM CS
Chemical Formula CS2 C2H2AsCl3 C2H5AsCl2 CHCl2NO C5H11N2O2P C5H12FO2P C7H14FO2P C10H24NO3PS C9H22NO2PS C10H5ClN2
CAS number 75-15-0 541-25-3 598-14-1 1794-86-1 77-81-6 1189-87-3 329-99-7 78-53-5 21770-86-5 2698-41-1
a Data compiled from the following sources (10 32-39) b Estimated with EPISuite v312 (40) c Hydrolysis rate estimated to be on the order of 10 min-1 at 20degC (41) d Hydrolysis half-life for ED estimated to be equal to that of L based on structural similarity e Half-life calculated based on 5 disappearance after 6 d (2) f Value estimated by averaging hydrolysis half-lives of GA GB and GD g Hydrolysis half-life estimated to be equal to that of VX based on structural similarity h Temperature not reported i Estimated using Wilke-Lee equation (42) j Estimated using Hayduk-Laudie equation (42) k pKa for CX estimated from a range of calculated pKa values for chloro-substituted oximes (43) l Estimated using Chem-Silico software package (44) m pKa for VG and VM estimated to be equivalent to that of VX MW is molecular weight bp is boiling point fp is freezing point KH is the Henryrsquos Law constant Kow is the octanol-water partition coefficient
S18Table S3 Henryrsquos law constant ranges for organic compounds originally modeled in MOCLA
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S18Table S3 Henryrsquos law constant ranges for organic compounds originally modeled in MOCLA
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S19Table S4 Log Kow ranges for organic compounds originally modeled in MOCLA
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S20
Table S5 Henryrsquos law constant ranges for CWAs and TICs Henrys law constant (dimensionless) Minimum Accepted Maximum
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S21
Table S6 Log Kow ranges for CWAs and TICs Log Kow Minimum Accepted Maximum
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S22
Table S7 Physical-chemical property data for CWA hydrolysatesa
a Data compiled from the following sources (10 35 37 45) b Estimated with EPI Suite v312 (40) c Estimated using Chem-Silico software (44) the log Kow value for EA2192 is estimated for the zwitterionic form at pH 7 d Estimated using Wilke-Lee equation (42) e Estimated using Hayduk-Laudie equation (42)
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S23
Table S8 Predicted fate routes for base-case scenario after one year with no biodegradation (λbiotic = infin)
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S24
Table S9 Predicted fate routes for base-case scenario after one year with λbiotic = 1000 days
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S25
Table S10 Predicted fate routes for base-case scenario after one year with λbiotic = 100 days
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S26
Table S11 Predicted fate routes for base-case scenario after one year with λbiotic = 10 days
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S27
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S1 Fate routes for carbon disulfide and the remaining CWAs after six months (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S2 Fate routes for carbon disulfide and the remaining CWAs after six months (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S28
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Lewisi
te
Ethyld
ichlor
oarsi
nePh
osgen
e Oxim
eGA (T
abun
)
GE GF VG VM CS
Fλ abiotic
Fadvection
Fractionremaining
Figure S3 Fate routes for carbon disulfide and the remaining CWAs after one year (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S4 Fate routes for carbon disulfide and the remaining CWAs after one year (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S29
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S5 Fate routes for the TICs and CWAs after five years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S6 Fate routes for the TICs and CWAs after five years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S30
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
000
020
040
060
080
100
Carbon
disul
fide
Furan
Distille
d Must
ard (H
D)
Nitroge
n Must
ardLe
wisite
Ethyld
ichlor
oarsi
ne
Phosg
ene O
xime
GA (Tab
un)
GB (Sari
n)GD (S
oman
)GE GF VX VG VM CS
Fλ abiotic
Fadvection
Fraction remaining
Figure S7 Fate routes for the TICs and CWAs after thirty years (arid scenario) The fraction of chemical transported via all other fate pathways was less than 1
Figure S8 Fate routes for the TICs and CWAs after thirty years (wet scenario) The fraction of chemical transported via all other fate pathways was less than 1
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S31
Literature Cited
(1) Somani S M ed Chemical Warfare Agents Academic Press Inc San Diego CA 1 1992 (2) Department of the Army Potential Military ChemicalBiological Agents and Compounds FM 3-9 NAVFAC P-467 AFR 355-7 Headquarters Department of the Army Navy and Air Force Fort McClellan AL 2005 (3) Kingery A F Allen H E The environmental fate of organophosphorus nerve agents A review Toxicol Environ Chem 1995 47 155-184 (4) Reinhart D R Gould J P Cross W H Pohland F G Sorptive behavior of selected organic pollutants codisposed in a municipal landfill In Emerging Technologies in Hazardous Waste ACS Symposium Series American Chemical Society 1990 422 292-310 (5) Ejlertsson J Johansson E Karlson A Meyerson U Svensson B H Anaerobic
degradation of xenobiotics by organisms from municipal solid waste landfilling conditions Antonie van Leeuwenhoek 1996 69 67-74
(6) Ejlertsson J Meyerson U Svensson B H Anaerobic degradation of phthalic acid esters during digestion of municipal solid waste under landfilling conditions Biodegradation 1996 7 345-352
(7) Sanin F Knappe D R U Barlaz M A Biodegradation and humification of toluene in a simulated landfill Water Res 2000 34 (12) 3063-3074 (8) Wu B Taylor C M Knappe D R U Nanny M A Barlaz M A Factors controlling alkylbenzene sorption to municipal solid waste Environ Sci Technol 2001 35 4569-4576 (9) Franke S Textbook of Military Chemistry Vol 1 USAMIIA-HT-039-82 AD B062913 Defense Technical Information Center Alexandria VA 1982 (10) Munro N B Talmage S S Griffin G D Waters L C Watson A P King J F
Hauschild V The sources fate and toxicity of chemical warfare agent degradation products Environ Health Perspect 1999 107 933-974
(11) Cohen B Chemical Warfare Agents and Related Chemical Problems Parts III-IV Summary Technical Report Division 9 NRDC Office of Science Research and Development 1946 (12) Morrill L G Reed L W Chinn K S K Toxic Chemicals in the Soil Environment Volume 2 Interactions of some toxic chemicalschemical warfare agents and soils TECOM Project 2-CO-210-049 Oklahoma State University Stillwater OK 1985 (13) Rosenblatt D H Miller T A Dacre J C Muul I Cogley D R Problem Definition Studies on Potential Environmental Pollutants II Physical Chemical Toxicological and Biological Properties of 16 Substances Tech Rpt 7509 AD A030428 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1975 (14) Clark D N Review of reactions of chemical agents in water AD-A213 287 Defense Technical Information Center Alexandria VA 1989 (15) Harvey S P Szafraniec L L Beaudry W T Earley J T Irvine R L Neutralization and biodegradation of sulfur mustard ERDEC-TR-388 US Army Munitions Chemical Command Aberdeen Proving Grounds MD 1997
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S32
(16) Epstein J Rosenblatt D Gallacio A McTeague W Summary Report on a Data Base for Predicting Consequences of Chemical Disposal Operations EASP 1200-12 Department of the Army Headquarters Edgewood Arsenal MD 1973
(17) Christensen TH Kjeldsen P Albrechtsen H-J Heron G Nielsen PH Bjerg PL Holm PE Attenuation of landfill leachate pollutants in aquifers Crit Rev Environ Sci Technol 1994 24 119-202 (18) Hilger HH Barlaz MA Anaerobic decomposition of refuse in landfills and methane
oxidation of cover soils In Manual of Environmental Microbiology 2nd ed 2001 pp 696-718
(19) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380
(20) Escher BI Schwarzenbach RP Partitioning of substituted phenols in liposome-water biomembrane-water and octanol-water systems Environ Sci Technol 1996 30 260- 270 (21) Skylar V I Mosolova T P Kucherenko I A Degtyarova N N Varfolomeyev S D Kalyuzhyi S V Anaerobic toxicity and biodegradability of hydrolysis products of chemical warfare agents Appl Biochem Biotechnol 1999 81 107-117 (22) Park J K Nibras M Mass flux of organic chemicals through polyethylene
geomembranes Water Environ Res 1993 65 227-237 (23) Millington RJ Gas diffusion in porous media Science 1959 130 100-102 (24) Johnson P C Ettinger RA Heuristic model for predicting the intrusion rate of
contaminant vapors into buildings Environ Sci Technol 1991 25 1445-1452 (25) Bendz D Singh VP Rosqvist H Bengtsson L Kinematic wave model for water movement in municipal solid waste Water Resour Res 1998 34 2963-2970 (26) Barlaz MA Carbon storage during biodegradation of municipal solid waste components in laboratory-scale landfills Global Biogeochem Cycles 1998 12 373-380 (27) Camobreco V Repa E Ham R K Barlaz M A Felker M Rousseau C Clark- Balbo M Rathle J Thorneloe S Life Cycle Inventory of a Modern Municipal Solid Waste Landfill Environmental Research and Education Foundation Washington DC 2000 (28) US Environmental Protection Agency Users Manual Landfill Gas Emissions Model (Version 20) EPA600R-98054 US EPA Research Triangle Park NC 1998 (29) US Environmental Protection Agency Standards of performance for new stationary sources and guidelines for control of existing sources municipal solid waste landfills Code of Federal Regulations Title 40 Sections 9 51 52 and 60 Fed Regist 1996 61 (30) Code of Federal Regulations 40 Parts 257 and 258 1991 (31) Benson C H Daniel DE Boutwell GP Field performance of compacted clay liners J Geotech Geoenviron Eng 1999 125 390-402 (32) Daubert T E Danner R P Physical and Thermodynamic Properties of Pure Chemicals Data Compilation Taylor and Francis Washington DC 1989 (33) Elliot S The solubility of carbon disulfide vapor in natural aqueous systems Atmos Environ 1989 23 977-1980 (34) Goldman M Dacre J C Lewisite - Its Chemistry Toxicology and Biological Effects Rev Environ Contam Toxicol 1989 110 75-115 (35) Hansch C Leo A Hoekman D Exploring QSAR Hydrophobic Electronic and Steric Constants American Chemical Society 1995
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984
S33
(36) Valvani S C Yalkowsky S H Roseman T J Solubility and partitioning 4 Aqueous solubility and octanol-water partition coefficients of liquid non-electrolytes J Pharm Sci 1981 70 502-507 (37) Yalkowsky S H He Y Handbook of Aqueous Solubility Data CRC Press 2003 (38) Yaws C L Handbook of Vapor Pressure Gulf Publishing Company Houston Texas 1994 (39) World Health Organization Epidemic and Pandemic Alert and Response (EPR) 2005 httpwwwwhointcsrdelibepidemicsbiochemguideenindexhtml (40) US Environmental Protection Agency Estimation Program Interface (EPI) Suite August 17 2004 httpwwwepagovopptintrexposuredocsepisuitehtm (41) Mitretek Systems Chemistry of Lewisite 2004
httpwwwmitretekorghomensfhomelandsecurityLewisite (42) Lyman W J Reehl W F Rosenblatt D H Handbook of Chemical Property Estimation Methods Environmental Behavior of Organic Compounds American Chemical Society Washington DC 1990 (43) Kurtz AP DSilva TDJ Estimation of dissociation constants (pKas) of oximes from
proton chemical shifts in dimethyl sulfoxide solution J Pharm Sci 1987 76 599-610 (44) Chemsilico LLC Chemsilico Product Secure Site 2003
httpssecurechemsilicocomindexphp (45) Small M J Compounds formed from the chemical decontamination of HD GB VX and their environmental fate Technical Report 8304 US Army Medical Bioengineering Research and Development Laboratory Fort Detrick MD 1984