EPA
United States
Environmental Protection
Agency
Solid Waste and
Emergency Response
(5305W)
EPA530-D-99-001C
November 1999
www.epa.gov/osw
Screening Level
Ecological Risk
Assessment Protocol
For Hazardous Waste
Combustion Facilities
Volume Three
Appendices B-H
Peer Review Draft
IWSROSSAIfNUE
Printed on paper that contains at least 30 percent postconsumer fiber
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APPENDIX B
ESTIMATING MEDIA CONCENTRATION EQUATIONS AND VARIABLE VALUES
Screening Level Ecological Risk Assessment Protocol
August 1999
-------
Screening Level Ecological Risk Assessment Protocol
Appendix B: Estimating Media Concentration Equations August 1999
APPENDIX B
TABLE OF CONTENTS
TABLE PAGE
SOIL INGESTION EQUATIONS
B-l-1 SOIL CONCENTRATION DUE TO DEPOSITION B-l
B-l-2 COPC SOIL LOSS CONSTANT DUE TO ALL PROCESSES B-10
B-l-3 COPC LOSS CONSTANT DUE TO SOIL EROSION B-14
B-l-4 COPC LOSS CONSTANT DUE TO RUNOFF B-20
B-l-5 COPC LOSS CONSTANT DUE TO LEACHING B-25
B-l-6 COPC LOSS CONSTANT DUE TO VOLATILIZATION B-31
SURFACE WATER AND SEDIMENT EQUATIONS
B-2-1 TOTAL COPC LOAD TO WATER BODY B-37
B-2-2 DEPOSITION TO WATER BODY B-41
B-2-3 DIFFUSION LOAD TO WATER BODY B-44
B-2-4 IMPERVIOUS RUNOFF LOAD TO WATER BODY B-48
B-2-5 PERVIOUS RUNOFF LOAD TO WATER BODY B-51
B-2-6 EROSION LOAD TO WATER BODY B-56
B-2-7 UNIVERSAL SOIL LOSS EQUATION (USLE) B-62
B-2-8 SEDIMENT DELIVERY RATIO B-67
B-2-9 TOTAL WATER BODY CONCENTRATION B-71
B-2-10 FRACTION IN WATER COLUMN AND BENTfflC SEDIMENT B-75
B-2-11 OVERALL TOTAL WATER BODY DISSIPATION RATE CONSTANT B-80
B-2-12 WATER COLUMN VOLATILIZATION LOSS RATE CONSTANT B-82
B-2-13 OVERALL COPC TRANSFER RATE COEFFICIENT B-86
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering B-i
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Screening Level Ecological Risk Assessment Protocol
Appendix B; Estimating Media Concentration Equations August 1999
APPENDIX B
TABLE OF CONTENTS
TABLE PAGE
B-2-14 LIQUID-PHASE TRANSFER COEFFICIENT B-90
B-2-15 GAS-PHASE TRANSFER COEFFICIENT B-95
B-2-16 BENTfflC BURIAL RATE CONSTANT B-99
B-2-17 TOTAL WATER COLUMN CONCENTRATION B-104
B-2-18 DISSOLVED PHASE WATER CONCENTRATION B-108
B-2-19 COPC CONCENTRATION IN BED SEDIMENT B-lll
TERRESTRIAL PLANT EQUATIONS
B-3-1 PLANT CONCENTRATION DUE TO DIRECT DEPOSITION B-l 15
B-3-2 PLANT CONCENTRATION DUE TO AIR-TO-PLANT TRANSFER B-125
B-3-3 PLANT CONCENTRATION DUE TO ROOT UPTAKE B-130
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering B-ii
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Screening Level Ecological Risk Assessment Protocol
Appendix B; Estimating Media Concentration Equations
August 1999
Pa
P»
e
a
A
A,
b
BD
BCFr
BS
Bs
Bv
c
C
Cd
Chv
Cs
Cyp
Cyv
Cywv
APPENDK B
LIST OF VARIABLES AND PARAMETERS
Empirical constant (unitless)
Dimensionless viscous sublayer thickness (unitless)
Viscosity of air (g/cm-s)
Viscosity of water corresponding to water temperature (g/cm-s)
Density of air (g/cm3 or g/m3)
Density of water corresponding to water temperature (g/cm3)
Temperature correction factor (unitless)
Bed sediment porosity (L volume/L sediment)—unitless
Soil volumetric water content (mL water/cm3 soil)
Empirical intercept coefficient (unitless)
Surface area of contaminated area (m2)
Impervious watershed area receiving COPC deposition (m2)
Total watershed area receiving COPC deposition (m2)
Water body surface area (m2)
Empirical slope coefficient (unitless)
Soil bulk density (g soil/cm3 soil)
Plant-soil biotransfer factor (mg COPC/kg DW plant)/(mg COPC/kg
soil)—unitless
Benthic solids concentration (g sediment/cm3 sediment)
Soil bioavailability factor (unitless)
Air-to-plant biotransfer factor (mg COPC/kg DW plant)/(mg COPC/kg
air)—unitless
Junge constant = l.TxlO"4 (arm-cm)
USLE cover management factor (unitless)
Drag coefficient (unitless)
Dissolved phase water concentration (mg COPC/L water)
Unitized hourly air concentration from vapor phase (ng-s/g-m3)
Unitized hourly air concentration from particle phase (ug-s/g-m3)
COPC concentration in soil (mg COPC/kg soil)
COPC concentration in bed sediment (mg COPC/kg sediment)
Total COPC concentration in water column (mg COPC/L water column)
Total water body COPC concentration including water column and bed sediment
(g COPC/m3 water body) or (mg/L)
Unitized yearly average air concentration from particle phase (ug-s/g-m3)
Unitized yearly average air concentration from vapor phase (ug-s/g-m3)
Unitized yearly average air concentration from vapor phase (over water body or
watershed) (ug-s/g-m3)
Diffusivity of COPC in air (cm2/s)
Depth of upper benthic sediment layer (m)
U.S. EPA Region 6
Multimedia Planning and Permitting Division
Center for Combustion Science and Engineering
U.S. EPA
Office of Solid Waste
B-iii
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Screening Level Ecological Risk Assessment Protocol
Appendix B; Estimating Media Concentration Equations
August 1999
Ds
dwc
Dw
Dydp
Dytwp
Dywp
Dywv
Dywwv
ER
Ev
/*.
Fd
Fw
Jwc
H
I
k
K
Kds
kp
ks
kse
ksg
ksl
ksr
ksv
Deposition term (mg COPC/kg soil-yr)
Depth of water column (m)
Diffusivity of COPC in water (cm2/s)
Unitized yearly average dry deposition from particle phase (s/m2-yr)
Unitized yearly average total (wet and dry) deposition from particle phase (over
water body or watershed) (s/m2-yr)
Unitized yearly average wet deposition from particle phase (s/m2-yr)
Unitized yearly average wet deposition from vapor phase (s/m2-yr)
Unitized yearly average wet deposition from vapor phase (over water body or
watershed) (s/m2-yr)
Total water body depth (m)
Soil enrichment ratio (unitless)
Average annual evapotranspiration (cm/yr)
Fraction of total water body COPC concentration in benthic sediment (unitless)
Fraction of diet that is soil (unitless)
Fraction of COPC wet deposition that adheres to plant surfaces (unitless)
Fraction of total water body COPC concentration in the water column (unitless)
Fraction of COPC air concentration in vapor phase (unitless)
Henry's Law constant (atm-m3/mol)
Average annual irrigation (cm/yr)
Von Karman's constant (unitless)
USLE erodibility factor (ton/acre)
Benthic burial rate constant (yr"1)
Bed sediment/sediment pore water partition coefficient
(cm3 water/g bottom sediment or L water/kg bottom sediment)
Soil-water partition coefficient (cm3 water/g soil)
Suspended sediment-surface water partition coefficient
(L water/kg suspended sediment)
Gas phase transfer coefficient (m/yr)
Liquid phase transfer coefficient (m/yr)
Soil organic carbon-water partition coefficient (mL water/g soil)
Octanol-water partition coefficient
(mg COPC/L octanol)/(mg COPC/L octanol)—unitless
Plant surface loss coefficient (yr !)
COPC soil loss constant due to all processes (yrn)
COPC loss constant due to soil erosion (yr"1)
COPC loss constant due to biotic and abiotic degradation (yr !)
COPC loss constant due to leaching (yrn)
COPC loss constant due to surface runoff (yr :)
COPC loss constant due to volatilization (yr"1)
Water column volatilization rate constant (yr l)
Overall COPC transfer rate coefficient (m/yr)
Overall total water body dissipation rate constant (yr *)
U.S. EPA Region 6
Multimedia Planning and Permitting Division
Center for Combustion Science and Engineering
U.S. EPA
Office of Solid Waste
B-iv
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Screening Level Ecological Risk Assessment Protocol
Appendix B; Estimating Media Concentration Equations August 1999
LDEP = Total (wet and dry) particle phase and wet vapor phase COPC direct deposition
load to water body (g/yr)
LKf = Vapor phase COPC diffusion (dry deposition) load to water body (g/yr)
LE = Soil erosion load (g/yr)
LR = Runoff load from pervious surfaces (g/yr)
LKI = Runoff load from impervious surfaces (g/yr)
LT = Total COPC load to the water body (including deposition, runoff, and erosion)
(g/yr)
LS = USLE length-slope factor (unitless)
OCsed = Fraction of organic carbon in bottom sediment (unitless)
p °L - Liquid phase vapor pressure of chemical (atm)
p °s = Solid phase vapor pressure of chemical (atm)
P = Average annual precipitation (cm/yr)
PF = USLE supporting practice factor (unitless)
Pd = Plant concentration due to direct deposition (mg COPC/kg DW)
Pr = Plant concentration due to root uptake (mg COPC/kg DW)
Pv = Plant concentration due to air-to-plant transfer (|ig COPC/g DW plant tissue or
mg COPC/kg DW plant tissue)
Q = COPC-specific emission rate (g/s)
r — Interception fraction—the fraction of material in rain intercepted by vegetation
and initially retained (unitless)
R = Universal gas constant (atm-m3/mol-K)
RO = Average annual surface runoff from pervious areas (cm/yr)
RF = USLE rainfall (or erosivity) factor (yr'1)
Rp = Interception fraction of the edible portion of plant (unitless)
SD = Sediment delivery ratio (unitless)
ASf = Entropy of fusion [ASf/R = 6.79 (unitless)]
SF = Slope factor (mg/kg-day)'1
ST = Whitby's average surface area of particulates (aerosols)
= 3.5x10"6 cnrVcm3 air for background plus local sources
= l.lxlO"5 cnrYcm3 air for urban sources
Ta = Ambient air temperature (K)
Tj = Tune period at the beginning of combustion (yr)
T2 = Length of exposure duration (yr)
tD = Time period over which deposition occurs (or time period of combustion) (yr)
Tm = Melting point of chemical (K)
Tp = Length of plant exposure to deposition per harvest of edible portion of plant (yr)
TSS = Total suspended solids concentration (mg/L)
Twk = Water body temperature (K)
t1/2 = Half-time of COPC (days)
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering B-v
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Screening Level Ecological Risk Assessment Protocol
Appendix B; Estimating Media Concentration Equations
August 1999
Current velocity (m/s)
Dry deposition velocity (cm/s)
Average volumetric flow rate through water body (mVyr)
Average annual wind speed (m/s)
Unit soil loss (kg/m2-yr)
Dry harvest yield = 1.22xlOH kg DW, calculated from the 1993 U.S. average
wet weight Yh of 1.35xlOn kg (USDA 1994b) and a conversion factor of 0.9
(Fries 1994)
Harvest yield of fth crop (kg DW)
Yield or standing crop biomass of the edible portion of the plant (productivity) (kg
DW/m2)
Vdv
Vfx
W
xe
Yh
Yht
Yp
0.01
10'6
10-6
0.31536
365
907.18
0.1
0.001
100
1000
4047
IxlO3
3.1536xl07
Soil mixing zone depth (cm)
Units conversion factor
Units conversion factor
Units conversion factor
Units conversion factor
Units conversion factor
Units conversion factor
Units conversion factor
Units conversion factor
Units conversion factor
Units conversion factor
Units conversion factor
Units conversion factor
Units conversion factor
(kg cm2/mg-m2)
(kg/mg)
(m-g-s/cm-ug-yr)
(days/yr)
(kg/ton)
(g-kg/cm2-m2)
(kg-crrrVmg-m2)
(mg-cm2/kg-cm2)
(mg/g)
(m2/acre)
(g/kg)
(s/yr)
U.S. EPA Region 6
Multimedia Planning and Permitting Division
Center for Combustion Science and Engineering
U.S. EPA
Office of Solid Waste
B-vi
-------
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Consistent with U.S. EPA (1994a; 1998), U.S. EPA OSW recommends incorporating
the Cs equation.
Uncertainties associated with this variable include the following:
(1) Five of the variables in the equation for Ds (Q, Cyv, Dywv, Dywp and Dydp) are
measured or modeled variables. The direction and magnitude of any uncertainty
Uncertainties associated with these variables will probably be different at each fi
(2) Based on the narrow recommended ranges, uncertainties associated with Vdv, F,
small.
(3) Values for Z, vary by about one order of magnitude. Uncertainty is greatly redui
are tilled or untilled.
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indicating that this assumption is unreasonable.
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the sum of all COPC removal processes.
Uncertainties associated with this variable are discussed in Table B-1-2.
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Soil Depth (cm)
Untilled 1
Tilled 20
The following uncertainty is associated with this variable:
(1) For soluble COPCs, leaching might lead to movement to below soil
This uncertainty may overestimate Cs.
(2) Deposition to hard surfaces may result in dust residues that have ne
other residues. This uncertainty may underestimate Cs.
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This variable is affected by the soil structure, such as looseness or compa
clay content of the soil (Hillel 1980), as summarized in U.S. EPA (1990a
originally cited in Hoffman and Baes (1979). U.S. EPA (1994c) recomm
a mean value for loam soil that was obtained from Carsel, Parrish, Jones,
g/cm3 also represents the midpoint of the "relatively narrow range" for &
The following uncertainty is associated with this variable:
(1) The recommended range of BD values may not accurately represeni
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ST lili
0 to 1 (see Appendix A-2)
variable is COPC-specific and should be determined from the COPC tables in Appendix A-
:nted in U.S. EPA (1993), RTI (1992), and NC DEHNR (1997) based on the work of Bidler
EPA(1994c).
Following uncertainty is associated with this variable:
It is based on the assumption of a default ST value for background plus local sources, rathe
urban sources. If a specific site is located in an urban area, the use of the latter ST value mi
Specifically, the ST value for urban sources is about one order of magnitude greater than th
local sources, and it would result in a lower calculated Fv value; however, the Fv value is li
percent lower.
According to Bidleman (1988), the equation used to calculate Fv assumes that the variable
constant for all chemicals. However, the value of c depends on the chemical (sorbate) mol
surface concentration for monolayer coverage, and the difference between the heat of deso:
the particle surface and the heat of vaporization of the liquid-phase sorbate. To the extent i
COPC-specific conditions may cause the value of c to vary, uncertainty is introduced if a c
of c is used to calculate Fv.
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TABLE B-1-1
SOIL CONCENTRATION DUE TO DEPOSITION
(SOIL EQUATIONS)
ral Soils." Journal of Contaminant Hydrology. Vol. :
3
3
(Page 8 of 9)
sel, R.F., R.S. Parrish, R.L. Jones, J.L. Hansen, and R.L. Lamb. 1988. "Characterizing the Uncertainty of Pesticide Leaching in Agrk
Pages 11-24.
£3
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This reference is cited by U.S. EPA (1994b) as the source for a mean soil bulk density value of 1.5 g/cm3 for loam soil.
lei, D. 1980. Fundamentals of Soil Physics. Academic Press, Inc. New York.
*^*
a
seness or compaction of the soil, depending on the
o
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This document is cited by U.S. EPA (1990a) for the statement that dry soil bulk density, BD, is affected by the soil structure, such as
water and clay content of the soil.
Radionuclides. ORNL/NOREG/TM-882.
^
. EPA. 1 990a. Interim Final Methodology for Assessing Health Risks Associated with Indirect Exposure to Combustor Emissions. Er
Research and Development. EPA 600-90-003. January.
1/1
3
:curs (time period for combustion ), tD, be
8 .
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This document is a reference source for the equation in Table B-1-1, and it recommends that (1) the time period over which depositk
represented by periods of 30, 60, and 100 years, and (2) undocumented values for soil mixing zone depth, Z,, for tilled and untilled si
•king Group Recommendations. Office of Solid
1
. EPA. 1 993. Addendum to the Methodology for Assessing Health Risks Associated with Indirect Exposure to Combustor Emissions .
Waste. Office of Research and Development. Washington, D.C. September 24.
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fraction of COPC air concentration in vapor phase) ii
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This document is a reference for the equation in Table B-1-1. It recommends using a deposition term, Ds, and COPC-specific F, val
the Cs equation.
Attachment C, Draft Exposure Assessment Guidanc
I .
. EPA 1994a. Revised Draft Guidance for Performing Screening Level Risk Analyses at Combustion Facilities Burning Hazardous Wa
for RCRA Hazardous Waste Combustion Facilities. Office of Emergency and Remedial Response. Office of Solid Waste. April 15,
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z,
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Waste. December 14.
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asition velocity for HNO3 from a U.S. EPA database
alue should be applicable to any organic compound h
following:
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alue for dry deposition velocity is based on median dry de
lered the most similar to the constituents covered and the
mendation was not cited. This document recommends thi
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REFERENCES AND DISCUSS!
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Protocol for Performing Indirect Expo,
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. Office of Solid Wasi
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Guidance for Performing Screening Le
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CRA Hazard
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is one of the
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(1) All of the equation variables are site-specific. Use of default values rather than site-specific vi
these variables will result in unit soil loss (X,) estimates that are under- or overestimated to so:
default values, Xe estimates can vary over a range of less than two orders of magnitude.
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Uncertainties associated with this variable include the following:
(1) The recommended default values for the empirical intercept coefficient, a, are average values
of sediment yields from various watersheds. Therefore, those default values may not accurate
watershed conditions. As a result, use of these default values may under- or overestimate SD.
(2) The recommended default value for the empirical slope coefficient, b, is based on a review of
various watersheds. This single default value may not accurately represent site-specific water
result, use of this default value may under- or overestimate SD.
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ent of the soil (Hillel 1980), as summarized in U.S. El
Baes (1979). U.S. EPA (1994) recommends a default
taken from Carsel, Parrish, Jones, Hansen, and Lamb
itively narrow range" for BD of 1.2 to 1.7 g/cm3 (U.S.
following uncertainty is associated with this variable:
The recommended range of soil dry bulk density val
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EPA OSW recommends the following values for this
Soil Depth (cm)
Untilled 1
Tilled 20
following uncertainty is associated with this variable:
For soluble COPCs, leaching might lead to mov<
This uncertainty may overestimate kse.
Deposition to hard surfaces may result in dust re
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TABLE B-1-3
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ONSTANT DUE T
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TABLE B-1-3
Z
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N*N
8
COPC LOSS CONSTANT DUE TO SOIL EK
(SOIL EQUATIONS)
©
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REFERENCES AND DISCUSSION
g in Agricultural Soils." Journal of Contaminant Hydrology. Vol
c
., R.S. Parish, R.L. Jones, J.L. Hansen, and R.L. Lamb. 1988. "Characterizing the Uncertainty of Pesticide Lez
ages 11-24.
u_ a.
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I
document is cited by U.S. EPA (1994) as the source for a mean soil bulk density, BD, value of 1.5 g/cm3 for lot
_«
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1980. Fundamentals of Soil Physics. Academic Press, Inc. New York.
Q
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document is cited by U.S. EPA (1990) for the statement that dry soil bulk density, BD, is affected by the soil st:
r and clay content of the soil.
«
-------
TABLE B-1-3
OIL EROSION
)SS CONSTANT DUE TO S
(SOIL EQUATIONS)
^
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Attachment C, Draft Exposure Assessment Guidance J
ng Hazardous Wastes.
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This variable depends on the available water and on soil structure; i
be estimated as the midpoint between a soil's field capacity and wil
of 0.2 mL/cm3 as a default value. This value is the midpoint of the
which is recommended by U.S. EPA (1993) (no source or reference
EPA(1994b).
The following uncertainty is associated with this variable:
(1) The default &„, values may not accurately reflect site-specific
overestimated to a small extent, based on the limited range of
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Soil Depth (cm)
Untilled 1
Tilled 20
The following uncertainty is associated with this variable:
(1) For soluble COPCs, leaching might lead to movement to belo\
uncertainty may overestimate ksr.
(2) Deposition to hard surfaces may result in dust residues that ha
in-situ materials), in comparison to that of other residues. Thi
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The following uncertainty is associated with this variable:
(1) Uncertainties associated with this parameter will be limited if
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TABLE B-1-4
COPC LOSS CONSTANT DUE TO RUNOFF
(SOIL EQUATIONS)
(Page 4 of 5)
REFERENCES AND DISCUSSION
Itural Soils." Journalof Contaminant Hydrology. Vol
3
U
'&
.F., R.S. Parrish, R.L. Jones, J.L. Hansen, and R.L. Lamb. 1988. "Characterizing the Uncertainty of Pesticide Leaching in Ai
'ages 11 -24.
a- &.
I"05
55
U
document is cited by U.S. EPA (1994) as the source of a mean soil bulk density, BD, value of 1.5 g/cm3 for loam soil.
t/;
1
i
><
1
|
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1
J.J., D.W. Miller, F. Van der Leeden, and F.L. Troise. 1973. Water Atlas of the United States. Water Information Center,
>,
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off, R. This reference provides maps with isolines of
^ interflow, and ground water recharge. Because these
te surface runoff.
C > TO
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document is cited by U.S. EPA (1993), U.S. EPA (1994c), and NC DEHNR (1997) as a reference to calculate average annus
lal average surface water runoff, which is defined as all flow contributions to surface water bodies, including direct runoff, sh
ss are total contributions, and not only surface runoff, U.S. EPA (1994c) recommends that they be reduced by 50 percent to e
•1 3 2
£ i 5
1980. Fundamentals of Soil Physics. Academic Press, Inc. New York.
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oseness or compaction of the soil, depending on the
Cfl
CS
document is cited by U.S. EPA (1990) for the statement that dry soil bulk density, BD, is affected by the soil structure, such
r and clay content of the soil.
« o
£ 1
e ofRadionuclides. ORNL/NUREG/TM-882.
1
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P.O., and C.F. Baes. 1979. A Statistical Analysis of Selected Parameters for Predicting Food Chain Transport and Interna
c
ta
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document presents a soil bulk density, BD, range of 0.83 to 1.84.
vi
S
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nj
H^
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^IR. 1997. NC DEHNR Protocol for Performing Indirect Exposure Risk Assessments for Hazardous Waste Combustion Uni
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document also recommends the following:
VD CO
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eden, and Troise 1973) or site-specific procedures,
the use of the CNE
3<8
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• Estimation of annual current runoff, RO (cm/yr), by using the Water Atlas of the United States (Geraghty, Miller, Van d<
such as using the U.S. Soil Conservation Service curve number equation (CNE) (U.S. EPA [1985]) is cited as an examp]
Default value of 0.2 mL/cm3 for soil volumetric water content (
-------
TABLE B-1-4
RUNOFF
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; of the Water Atlas of the United States (Geraght
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•a
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1
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D.C. EPA/600/6-88/005Cc. June.
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1, D. 1980. Fundamentals of Soil Physics. Academic Press, Inc. New, New York.
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in Transport and Internal Dose of Radionuclides. ORNL/NUREG/TM-882.
ing Food Cha\
nan, P.O., and C.F. Baes. 1979. A Statistical Analysis of Selected Parameters for Predict
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es", In: Pollutants in a Multimedia Environment. Yoram Cohen, Ed. Plenum
i waste faciliti
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Publishing Corp. New York.
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recommends the following:
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sources of these values are not identified.
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TABLE B-1-6
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Science and Technology. Volume 22. Number 4. Pages 3i
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Bxposure Risk Assessments for Hazardous Waste Combusl
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s calculated by using the equation in Table B-2-7.
iated with this variable:
(see Table B-2-7) are site-specific. Use of defaul
; variables, will result in estimates of unit soil loss
e. The range of X, calculated on the basis of defa
(0.6 to 36.3 kg/m2-yr).
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Inorganic COPCs: 1
Organic COPCs: 3
COPC enrichment occurs because lighter soil particles erode more than heavier sc
of organic COPCs which is a function of organic carbon content of sorbing media
eroded material than in-situ soil (U.S. EPA 1993). In the absence of site-specific
a default value of 3 for organic COPCs and 1 for inorganic COPCs. This is consi
guidance (1993), which recommends a range of 1 to 5 and a value of 3 as a "reasc
range has been used for organic matter, phosphorus, and other soil-bound COPCs
no sources or references were provided for this range. ER is generally higher in s
loamy soils (U.S. EPA 1993).
The following uncertainty is associated with this variable:
(1) The default ER value may not accurately reflect site-specific conditions; the
underestimated to an unknown, but relatively small, extent.
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Varies (calculated - Table B-1-1)
This value is COPC-and site-specific and should be calculated using the equation
Cs in watersheds, the maximum or average of air parameter values at receptor grii
watershed may be used (see Chapter 4). Uncertainties associated with this variab!
eo
1
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This variable is COPC-specific and should be determined from the COPC tables i
The following uncertainty is associated with this variable:
(1) Uncertainties associated with this parameter will be limited if Kd, values an
Appendix A-2.
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EROSION LOAD TO WATER BO
(SURFACE WATER AND SEDIMENT EQ
(Page 5 of 6)
REFERENCES AND DISCUSSION
in Agricultural Soils." Journal of Contaminant Hydrology.
.5
IS
.F., R.S. Parrish, R.L. Jones, J.L. Hansen, and R.L. Lamb. 1988. "Characterizing the Uncertainty of Pesticide
ume2. Pages 11-24.
oi "3
"o
»
S3
U
i document is the source for a mean soil bulk density of 1.5 cm3 for loam soil.
1
1980. Fundamentals of Soil Phys ics. Academic Press, Inc. New York.
Q
s
—
ffi
such as looseness or compaction of the soil, depending on the
structure,
i document is cited by U.S. EPA (1990) for the statement that dry soil bulk density, BD, is affected by the soil
sr and clay content of the soil.
II
malDose ofRadionuclides. ORNL/NUREG/TM-882.
n and Inte
P.O., and C.F. Baes. 1979. A Statistical Analysis of Selected Parameters for Predicting Food Chain Transpoi
c
ca
1
o
E
i document presents a soil bulk density, BD, range of 0.83 to 1.84 g/cm3.
s
>,
1
&a
1
mbustion
••JR. 1 997. NC DEHNR Protocol for Performing Indirect Exposure Risk Assessments for Hazardous Waste Co
a
w
Q
U
water content.
\
1
document is cited as one of the sources for the range of BD and Kd, values, and the default value for the volui
W2
1
ns. Environmental Criteria and Assessment Office. Office of
tr Emissio
. 1 990. Interim Final Methodology for Assessing Health Risks Associated with Indirect Exposure to Combush
;arch and Development. EPA 600-90-003. January.
•^ CO
^ 3
w °*
c/i
3
oseness or compaction of the soil, depending on the water and
JO
M
a
1
V3
document cites Hillel (1980) for the statement that dry soil bulk density, BD, is affected by the soil structure,
content of the soil.
'£ S
H "3
ssions. External Review Draft. Office of Research and
ustor Emii
1993. Addendum to the Methodology for Assessing Health Risks Associated with Indirect Exposure to Comb
elopment. Washington, D.C. November 1993.
l&
tn
H>
jsed for organic matter, phosphorous, and other soil-based
ecause lighter soil particles erode more than heavier soil
e, concentrations of organic COPCs, which are a function of the
SB!
Ill
£ ° H
document is the source of the recommended range of COPC enrichment ratio, ER, values. This range, 1 to 5,
'Cs. This document recommends a value of 3 as a "reasonable first estimate," and states that COPC enrichmer
cles. Lighter soil particles have higher surface-area-to-volume ratios and are higher in organic matter content.
nic carbon content of sorbing media, are expected to be higher in eroded material than in in-situ soil.
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(Page 6 of 6)
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imends the use of current j
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), was based on a soil orga
Vhelan 1989), and chosen
" "O ^J"
iP H5 •-< ca
This value is site-specific. U.S. EPA OSW i
1997; U.S. EPA 1985) in determining water!
default value of 0.36, as cited in U.S. EPA (
Strenge, Buck, Hoopes, Brockhaus, Walter, i
variable:
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e, use of this value may ca
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represent site-specific conditions. The
overestimated.
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overestimated.
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VERSAL SOIL LOSS EQUATIC
(SOIL EQUATIONS)
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(Page 4 of 5)
REFERENCES AND DISCUSSIO
ental Pollutant Assessment System (MEPAS) Application
i. December.
timedia Environm
hland, Washingtol
, M.B. Walter, and G. Whelan. 1989. Mult
'.meters. Pacific Northwest Laboratory. Ric
ppo, J.G. Jr., D.L. Strenge, J.W. Buck, B.L. Hoopes, R.D. Brockhaus
Guidance: Volume 2 -Guidelines for Evaluating MEPAS Input Para
2
Q
value of 0.36, based on a soil organic matter content of
erodibility factor
3
1
o
•o
i
8
09
8
g
1
1
This document is cited by U.S. EPA 1994 and NC DEHNR 1997 as
1 percent.
c
CS
e Combustion Uni
sure Risk Assessments for Hazardous Wast
DEHNR. 1997. NC DEHNR Protocol for Performing Indirect Expo
U
z
This document recommends the following:
ientative of a whole watershed, not just an agricultural field.
of 0. 1 to be repres
§
1
I
u
"O
cfl
T3
§
t-l
O
CQ
2
• A USLE erodibility factor, K, value of 0.36 ton/acre
• A USLE length-slope factor, LS, value of 1.5 (unitless)
A range of USLE cover management factor, C, values of 0
• A USLE supporting practice factor, P, value of 1
rsal Soil Loss Equation (RUSLE). Agricultural Research
the Revised Unive
r: A Guide to Conservation Planning With
. Department of Agriculture. 1997. Predicting Soil Erosion by Wate,
Service, Agriculture Handbook Number 703. January.
CO
D
CO*
f
a
O
1
S
o
I
i
1
1
face and Ground
**•
e
1
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1
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. EPA. 1985. Water Quality Assessment: A Screening Procedure foi
EPA/600/6-85/002a.
GO
3
lid Waste. Washington, D.C. April.
.EPA. 1988. Superfund Exposure Assessment Manual. Office of Sol
CO
D
of 1.5. This value reflects a variety of possible distance and
ilope factor value
the reference source for the USLE length-!
tershed, not just an agricultural field.
This document is cited by U.S. EPA 1994 and NC DEHNR 1997 as
slope conditions and was chosen to be representative of a whole wa
Working Group Recommendations. Office of Solid Waste
>ustor Emissions.
Associated with Indirect Exposure to Coml
mber 24.
EPA. 1993a. Addendum: Methodology for Assessing Health Risks .
and Office of Research and Development. Washington, D.C. Septe:
GO
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en
3
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e
CS
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2
i
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55
C
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average annual USLE rainfall factors, RF,
This document cites Wischmeier and Smith (1978) as the source of
United States to greater than 300 for the southeast.
This document also recommends the following:
ntrol measures
and agricultural crops
ssumed absence of any erosion or runoff co:
• A USLE cover management factor, C, of 0.1 for both grass
A USLE supporting practice factor, P, of 1, based on the a
52
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ION (USLE)
'ect Exposure to Combustion Emissions. Office of Health and Environmental
H /— * «
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55 ^ Q*
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Review Draft Addendum to the Methodology for A
Office of Research and Development. EPA-600-A
x> +J
en c
ON oa
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i is influenced by vegetative cover and cropping practices, such as planting
;s greater than 0.1 but less than 0.2 are appropriate for agricultural row crops,
R X
ily reflects how erosu
alues for 0.1 to 1; vah
3 >
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the -(1/8) power of the drainage ratio.
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:s document concludes that the sediment delivery ratios vary approximately wi
ited by U.S. EPA (1993) as
yields from watersheds, thi
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variable is site-specific and should be an annual average.
following uncertainty is associated with this variable:
Use of default average volumetric flow rate ( VfJ information may not accurately represent site-
especially for those water bodies for which flow rate information is not readily available. There
values may contribute to the under- or overestimation of total water body COPC concentration,
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following uncertainty is associated with this variable:
The default values for the variables in the equation in Table B-2-10 may not accurately represei
- specific conditions. However, the range of several variables— including dbs, CBS, and 6b— is re
Other variables, such as d^ and dz, can be reasonably estimated on the basis of generally avails
The largest degree of uncertainty may be introduced by the default medium-specific organic cai
content values. Because OC content values may vary widely in different locations in the same i
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following uncertainty is associated with this variable:
All of the variables in the equation in Table B-2-11 are site-specific; therefore, the use of defau
of these variables will contribute to the under- or overestimation of Cmat The degree of uncerti
the variable k,, is expected to be under one order of magnitude and is associated largely with the
soil loss, X,, values for the variables fm, k,, and/,,, are dependent on medium-specific estimates i
Because OC content can vary widely for different locations in the same medium, uncertainty as
three may be significant in specific instances.
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REFERENCES AND DISCUSSION
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TWeRM Assessments for Hazardous Waste Combustion Uni
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accurately reflect site- and water body-specific conditions long term.
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ference was cited for this range.
bllowing uncertainty is associated with this variable:
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conditions. However, any uncertainly introduced is
range.
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**^ V fli U 7S
11 -2 1 1
*^ *^ 5 S jiS
* (U O Tl
a J3 M « "c
1 ~ S '^.«
S2 t» "<3 M
^_, -S s ^ u
» eo .2 J= -°
Varies
variable is site-specific. U.S. EPA OSW recommend
depth, consistent with NC DEHNR (1997):
dt = d^ + d^
bllowing uncertainty is associated with this variable:
Calculation of this variable combines the concentrati
summed. Because most of the total water body dept
uncertainties associated with dwc are not expected to
variable, dt, are also not expected to be significant.
.2 •§" o
£.8 iS £
s
f
•8
i
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u
&
~a
o
H
•a"
X
0
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C^- ^ . ^
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WO *5
co "3 "§ o
5 .2 8 «
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'? "« '52
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C *-• D< W
11 ^2
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1 2 •« -
l! o '55 C
±; _e u ^ o
3 £ o e -a
jt ^ c o a.
^ ca » c
® ^ g S 2 |
" sla &a
variable is site-specific. U.S. EPA OSW recommend
i that this value should be reasonable for most applica
U.S. EPA (1993b and 1994) and NC DEHNR (1997]
bllowing uncertainty is associated with this variable:
The recommended default value may not accurately
the variable/^ may be under- or overestimated; the
based on the narrow recommended range.
.2 o E u ^
H to o c"* ^^
S
"g J 5
o 5 ob
f
e
_o
1
u
o
o
12
"o
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'^
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u
ra
S
PQ
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o
CQ
CQ
H
in
%
Tt
I
£
CO
§
1
S
a
§
i
i
a
o
2
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>
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O
s
"73
«
00
>>
«
C)
0
+j
o
D.
S
0.6
variable is site-specific. U.S. EPA OSW recommends a default bed sedime
CQ
^^
en
ON
^
§1
D^
c
•J
C3
«°
i
m3 and a solid density (p,) value of 2.65 kg/L, calculated by using the folio'
"So
0bs = 1 -BS/ps
is consistent with other U.S. EPA (1993b and 1994) guidance.
1
following uncertainty is associated with this variable:
a
•o
w c
J3 cd
c o
• £rt ^^
•o '3
1 g
__ CO
^ a
"O u
§^*
Ji*
Co "^
05 «J
~ 3
efl r>
u u
2 B
ea "t?
"C
> O
0 "^
.B ^
Calculation of this variable combines the uncertainties associated with the
calculation. To the extent that the recommended default values of BS and
o
•6
cd
1
C
fe
1
'I
I
•3
g
u
0
s
fc
j
&
"w
§
a.
1
•3
c/3
T3
U
O?
Varies (see Appendix A-2)
-------
o
1-H
«
tt
K
3
PQ
•<
H
H
Z
a
5 /-"v
B &
s§
S g
B<
3 s
H R
z w
W H
« Z
0 g
Z S
^5
z 3
S w
3 Q
J Z
O <<
Was
tf W
a H
H <
$*
& W
Z U
NN ^
§§
S p
H So
rj -'
S
'ERENCES AND DISCUSSION
a*
$
1
ba
ssessments for Hazardous Waste Combustion Unit
.. 1997. NC DEHNR Protocol for Performing Indirect Exposure Risk A
K
§
W
Q
U
Z
en
CB
T3
«J
'o
lent is also
sediment, respectively. This docurr
1
53
sumed OC values of 0.075 and 0.04 for surface wal
ocument is cited as one of the sources of the range of Kd, values and ass
•o
CO
f
H
I a
£'!l
:al water bo
is documen
yer. Thede
:e of the equation for calculating tot
alue for bed sediment porosity. Th
ue for depth of the upper benthic la;
Hi
a-Sl
:e of information. This document is also cited as tl
as one of the reference source documents for the d
one of the reference source documents for the defi
the sources of TSS. This document cites U.S. EPA (1993b) as its sourc
No source of this equation was identified. This document is also cited
PA ( 1 993b) as its source of information. This document is also cited as
^- - rrj
O -C
1993b) as its source of information for the range oi
t bed sediment concentration.
is the midpoint of an acceptable range. This document cites U.S. EPA (
tent is also cited as one of the reference source documents for the defaul
0 fc
3 3
CJ
« O
> -o
earch and
ternal Review Draft. Office of Res
£
&5
'ated with Indirect Exposure to Combustor Emissic
993a. Addendum to the Methodology for Assessing Health Risks Associ
3pment. Washington, D.C. November 1993.
_
o
<: Z
^ o
CU Q
nl ""^
PU
t/3
Z>
& 53
fe S 1 I
*- a o ^
1 H £ § § ,
I ss § '1 1 5
^•Sff.SS
sediment, respectively. The generic
value; however, OC is medium-spe
Y 7.5 and 4, because the OC values
ent porosity ( 6bs); no source of this
range was identified. Finally, this
10 to 20 be specified in streams an
•o ,a * a .a -g
g S K =5 •£ o
s 0 S U S
i_ o 2 "> "-1 -a
« D, 13 TI 0 ^
iumed OC values of 0.075 and 0.04 for surface wat
follows: Kd,j = Koc * OC,. Koc is a chemical-s
d,,, values were estimated by multiplying the Kd, v
iment also presents the equation for calculating be*
nthic solids concentration (BS); no original source
to 10 be specified for parks and lakes, and a TSS \
ocument is cited as one of the sources of the range of Kd, values and ass
jting partition coefficients (soil, surface water, and bed sediments) is as
, values was based on an assumed OC value of 0.01 for soil. Kd^, and K
diment are 7.5 and 4 times greater than the OC value for soil. This doci
led. This document was also cited as the source for the range of the be
mends that, in the absence of site-specific information, a TSS value of 1
-o — 13 o sr c
-1 1 * -S § 1
f 13 <4- c £ H
H o o « .2 "
a
w
I
of Solid W
» Group Recommendations. Office
1
with Indirect Exposure to Combustor Emissions. )
993b. Addendum: Methodology for Assessing Health Risks Associated
of Research and Development. Washington, D.C. September 24.
— o
O
.S. EPA (1994) as the source of the
he depth of the upper benthic layer
P s
"S"3
!&
This document is also cited by NC DEHNR (1997;
fault bed sediment concentration value, and the rar
ocument is cited by NC DEHNR (1997) as the source of the TTS value.
:nt porosity value and the equation used to calculate the variable, the de:
•o £
& .£
"2 "O
f u
H to
4
f Guidance.
nent C, Draft Exposure Assessment
•5
5
•3
Combustor Facilities Burning Hazardous Wastes.
994. Draft Guidance for Performing Screening Level Risk Analyses at i
Hazardous Waste Combustion Facilities. April 15.
•<
<5
n U
Si °<
W
CO
D
&
IS
ibrmation. '
.S. EPA (1993b) as its source of ini
D
CO
£
'3
It value for bed sediment porosity. This document
ocument is cited as one of the reference source documents for the defau
"O
CO
2
H
C4
'£ 8
SB
H
« h
alue is the midpoint of an acceptab
iment is also cited as one of the reft
*• 5
a o
i "°
<2 2
o ?
t value for depth of the upper benthic layer. The d
values for the depth of the upper benthic layer. Tl
icnt is also cited as one of the reference source documents for the defaul
tent cites U.S. EPA (1993b) as its source of information for the range of
icnts for the default benthic solids concentration.
SEE
333
U U O
o o o
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0\
t-
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Z
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n
TABLE
N
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<
H
VI
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u o
z ex
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li
g o
Q Ed
WATER BODY
WATER AND S
LL TOTAL
(SURFACE
F**4
OS
Ed
o
BO
1
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.s « ^ •§ g s>
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c co 53 f; •s *
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• <*• c oo c -o
2 S | § 8 a
' 3 -»-< J-t r . W
S 1 g| o|
4i *•* .O fli *4-« Ofi
3 i 2 3 S £,
.s 2 ll II
Varies (calculated - Table B-2-13)
ariable is COPC- and site-specific, and is calculated by using the equation i
ated with this variable include the following:
All of the variables in Table B-2-13 are site-specific. Therefore, the use o
variables could contribute to the under- or overestimation of kv.
The degree of uncertainty associated with the variables dt and TSS is expe<
information necessary to estimate these variables is generally available or
narrow.
Values for the variable k, and Airfw are dependent on medium-specific estii
content can vary widely for different locations in the same medium, uncer
variables may be significant in specific instances.
> *r?
.2 o
s eft ^^. ^*. ^*.
_
k
u
2
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o
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i§
ca
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c
3
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53 -5
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H ^ jj | o g- c
.S a5So'5 e8R
Varies (calculated - Table B-2-10)
ariable is COPC- and site-specific, and is calculated by using the equation :
tainties associated with this variable include the following:
The default variable values recommended for use in the equation in Table
site-specific water body conditions. However, the range of several variabi
relatively narrow; therefore, the degree of uncertainty associated with thes
small. Other variables, such as d^ and dt, can be reasonably estimated on
information.
The largest degree of uncertainty may be introduced by the default mediur
content values are often not readily available and can vary widely for diffe
Therefore, the degree of uncertainty may be significant in specific instanci
> g
•2 c ^ /-,
H S C- CJ-
CA
J-
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3
O
u
>, u
o '-S
XI C
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l|
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ca P *u
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1 1 J ^ | ^"
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Varies (calculated - Table B-2-16)
ariable is COPC- and site-specific, and is calculated by using the equation :
tainties associated with this variable include the following:
All of the variables in Table B-2-16 are site-specific. Therefore, the use o
values, for any or all of these variables, will contribute to the under- or ovi
The degree of uncertainty associated with each of these variables is as foil
magnitude at most, (2) BS, dbr Vfff TSS, and Aw— limited because of the ni
variables or because resources to estimate variable values are generally av
site-specific and degree of uncertainty unknown.
> lg
.2 o
P 5 B &
— .
k
^_,
1
s
o
u
o
03
13
3
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0
IS
n
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e
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'S
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any or all
c ?
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s .s -S
(9 T3 *J
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'l> S to
— "O o
a. a js
inim
depe
i
f
e
s
be
ar
ble
to
d
m
ab
lt v
ted
Kd
ari
ati
de
expec
s Kv an
ing from volati
refore, the use
t, and TSS are
or the variable
ciated with the
« <0
1 a
S S "8
•J3 •—l rj
"^ ™ "^
•o ja I
O -~ tf "3
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= u
u <*« 55 £•
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i
CQ
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EN
ECONS
TIONS)
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£53 g •« .E % •§
jB £5 o £ € E
-2 • •§ 2 "S E a
•§ •§ rt. S '§ :| u
2 u» "a «3 ?* e "
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CS "• *C "S O 3 U ^
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Varies (calculated - Table B-2-13)
variable is COPC- and site-specific, and is calculated by using the equation
rtainties associated with this variable include the following:
All of the variables in Table B-2-13— except R, the universal gas constant,
Therefore, the use of default values, for any or all these variables, could co
Kv.
The degree of uncertainty associated with the variables H and Twk is expect
well-established, and average water body temperature, Twk, will likely vary
The uncertainty associated with the variables KL and KG is attributable larg
content. Because OC content values can vary widely for different location
values may generate significant uncertainty in specific instances. Finally, 1
unknown; therefore, the degree of associated uncertainty is also unknown.
•- " ^ ^ /->
fS ;§ S S S
t
&
2
t_
1
1
^j
Eh
i- -—
*^ IM
U **-*
o 8
fef
^%
«3 ta -f<
Varies (site-speciflc)
variable is site-specific and should be an average annual value.
following uncertainty is associated with this variable:
Use of default values for depth of water column, d^., may not accurately r<
those water bodies for which depth of water column information is unavail
d^. values may contribute to the under- or overestimation of total water hot
degree of under- or overestimation is not expected to be significant.
'£ ° —
H S C
£
c
|
1
53
ta
o
x
s.
JT
Q
u
"^
15 °Q
-•§« i
•s Z >. >-
?g •g'S
>-" S -D "°
Is II
8-g a I
O ea |B o
"ft ^ 0 *
0 OS 0, o
J3 *S
0.03
variable is site-specific. U.S. EPA OSW recommends a default upper-bentl
1 on the center of this range cited by U.S. EPA (1993b). This is consistent v
?)•
"ollowing uncertainty is associated with this variable:
Use of default values for depth of upper benthic layer, dbs, may not accurat
conditions. However, any uncertainty introduced is expected to be limited,
W U O\ -v
"3 ^ O\ S- >—*
J3 (3 S fC £2
H jo C- H C-
£
0
E
1
GA
U
1
1
53
a.
o.
3
o
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n. u
0 >>
D —
"^
-------
PQ
S
PQ
H
Z
GQ w
W H
||
II
3z
P«
*o '5
8«* P-
05 f
tf5 C 4)
u O *S
3 "J3 w
^1^
te ° o
e .a s
£ it5 5
c y *-"
j |||
Varies (see Appendix A-2)
variable is COPC-specific and should be determined from the COPC tables in Append
bllowing uncertainty is associated with this variable:
The values contained in Appendix A-2 for Kd^, are calculated on the basis of default
soil. Kd^ values based on default values may not accurately reflect site-and water bo
under- or overestimate actual Kdm values. Uncertainty associated with this variable \
medium-specific OC estimates are used to calculate Kdm.
.2 u ^
S
8
1
1-
° S
E "5
'"5 £
EC O
•a R
w
•o c
c o
CL .^
c« "C
3 a
c/2 a,
4
IB
| 0 I
% o
S 2P 45 S 5
3 E ^ o -O
1 o •§ 5 'S
> — < C cs c
T3 'S 3 > 0
u O ^ >-^ o
S " c ^ u
a § !§ 73
H >-< o "O oo
& V *S W F*-
2 to 300
variable is site-specific. U.S. EPA OSW recommends the use of site- and waterbody (
sentative of long-term average annual values for the water body of concern (see Chapl
by NC DEHNR (1997), U.S. EPA (1993a), and U.S. EPA (1993b) in the absense of si
bllowing uncertainty is associated with this variable:
Limitation on measured data used for determining a water body specific total suspend
accurately reflect site- and water body-specific conditions long term. Therefore, the
under-or overestimation of /„..
111 1
1
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g
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QJ
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g.2
cin ^
3 *"*
M C
*«3 o
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•
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5
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jommendations. Office of Solid Waste
1
Q,
3
O
0
$
3
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1
=
a
g
for Assessing Health Risks Associated with Indirect Exposure to Combustor Em,
tit. Washington, D.C. September 24.
ndum: Methodology
arch and Developmel
u u
^J en
-w t>
^£
J-, 0
r^ u
ON o
ON ic
«— • U-.
o
< T3
& c
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yer (d,,,). This document is also cited by
_e«
U
1
1
1-1
O>4
3
U
«M
O
1
•Q
>94) and NC DEHNR (1997) as the source of the range and default value for the <
7SS value.
ited by U.S. EPA (IS
) as the source of the
o r~
.2 |
|g
3 fc
U X
^g
W5 '"'
1^
Exposure Assessment Guidance for
t
Q
U"
c
^M
u
g
•W*
"
S
E^
^
^
ning Screening Level Risk Analysis at Combustion Facility Burning Hazardous V
ycility. April 15.
juidancefor Perforn
Waste Combustion Ft
%- s
!•§
*** ^
^ s
ON ,«
ON a;
" S
il
5 midpoint of an acceptable range. This
.22
u
_s
"a
>
3
S
^M
T3
U
S
^
R4
:rence source documents for the default value of the depth of the upper benthic li
source of information.
ited as one of the refi
i.EPA(1993b)asits
o VJ
-^ 3
*J en
C U
u "
E o
If
•o S
•2 3
£ 0
H T3
U
t/5
c/i
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PQ
&
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en w
i. S 8
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ill
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h
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ted
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II
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NM ^J
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Varies (calculated - Table B-2-14)
Ui
•£"
!
1
y—
**-
8
<§
cfl
a
w
a
o,
12
's
a-
J
is variable is COPC- and site-specific, and is calculated by using the equation in Table B-2-14.
j*
P
certainties associated with this variable include the following:
e
5
u
m*
'o
3
U 14- K
30 0 S
111 1 8 1 .8
Minimal or insignificant uncertainty is assumed to be associated with six variables — Dw u, dff pa pw, i
rtv— either because of narrow recommended ranges for these variables or because information to estim
variable values is generally available.
No original sources were identified for the equations used to derive recommended values or specific
recommended values for variables Cd, k, and At. Therefore, the degree and direction of any uncertain!
associated with these variables are unknown.
Uncertainties associated with the variable W are site-specific.
Varies (calculated - Table B-2-15)
is variable is COPC- and site-specific, and is calculated by using the equation in Table B-2-15.
certainties associated with this variable include the following:
of the variables in Table B-2- 1 5, with the exception of k, are site-specific. Therefore, the use of default
tier than site-specific values, for any or all of these variables, will contribute to the under- or overestimati
. The degree of uncertainty associated with each of these variables is as follows:
Minimal or insignificant uncertainty is assumed to be associated with the variables £)„, //„, and pa, bee
these variables have been extensively studied, and equation procedures are well-established.
No original sources were identified for equations used to derive recommended values or specific
recommended values for variables C^ k, and dv Therefore, the degree and direction of any uncertainti
unknown.
Uncertainties associated with the variable W are site-specific and cannot be readily estimated.
O 52- C- P D < 2 !* C Ci C-
^
-C»
'c
u
'5
S
o
o
u
<§
c
u
&
ca
a.
«
«
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s*? t<
n
-------
fl
09
3
pa
,
o
1
1
I
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w
s
a
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3
1
eg
>
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h -a
4) c
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3 "S
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03 ii
E -a
. u
^ ^ 1
< < .1
S x «
t3 -3 SJ
C e u
0 u >
& ft 0
ft n, u<
< < 0
.S e i
^ -^ S
o 2 "2
1 J §
S .ts o
u §•?
« ft "cfl
Varies (see Appendix A-
-specific and should be determined from the C(
inty is associated with this variable:
ariable, estimated by using the parameters and
actual COPC-specific values. As a result, K, n
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Page (4 of 4)
REFERENCES AND DISCUSSION
Working Group Recommendations. Office of Solid Waste
tn
9r Emission,
ssociated with Indirect Exposure to Combusti
mber 24.
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d Waste. December 14.
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To the extent that site-specific or local values for this variable ari
represent site-specific conditions. The uncertainty associated wii
range of windspeeds at a single location may be more significant
single windspeed to represent all locations.
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(Page 4 of 4)
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REFERENCES AND DISCUSSION
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This document
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.s
Risks Associated with Indirect Exposure to Combustor Emissi
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This document
sublayer thickn
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Waste. December 14.
^s T:
Level Risk Analyses at Combustion Facilities Burning Hazar
Office of Emergency and Remedial Response. Office of Soli
for Performing Screening
te Combustion Facilities.
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CRA Hazardous Was
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atainties associated with this variable include the following:
The default values for empirical intercept coefficient, a, recommended for use in th
average values based on various studies of sediment yields from various watershed.'
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contribute to under- or overestimation of the benthic burial rate constant, kb.
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on a review of sediment yields from various watersheds. This single default value i
site-specific water shed conditions. As a result, use of this default value may contri
ofkb.
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photographs, and gauging station measurements— from which average volumetric fl
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the uncertainty is expected to be relatively small. Other variables, such as d^. and df, c
the basis of generally available information. The largest degree of uncertainty may be
medium specific OC content values. OC content values are often not readily available
different locations in the same medium. Therefore, default values may not adequately
conditions.
Varies (calculated - Table B-2-9)
variable is COPC- and site-specific, and is calculated by using the equation in Table B-
following uncertainty is associated with this variable:
The default variable values recommended for use in the equation in Table B-2-9 may r
-specific water body conditions. The degree of uncertainty associated with variables I
to be limited either because the probable ranges for variables are narrow or informatioi
is generally available. Uncertainty associated with/w is largely the result of water bod
content values, and may be significant in specific instances. Uncertainties associated >
water body (L,) and overall total water body COPC dissipation rate constant (&„,) may
instances because of the summation of many variable-specific uncertainties.
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PER AND SEDIMEN1
(SURFACE WA'
§
(Page 4 of 4)
2RENCES AND DISCUSS!
b
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'5
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'aste Combust
ssessments for Hazardous W
NC DEHNR Protocol for Performing Indirect Exposure Risk A
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icument cites U.S. EPA (199:
is cited as one of the sources of the range of db, values. This dc
c
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is cited by U.S. EPA (1994) and NC DEHNR (1997) as one of
c
CO
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&:
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Asians. External Review Draft. Office of Research and
i.
to Combusto
iated with Indirect Exposure
ddendum to the Methodology for Assessing Health Risks Assoc
Washington, D.C. November.
•^
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ON Q.
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iter column, cannot be precisely specified. However, the
ca
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librium with i
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states that the upper benthic sediment depth, dbs, representing t
5 that values from 0.01 to 0.05 meter would be appropriate.
= 1
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•.. Attachment C, Draft Exposure Assessment Guidance for
HJ
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•aft Guidance for Performing Screening Level Risk Analyses at
us Waste Combustion Facility. April 15.
Q|
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WJ
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ended value is the midpoint of an acceptable range. This
and db! is expected to be minimal either because informatil
;iated with the variables /^ and Cwo/ is largely associated
ium, use of default medium-specific values can result in
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32 D. a
depth of upper benthic layer
of uncertainty associated wil
for a variable (dj,,) is narrow
iry widely in different locatio
is cited as one of the reference sources for the default value for
U.S. EPA (1993a) as the source of its information. The degree
hese variables is generally available (d^) or the probable range
default OC content values. Because OC content is known to va
:rtainty in some instances.
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variable is COPC- and site-specific, and is calculated by using the equation in Table B-2-1'
following uncertainty is associated with this variable:
All of the variables in Table B-2-17 are COPC- and site-specific. Therefore, the use of def
specific values, for any or all of these variables, will contribute to the under- or overestimal
The degree of uncertainty associated with the variables dm and dh, is expected to be minimi
for estimating a variable (d^) is generally available or because the probable range for a vai
uncertainty associated with the variables fm and Cwtol is associated with estimates of OC co
values can vary widely for different locations in the same medium, using default OC value
uncertainty in specific cases.
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DISSOLVED PHASE WATER CONCENTRATION
(SURFACE WATER AND SEDIMENT EQUATIONS
(Page 3 of 3)
>>
3
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jj
REFERENCES AND DISCUSSION
NC DEHNR Protocol for Performing Indirect Exposure Risk Assessments for Hazardous Waste Combustion Uni
DEHNR 1997. .
U
z
) as its sources of information regarding TSS, and
J3
f"J
$
y
m
o\
o\
is cited as one of the sources for Kd, values and a default TSS value of 10. This document cites (1) U.S. EPA (1
as its source regarding Kd,.
This document
(2) RTI (1992)
ng Group Recommendations. Office of Solid
3
1
§'
.0
ddendum to the Methodology for Assessing Health Risks Associated with Indirect Exposure to Combustor Emiss,
ce of Research and Development. Washington, D.C. September 24.
^ £
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1 "§
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W &
CO
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lie of 0.075 for surface water. The generic
ecific value; however, OCis medium-specific.
Kd, values by 7.5, because the OC value for
s source of the recommended TSS value.
•a g- o -s
> _i •£ x
&•§ t?~
E -S Rr
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E|J-H CX 1— <
o -a C-
is cited by U.S. EPA (1994) and NC DEHNR (1997) as one of the sources of the range ofKd, value and the assu
Iculating partition coefficients (soil, surface water, and bed sediments) is as follows: Kdv = Kxj * OC,. Kx is a
'd, values was based on an assumed OC value of 0.01 for soil. Therefore, the Kdm values were estimated by mull
> 7.5 tunes greater than the OC value for soil. This document is also cited by U.S. EPA (1994) and NC DEHNR
This document
equation for ca
The range of A
surface water if
view Draft. Office of Research and
u
rv!
External 1
ddendum: Methodology for Assessing Health Risks Associated with Indirect Exposure to Combustor Emissions.
November.
EPA. 1993b. A
Development.
yi
b
le of 0.075 for surface water. The generic
Ecific. The range of Kd, values was based on an
ir surface water is 7.5 times greater than the OC
•a S"2
™ A a
8Ji .
•o ^ d
•o o u 3
1 SO 5
is cited by U.S. EPA (1994) and NC DEHNR (1997) as one of the sources of the range ofA^, value and the assui
Iculating partition coefficients is as follows: Kdv = Kxj * OC,. Kx is a chemical-specific value; however, OC is
ilue of 0.01 for soil. Therefore, the Kdm values were estimated by multiplying the Kd, values by 7.5, because the
Fhis document is also cited by U.S. EPA (1994) and NC DEHNR (1997) as the source of the recommended TSS i
This document
equation for cal
assumed OC va
value for soil. '
f C, Draft Exposure Assessment Guidance for
s
.«
1
"5
aft Guidance for Performing Screening Level Risk Analyses at Combustion Facilities Burning Hazardous Waste.
us Waste Combustion Facilities. April 15.
EPA. 1994. Dn
RCRA Hazardo
CO
b
is cited as one of the sources of the range of Kd, values, citing RTI (1992) as its source of information.
This document
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following uncertainty is associated with this variable:
The default variable values recommended for use in the equation in Tal
-specific water body conditions. The degree of uncertainty associated i
to be limited either because the probable ranges for these variables are i
estimates is generally available.
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be significant in specific instances. Uncertainties associated with the v;
because of the summation of many variable-specific uncertainties.
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Varies (see Appendix A-2)
variable is COPC-specific, and should be determined from the COPC ta
following uncertainty is associated with this variable:
The default range (8 to 2,100,000 L/kg) of Kdbs values are based on def;
Because medium-specific OC content may vary widely at different loc<
associated with Kdbl values calculated by using default OC content vah
s a e
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e o s u ft
S S O k4 U
e o o eo 3
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0.4 to 0.8
Default: 0.6
variable is site-specific. U.S. EPAOSW recommends a default bed sedi
:m3 and a solids density [/oj value of 2.65 kg/L), calculated by using the
eb, = i -BS /p,
is consistent with other U.S. EPA (1993b and 1994) guidance.
following uncertainty is associated with this variable:
To the extent that the recommended default values of BS and p, do not
body-specific conditions, 6bs will be under- or overestimated to some d
expected to be minimal, based on the narrow range of recommended va
.2 -Si .2 o
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0.5 to 1.5
Default: 1.0
, U.S. EPA OSW recommends a default value of 1
tie reasonable for most applications. No reference
S. EPA (1993b and 1994) guidance.
associated with this variable:
ault value for BS may not accurately represent site
Csed may be under- or overestimated to a limited
o ~ -; «; « 4J .
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Varies (site-specific)
associated with this variable:
es may not accurately reflect site-specific conditio:
inder- or overestimation of the variable Csed. How
sources allowing reasonable water body-specific e
o K s ~ K
Ctv* "3 O
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0.03
. U.S. EPA recommends a default upper-benthic si
ted by U.S. EPA (1993b). This is consistent with
associated with this variable:
;s may not accurately reflect site-specific conditioi
- or overestimation of the variable Cscd. However,
TOW recommended range of default values.
.a 3 -2 js s a
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DISCUSSION
REFERENCES AND
zardous Waste Combustion Units. January.
DEHNR. 1997. NC DEHNR Protocol for Performing Indirect Exposure Risk Assessments for Ha.
U
z
993a; 1993b) as its source of
t value is the midpoint of an
lyer. This document is also cited as
_H *-H fc«
ro 3 ~^
liment porosity ( 6bs). This document cites U.S. EPA 1
t value for depth of the upper benthic layer. The defa
the range of values for the depth of the upper benthic
This document is cited as one of the reference source documents for the default value for bed sed
infonnation. This document is also cited as one of the reference source documents for the defaul
acceptable range. This document cites U.S. EPA (1993a; 1993b) as its source of information for
one of the reference source documents for the default benthic solids concentration ( BS).
•raft. Office of Research and
u
Exposure to Combustor Emissions. External Review
. EPA. 1993a. Addendum to the Methodology for Assessing Health Risks Associated with Indirect
Development. Washington, D.C. November 1993.
cr>
S
ir sediment. The generic equation for
1 is medium-specific. The range of
OC value for sediment is four times
lis equation was identified. This
<£
range of Kd, values and an assumed OC value of 0.04
This document is cited by U.S. EPA (1994) and NC DEHNR (1997) as one of the sources of the
y u
•43
'x * OC,. Kx is a chemical-specific value; however, O
imated by multiplying the Kd, values by 4, because th
alculating bed sediment porosity ( 6bs). No source of
source of this range was identified.
calculating partition coefficients (soil, surface water, and bed sediments) is as follows: Kdu = K
Kd, values was based on an assumed OC value of 0.01 for soil. Therefore, the Kdb, value was est
greater than the OC value for soil. This document is also cited as the source of the equation for c
document was also cited as the source for the range of the benthic solids concentration (BS). No
mendations. Office of Solid Waste
e
>sure to Combustor Emissions. Working Group Recoi
EPA. 1993b. Addendum: Methodology for Assessing Health Risks Associated with Indirect Expc
and Office of Research and Development. Washington, D.C. September 24.
CO
S
U
i
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!
0
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73
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83
1
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en
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73
>ed sediment porosity value (6bs), the default benthic s
This document is cited by NC DEHNR (1997) and U.S. EPA (1994) as the source of the default I
range for depth of upper benthic layer (dbt) values.
posure Assessment Guidance for
t3
es Burning Hazardous Wastes. Attachment C, Draft 1
EPA. 1994. Draft Guidance for Performing Screening Level Risk Analyses at Combustor Faciliti
RCRA Hazardous Waste Combustion Facilities. April 15.
CO
S
as its source of information
lent cites U.S. EPA ( 1993a; 1993W
s- c
of 0.04 for sediment. This document cites RTI (1992
fault value for bed sediment porosity ( 6L). This docu
This document is cited as one of the sources of the range of Kd, values and an assumed OC value
regarding Kd, values. This document is cited as one of the reference source documents for the de
lit value is the midpoint of an
yer. This document is also cited as
.« «
t value for depth of upper benthic layer ( dbs). The def
the range of values for the depth of the upper benthic 1
as its source. This document is also cited as one of the reference source documents for the defaul
acceptable range. This document cites U.S. EPA (1993a; 1993b) as its source of information for I
one of the reference source documents for the default benthic solids concentration (BS).
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TABLE B-3-1
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ESTRIAL PLANT EQ
(Page 3 of 10)
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'4b; 1995) in development of
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ertainties associated with this
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Anions: 0.20
Cations and most Organics: 0.6
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Consistent with U.S. EPA (194b; 1995) in evaluating aboveground forage, U.S. EPA OSW recommends using tl
value of 0.2 for anions and 0.6 for cations and most organics. These values are the best available information, bi
on a review of the current scientific literature, with the following exception: U.S. EPA OSW recommends using
Fw value of 0.2 for the three organic COPC that ionize to anionic forms. These include (1) 4-chloroaniline, (2) i
nitrosodiphenylamine, and (3) n-nitrosodi-n-proplyamine (see Appendix A-2).
The values estimated by U.S. EPA (1994b; 1995) are based on information presented in Hoffman, Thiessen, Frai
and Blaylock (1992), which presented values for a parameter (r) termed the "interception fraction." These value
were based on a study in which soluble radionuclides and insoluble particles labeled with radionuclides were
deposited onto pasture grass (specifically a combination of fescues, clover, and old field vegitation) via simulate
rain. The parameter (r) is defined as "the fraction of material in rain intercepted by vegetation and initially retail
or, essentially, the product of Rp and Fw, as defined for use in this guidance:
r = Rp • Fw
The r values developed by Hoffman, Thiessen, Frank, and Blaylock (1992) were divided by an Rp value of 0.5 fi
forage (U.S. EPA 1994b). TheFw values developed by U.S. EPA (1994b) are 0.2 for anions and 0.6 for cations
insoluble particles. U.S. EPA (1994b; 1995) recommended using the Fw value calculated by using the r value fr
insoluble particles to represent organic compounds; however, no rationale for this recommendation is provided.
Uncertainties associated with this variable include the following:
(1) Values of r developed experimentally for pasture grass (specifically a combination of fescues, clover, and i
field vegitation) may not accurately represent all forage varieties specificto a site.
(2) Values of r assumed for most organic compounds, based on the behavior of insoluble polystryene
microspheres tagged with radionuclides, may not accurately represent the behavior of organic compounds
under site-specific conditions.
Varies (modeled)
This variable is COPC- and site-specific, and is determined by air dispersion modeling (see Chapter 3).
Uncertainties associated with this variable are site-specific.
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U.S. EPA OSW recommends thefcp value of 18 recommended by U.S. EPA (1993; 1994b).
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the midpoint of a possible range of values. U.S. EPA (1990) identified several processes— il
water removal, and growth dilution— that reduce the amount of contaminant that has been de
•
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surface. The term kp is a measure of the amount of contaminant lost to these physical proce
EPA (1990) cited Miller and Hoffman (1983) for the following equation used to estimate kp
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kp = (In 21 tl/2) • 365 days/yr
where:
t1/2 = half-time (days)
Miller and Hoffman (1983) report half-time values ranging from 2.8 to 34 days for a variety
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herbaceous vegetation. These half-time values result in kp values of 7.44 to 90.36 yr '. U.S
recommend a kp value of 18, based on a generic 14-day half-time, corresponding to physica
c
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14-day half-time is approximately the midpoint of the range (2.8 to 34 days) estimated by M
(1983).
Uncertainties associated with this variable include the following:
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(1) Calculation of kp does not consider chemical degradation processes. The addition of c
processes would decrease half-times and thereby increase kp values; plant concentratil
« =g
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increases. Therefore, use of a fcp value that does not consider chemical degradation pr
(2) The half-time values reported by Miller and Hoffman (1983) may not accurately repre
COPCs on plants.
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(3) Based on this range (7.44 to 90.36), plant concentrations could range from about 1 .8 ti
times lower than the plant concentrations, based on a kp value of 18.
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: values in the absenc
0.12
This variable is site-specific. U.S. EPA OSW recommends the use of these defauli
s
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1997) recommended
essive grazing.
site-specific information. U.S. EPA (1990), U.S. EPA (1994b), and NC DEHNR (
a constant, based on the average periods between successive hay harvests and succ<
T3
0
I
(11
days) and the averagi
follows:
For forage, the average of the average period between successive hay harvests (60
between successive grazing (30 days) is used (that is, 45 days). Tp is calculated as
&
Tp = (60 days + 30 days)/ 2 -f 365 days/yr = 0. 12
|
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ulating the COPC co
These average periods are from Belcher and Travis (1989), and are used when calc
in cattle forage.
The following uncertainty is associated with this variable:
1
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(1) Beyond the time frame of about 3 months for harvest cycles, if the kp value r
Tp values will have little effect on predicted COPC concentrations in plants.
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0.12
U.S. EPA OSW recommends using the value of 0.12. This default value is based c
CO
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1 the range of 80 to 95 percent water content in herbaceous plants and nonwoody pla
The following uncertainty is associated with this variable:
?-.
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Tf\
it from plant varietiei
(1) The plant species considered in determining the default value may be differei
present at a site.
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REFERENCES AND DISCUSSION
'ronmentally Released Radionuclides through Agriculture .
1
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Q£
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^ 2
U o
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ca
n
;s. Class-specific estimates of the empirical constant, y> were
n estimates of Rp and Yp.
z g
CA 3
.3 E
e x
lip developed by Chamberlain (1970) for other vegetation
ough several points, including average and theoretical ma
it proposed using the same empirical relations!
forcing an exponential regression equation thr
c ^
CO >>
o u
o g.
•a 2,
01 O
JS %
H T3
irt on Sensitivity and Uncertainty Analysis for the Terrestrial Food
Oak Ridge National Laboratory. Oak Ridge, Tennessee.
&§
of ;a
; RURA and Municipal Waste Combustion Projects: Final
, Office of Risk Analysis, Health and Safety Research Div
C.C.Travis. 1989. "Modeling Support for tht
" Interagency Agreement No. 1824-A020-A1,
•o -3
§"8
^!l
-i %
J U O
u
~s
03
eb
_e
*N
CS
i period between successive hay harvests and successive g:
t recommends Tp values based on the average
c
documei
c«
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Tt
tH
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oveml
Science and Technology. Volume 22. Pages 361-367. N
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IR (1997) as the source of the equations for calculating Fv.
t is cited by U.S. EPA (1994a) and NC DEHN
c
documei
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00
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:tive Aerosols by Vegetation." Atmospheric Environment.
1970. "Interception and Retention of Radioac
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£
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= Empirical constant; range provided z
= Standing crop biomass (productivity
(£• x. -?•
ft: ^- >i
f Radioactive Contaminants Deposited on Pasture Grass by
o
|
992. "Quantification of the Interception and Initial Reten
:3313to3321.
I. Thiessen, M.L. Frank, and E.G. Blaylock. 1
n." Atmospheric Environment. Vol. 26A. 18
>; •—
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gamma-emitting radionuclides and insoluble particles tagged
d field vegetation, including fescue) via simulated rain. The
5 product of Rp and Fw, as defined by this guidance:
| 05
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O rt ^
srmed "interception fraction," based on a study in which si
ture grass (specifically, a combination of fescues, clover, i
tercepted by vegetation and initially retained" or, essential
t developed values for a parameter (r) that it tf
mitting radionuclides were deposited onto pas
s defined as "the fraction of material in rain in
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1
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ge of 0.006 to 0.3 for anions (based on the sol
(0.08) observed in the study.
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luclide beryllium-7 [7Be]; when calcu
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micrometers, labeled with cerium- 141 [ l41Ce], [9SN]b,
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ing in diameter fron
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the geometric mean r value for IPM w
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. EPA (1994a) i
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TABLE B-3-2
PS
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PLANT CONCENTRATION DUE TO AIR-TO-PLANT TRA]
(TERRESTRIAL PLANT EQUATIONS)
nes that the variable c (the Junge constant) is constant for
ncentration for monolayer coverage, and the difference
3 9
(Page 5 of 5)
Ference for the statement that the equation used to calculate the fraction of air concentration in vapor phase (Fv) ass
however, this reference notes that the value of c depends on the chemical (sorbate) molecular weight, the surface <
leat of desorption from the particle surface and the heat of vaporization of the liquid-phase sorbate.
pa
to
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Interim Final Methodology for Assessing Health Risks Associated with Indirect Exposure to Combustor Emissioi
nd Development. EPA -600-90-003. January.
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t is a source of air density values.
c
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g
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OlTiceof Research and Development. EPA-600-AP-93-003. November 10.
fi "A
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this document recommends reducing, by a factor of 10,
or "made predictions [of beef concentrations] come in
«,- 3
npts to model background concentrations of dioxin-like compounds in beef on the basis of known air concentration
:ulated by using the Bacci, Cerejeira, Gaggi, Chemello, Calamari, and Vighi (1992) algorithm The use of this fa
rvations."
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^
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Washington, DC. EPA/600/6-88/005Cb. June.
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aste. December 14.
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RCRA Hazardous Waste Combustion Facilities. Office of Emergency and Remedial Response. Office of Solid
,
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APPENDIX C
MEDIA-TO-RECEPTOR BIOCONCENTRATION FACTORS (BCFs)
Screening Level Ecological Risk Assessment Protocol
August 1999
-------
Screening Level Ecological Risk Assessment Protocol
Appendix C; Media-To-Receptor BCF Values August 1999
APPENDIX C
TABLE OF CONTENTS
Section Page
C-1.0 GENERAL GUIDANCE C-l
C-l.l SOIL-TO-SOIL INVERTEBRATE BIOCONCENTRATION FACTORS C-2
C-1.2 SOIL-TO-PLANT AND SEDIMENT-TO-PLANT BIOCONCENTRATION
FACTORS C-2
C-l.3 WATER-TO-AQUATIC INVERTEBRATE BIOCONCENTRATION FACTORS C-3
C-l.4. WATER-TO-ALGAE BIOCONCENTRATION FACTORS C-4
C-1.5 WATER-TO-FISH BIOCONCENTRATION FACTORS C-4
C-l.6 SEDEMENT-TO-BENTfflC INVERTEBRATE BIOCONCENTRATION FACTORS C-5
C-l.7 AIR-TO-PLANT BIOTRANSFER FACTORS C-5
REFERENCES: APPENDIX C TEXT C-9
TABLES OF MEDIA-TO-RECEPTOR BCF VALUES C-13
REFERENCES: MEDIA-TO-RECEPTOR BCF VALUES C-99
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering C-i
-------
Screening Level Ecological Risk Assessment Protocol
Appendix C: Media-To-Receptor BCF Values August 1999
APPENDIX C
MEDIA-TO-RECEPTOR BCFs
Appendix C provides recommended guidance for determining values for media-to-receptor bioconcentration
factors (BCFs) based on values reported in the scientific literature, or estimated using physical and
chemical properties of the compound. Guidance on use of BCF values in the screening level ecological risk
assessment is provided in Chapter 5.
Section C-1.0 provides the general guidance recommended to select or estimate BCF values.
Sections C-l.l through C-1.7 further discuss determination of BCFs for specific media and receptors.
References cited in Sections C-l.l through C-1.7 are located following Section C-1.7.
For the compounds commonly identified in risk assessments for combustion facilities (identified in Chapter
2), BCF values have been determined following the guidance in Sections C-l.l through C-1.7. BCF values
for these limited number of compounds are included in this appendix in Tables C-l through C-7 to
facilitate the completion of screening ecological risk assessments. However, it is expected that additional
compounds may require evaluation on a site specific basis, and in such cases, BCF values for these
additional compounds could be determined following the same guidance (Sections C-l.l through C-1.7)
used in determination of the BCF values reported in this appendix. For reproducibility and to facilitate
comparison of new data and values as they become available, all data reviewed in the selection of the BCF
values provided at the end of this appendix are also included in Tables C-l through C-7. References cited
in Tables C-l through C-7 (Media-to-Receptor BCF Values) are located following Table C-7.
For additional discussion on some of the references and equations cited in Sections C-l.l through C-1.7,
the reader is recommended to review the Human Health Risk Assessment Protocol (HHRAP) (U.S. EPA
1998) (see Appendix A-3), and the source documents cited in the reference section of this appendix.
C-1.0 GENERAL GUIDANCE
This section summarizes the recommended general guidance for determining compound-specific BCF
values (media-to-receptors) provided in Tables C-l through C-7. As a preference, BCF values were
selected from empirical field and/or laboratory data generated from reviewed studies that are published in
the scientific literature. Information used from these studies included calculated BCF values, as well as,
collocated media and organism concentration data from which BCF values could be calculated. If two or
more BCF values, or two or more sets of collocated data, were available in the published scientific
literature, the geometric mean of the values was used.
Field-derived BCF values were considered more indicative of the level of bioconcentration occurring in the
natural environment than laboratory-derived values. Therefore, when available and appropriate,
field-derived BCF values were given priority over laboratory-derived values. In some cases, confidence in
the methods used to determine or report field-derived BCF values was less than for the laboratory-derived
values. In those cases, the laboratory-derived values were used for the recommended BCF values.
When neither field or laboratory data were available for a specific compound, data from a potential
surrogate compound were evaluated. The appropriateness of the surrogate was determined by comparing
the structures of the two compounds. Where an appropriate surrogate was not identified, a regression
equation based on the compound's log K^ value was used to calculate the recommended BCF value.
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering C-l
-------
Screening Level Ecological Risk Assessment Protocol
Appendix C; Media-To-Receptor BCF Values August 1999
With the exception of the air-to-plant biotransfer factors (Bv), recommended BCF values provided in the
tables at the end of this appendix are based on wet tissue weight and dry media weight (except for water).
As necessary, reported values were converted to these units using the referenced tissue or media wet weight
percentages. The conversion factors, equations, and references for these conversions are discussed in
Sections C-l.l through C-1.7 where appropriate, and are presented at the end of each table (Tables C-l
through C-7).
C-l.l SOIL-TO-SOIL INVERTEBRATE BIOCONCENTRATION FACTORS
Soil-to-soil invertebrate BCF values (see Table C-l) were developed mainly from data for earthworms.
Measured experimental results were primarily in the form of ratios of compound concentrations in a
earthworm and the compound concentrations in the soil in which the earthworm was exposed. As
necessary, values were converted to wet tissue and dry media weight assuming a moisture content (by
mass) of 83.3 percent for earthworms and 20 percent for soil (Pietz et al. 1984).
Organics For organic compounds with no field or laboratory data available, recommended BCF values
were estimated using the following regression equation:
log BCF= 0.819 log Km -1.146 Equation C-l-1
• Southworth, G.R., J.J. Beauchamp, and P.K. Schmieder. 1978. "Bioaccumulation
Potential of Polycyclic Aromatic Hydrocarbons in Daphnia Pulex." Water Research.
Volume 12. Pages 973-977.
Inorganics For inorganic compounds with no field or laboratory data available, the recommended BCF
value is equal to the arithmetic average of the available BCF values for other inorganics as specified in
Table C-l.
C-1.2 SOIL-TO-PLANT AND SEDIMENT-TO-PLANT BIOCONCENTRATION FACTORS
Soil-to-plant BCF values (see Table C-2) account for plant uptake of compounds from soil. Data for a
variety of plants and food crops were used to determine recommended BCF values.
Organics For all organics (including PCDDs and PCDFs) with no available field or laboratory data, the
following regression equation was used to calculate recommended values:
log BCF = 1.588 - 0.578 log K^ Equation C-l-2
• Travis, C.C. and A.D. Anns. 1988. "Bioconcentration of Organics in Beef, Milk, and
Vegetation." Environmental Science and Technology. 22:271-274.
Inorganics For most metals, BCF values were based on empirical data reported in the following:
• Baes, C.F., R.D. Sharp, A.L. Sjoreen, and R.W. Shor. 1984. "Review and Analysis of
Parameters and Assessing Transport of Environmentally Released Radionuclides Through
Agriculture." Oak Ridge National Laboratory, Oak Ridge, Tennessee.
The scientific literature also was searched to identify studies. Although U.S. EPA (1995a) provides values
for certain metals calculated on the basis of plant uptake response slope factors, it is unclear how the BCF
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering C-2
-------
Screening Level Ecological Risk Assessment Protocol
Appendix C; Media-To-Receptor BCF Values August 1999
values were calculated or which sources or references were used. Therefore, values reported in
U.S. EPA (1995a) were not used.
C-1.3 WATER-TO-AQUATIC INVERTEBRATE BIOCONCENTRATION FACTORS
Experimental data for crustaceans, aquatic insects, bivalves, and other aquatic invertebrates were used to
determine recommended BCF values for water-to-aquatic invertebrate (see Table C-3). Both marine and
freshwater exposures were reviewed. As necessary, available results were converted to wet tissue weight
assuming that invertebrate moisture content (by mass) is 83.3 percent (Pietz et al. 1984).
Orsanics Reported field values for organic compounds were assumed to be total compound concentrations
in water and, therefore, were converted to dissolved compound concentrations in water using the following
equation from U.S. EPA (1995b):
BCF (dissolved) = (BCF (total) / fffl) - 1 Equation C-l-3
where
BCF (dissolved) = BCF based on dissolved concentration of compound in
water
BCF (total) = BCF based on the field derived data for total
concentration of compound in water
jja = Fraction of compound that is freely dissolved in the water
and,
ft, = l/[l + ((DOCxKow)/10) + (POCxKow)]
DOC = Dissolved organic carbon, kilograms of organic carbon /
liter of water (2.0 x 10^* Kg/L)
Km = Octanol-water partition coefficient of the compound, as
reported in U.S. EPA (1994a)
POC = Paniculate organic carbon, kilograms of organic carbon /
liter of water (7.5 x lO"09 Kg/L)
Laboratory data were assumed to be based on dissolved compound concentrations.
For organic compounds with no field or laboratory data available, BCF values were determined from
surrogate compounds or calculated using the following regression equation:
log BCF = 0.819 x log KoW - 1.146 Equation C-l-4
• Southworth, G.R., J.J. Beauchamp, and P.K. Schmieder. 1978. "Bioaccumulation
Potential of Polycyclic Aromatic Hydrocarbons in Daphnia Pulex." Water Research.
Volume 12. Pages 973-977.
Inorganics For inorganic compounds with no field or laboratory data available, the recommended BCF
values were estimated as the arithmetic average of the available BCF values for other inorganics, as
specified in Table C-3.
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering C-3
-------
Screening Level Ecological Risk Assessment Protocol
Appendix C; Media-To-Receptor BCF Values August 1999
C-1.4 WATER-TO-ALGAE BIOCONCENTRATION FACTORS
Experimental data for both marine and freshwater algal species were reviewed. As necessary, available
results were converted to wet tissue weight assuming that algae moisture content (by mass) is 65.7 percent
(Isensee et al. 1973).
Organics For organic compounds with no field or laboratory data available, BCF values were calculated
using the following regression equation:
log BCF = 0.819 x log K™ -1.146 Equation C-l-5
• Southworth, G.R., J.J. Beauchamp, and P.K. Schmieder. 1978. "Bioaccumulation
Potential of Polycyclic Aromatic Hydrocarbons in Daphnia Pulex." Water Research.
Volume 12. Pages 973-977.
Inorganics For inorganics, available field or laboratory data were evaluated for each compound.
C-1.5 WATER-TO-FISH BIOCONCENTRATION FACTORS
Experimental data for a variety of marine and freshwater fish were used to determine recommended BCF
values (see Table C-5). As necessary, values were converted to wet tissue weight assuming that fish
moisture content (by mass) is 80.0 percent (Holcomb et al. 1976).
For both organic and inorganic compounds, reported field values were considered bioaccumulation factors
(BAFs) based on contributions of compounds from food sources as well as media. Therefore, field values
were converted to BCFs based on the trophic level of the test organism using the following equation:
BCF = (BAF^ I FCMjjJ - 1 Equation C-l-6
where
= The reported field bioaccumulation factor for the trophic level "n"
of the study species.
, = The food chain multiplier for the trophic level "n" of the study
species.
Organics Reported field values for organic compounds were assumed to be total compound concentrations
in water and, therefore, were converted to dissolved compound concentrations in water using the following
equation from U.S. EPA (1995b):
BAF(dissolved) = (BAF(total) lffd) -1 Equation C-l-7
where
BAF (dissolved) = BAF based on dissolved concentration of compound in
water
BAF (total) = BAF based on the field derived data for total
concentration of compound in water
ffd = Fraction of compound that is freely dissolved in the water
and,
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering C-4
-------
Screening Level Ecological Risk Assessment Protocol
Appendix C; Media-To-Receptor BCF Values August 1999
fju = 1 / [1 + ((DOC x K^) / 10) + (POC x K.J]
DOC = Dissolved organic carbon, Kg of organic carbon / L of
water (2.0 x lO"06 Kg/L)
Kow = Octanol-water partition coefficient of the compound, as
reported in U.S. EPA (1994a)
POC = Paniculate organic carbon, Kg of organic carbon / L of
water (7.5 x lO"09 Kg/L)
Laboratory data were assumed to be based on dissolved compound concentrations.
For organics for which no field or laboratory data were available, the following regression equation was
used to calculate the recommended BCF values:
log BCF = 0.91 x log K^ -1.975 x log (6.8E-07 x K^ + 1.0) - 0.786 Equation C-l-8
• Bintein, S., J. Deviflers, and W. Karcher. 1993. "Nonlinear Dependence of Fish
Bioconcentrations on n-Octanol/Water Partition Coefficients." SAR and QSAR in
Environmental Research. Vol.1. Pages 29-39.
Inorganics For inorganic compounds with no available field or laboratory data, the recommended BCF
values were estimated as the arithmetic average of the available BCF values reported for other inorganics.
C-1.6 SEDEMENT-TO-BENTHIC INVERTEBRATE BIOCONCENTRATION FACTORS
Experimental data for a variety of benthic infauna, worms, insects, and other invertebrates were used to
determine the recommended BCF values for sediment-to-benthic invertebrate (see Table C-6). As
necessary, values were converted to wet tissue weight assuming that benthic invertebrate moisture content
(by mass) is 83.3 percent (Pietz et al. 1984).
Orsanics For organic compound (including PCDDs and PCDFs) with no available field or laboratory
data, the recommended BCF values were determined using the following regression equation:
log BCF = 0.819 x log K^ - 1.146 Equation C-l-9
• Southworth, G.R., J.J. Beauchamp, and P.K. Schmieder. 1978. "Bioaccumulation
Potential of Polycyclic Aromatic Hydrocarbons in Daphnia Pulex." Water Research.
Volume 12. Pages 973-977.
Inorganics For inorganic compound with no available field or laboratory data, the recommended BCF
values were estimated as the arithmetic average of the available BCF values for other inorganics.
C-1.7 AIR-TO-PLANT BIOCONCENTRATION FACTORS
The air-to-plant bioconcentration (Bv) factor (see Table C-7) is defined as the ratio of compound
concentrations in exposed aboveground plant parts to the compound concentration in air. Bv values in
Table C-7 are reported on dry-weight basis since the plant concentration equations (see Chapter 3) already
include a dry-weight to wet-weight conversion factor.
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering C-5
-------
Screening Level Ecological Risk Assessment Protocol
Appendix C; Media-To-Receptor BCF Values
August 1999
Oreanics For organics (excluding PCDDs and PCDFs), the air-to-plant bioconcentration factor was
calculated using regression equations derived for azalea leaves in the following documents:
• Bacci E., D. Calamari, C. Gaggj, and M. Vighi. 1990. "Bioconcentration of Organic
Chemical Vapors in Plant Leaves: Experimental Measurements and Correlation."
Environmental Science and Technology. Volume 24. Number 6. Pages 885-889.
Bacci E., M. Cerejeira, C. Gaggi, G. Chemello, D. Calamari, and M. Vighi. 1992.
"Chlorinated Dioxins: Volatilization from Soils and Bioconcentration in Plant Leaves."
Bulletin of Environmental Contamination and Toxicology. Volume 48. Pages 401-408.
Bacci et al. (1992) developed a regression equation using empirical data collected for the uptake of
1,2,3,4-TCDD in azalea leaves and data obtained from Bacci et al. (1990). The bioconcentration factor
obtained was included in a series of 14 different organic compounds to develop a correlation equation with
Kg* and H (defined below). Bacci et al. (1992) derived the following equations:
log Bvol = 1.065 log Kow - log
;—) - 1.654
RT
(r = 0.957) Equation C-l-10
Bv =
Pair •
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orage
where
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1.19g/L(Weastl986)
770 g/L (Macrady and Maggard 1993)
0.85 (fraction of forage that is water—Macrady and Maggard
[1993])
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Universal gas constant (atm-nrVmole °K)
Temperature (25 °C, 298 °K)
Equations C-l-10 and C-l-11 are used to calculate Bv values (see Table C-7) using the recommended
values of H and Kow provided in Appendix A at a temperature (T) of 25 °C or 298.1 K. The following
uncertainty should be noted with use of Bv values calculated using these equations:
U.S. EPA Region 6
Multimedia Planning and Permitting Division
Center for Combustion Science and Engineering
U.S. EPA
Office of Solid Waste
C-6
-------
Screening Level Ecological Risk Assessment Protocol
Appendix C; Media-To-Receptor BCF Values August 1999
• For organics (except PCDDs and PCDFs), U.S. EPA (1993) recommended that Bv values
be reduced by a factor of 10 before use. This was based on the work conducted by U.S.
EPA (1993) for U.S. EPA (1994b) as an interim correction factor. Welsch-Pausch,
McLachlan, and Umlauf (1995) conducted experiments to determine concentrations of
PCDDs and PCDFs in air and resulting biotransfer to welsh ray grass. This was
documented in the following:
Welsch-Pausch, K.M. McLachlan, and G. Umlauf. 1995. "Determination of the
Principal Pathways of Polychlorinated Dibenzo-p-dioxins and Dibenzofurans to
Lolium Multiflorum (Welsh Ray Grass)". Environmental Science and
Technology. 29: 1090-1098.
A follow-up study based on Welsch-Pausch, McLachlan, and Umlauf (1995) experiments
was conducted by Lorber (1995) (see discussion below for PCDDs and PCDFs). In a
following publication, Lorber (1997) concluded that the Bacci factor reduced by a factor
of 100 was close in line with observations made by him through various studies, including
the Welsch-Pausch, McLachlan, and Umlauf (1995) experiments. Therefore, this
guidance recommends that Bv values be calculated using the Bacci, Cerejeira, Gaggi,
Chemello, Calamari, and Vighi (1992) correlation equations and then reduced by a factor
of 100 for all organics, excluding PCDDs and PCDFs.
PCDDs and PCDFs For PCDDs and PCDFs, Bv values, on a dry weight basis, were obtained from the
following:
• Lorber, M., and P. Pinsky. 1999. "An Evaluation of Three Empirical Air-to-Leaf Models
for Polychlorinated Dibenzo-p-Dioxins and Dibenzofurans." National Center for
Environmental Assessment (NCEA). U. S. EPA, 401 M St. SW, Washington, DC.
Accepted for Publication in Chemosphere.
U.S. EPA (1993) stated that, for dioxin-like compounds, the use of the Bacci, Cerejeira, Gaggi, Chemello,
Calamari, and Vighi (1992) equations may overpredict Bv values by a factor of 40. This was because the
Bacci, Calamari, Gaggi, and Vighi (1990) and Bacci, Cerejeira, Gaggi, Chemello, Calamari, and Vighi
(1992) experiments did not take photodegradation effects into account. Therefore, Bv values calculated
using Equations C-10 and C-l 1 were recommended to be reduced by a factor of 40 for dioxin-like
compounds.
However, according to Lorber (1995), the Bacci algorithm divided by 40 may not be appropriate because
(1) the physical and chemical properties of dioxin congeners are generally outside the range of the 14
organic compounds used by Bacci, Calamari, Gaggi, and Vighi (1990), and (2) the factor of 40 derived
from one experiment on 2,3,7,8-TCDD may not apply to all dioxin congeners.
Welsch-Pausch, McLachlan, and Umlauf (1995) conducted experiments to obtain data on uptake of
PCDDs and PCDFs from air to Lolium Multiflorum (Welsh Ray grass). The data includes grass
concentrations and air concentrations for dioxin-congener groups, but not the invidual congeners. Lorber
(1995) used data from Welsch-Pausch, McLachlan, and Umlauf (1995) to develop an air-to-leaf transfer
factor for each dioxin-congener group. Bv values developed by Lorber (1995) were about an order of
magnitude less than values that would have been calculated using the Bacci, Calamari, Gaggi, and Vighi
(1990; 1992) correlation equations. Lorber (1995) speculated that this difference could be attributed to
several factors including experimental design, climate, and lipid content of plant species used.
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering C-7
-------
Screening Level Ecological Risk Assessment Protocol
Appendix C; Media-To-Receptor BCF Values August 1999
Lorber (1999) conducted an evaluation of three empirical air-to-leaf models for estimating grass
concentraions of PCDDs and PCDFs from air concentrations of these compounds described and tested
against field data. Bv values recommended for PCDDs and PCDFs in this guidance were obtained from the
experimentally derived values of Lorber (1999).
Metals For metals, no literature sources were available for Bv values. U.S. EPA (1995a) quoted from the
following document, that metals were assumed not to experience air to leaf transfer:
• Belcher, G.D., and C.C. Travis. 1989. "Modeling Support for the RURA and Municipal
Waste Combustion Projects: Final Report on Sensitivity and Uncertainty Analysis for the
Terrestrial Food Chain Model." Interagency Agreement No. 1824-A020-A1. Office of
Risk Analysis, Health and Safety Research Division. Oak Ridge National Laboratory.
Oak Ridge, Tennessee. October.
Consistent with the above references, Bv values for metals (excluding elemental mercury) were assumed to
be zero (see Table C-7).
Mercuric Compounds Mercury emissions are assumed to consist of both the elemental and divalent
forms. However, only small amounts of elemental mercury is assumed to be deposited (see Chapter 2).
Elemental mercury either dissipates into the global cycle or is converted to the divalent form. Methyl
mercury is assumed not to exist in the stack emissions or in the air phase. Consistent with various
discussions in Chapter 2 concerning mercury, (1) elemental mercury reaching or depositing onto the plant
surfaces is negligible, and (2) biotransfer of methyl mercury from air is zero. This is based on assumptions
made regarding speciation and fate and transport of mercury from stack emissions. Therefore, the Bv value
for (1) elemental mercury was assumed to be zero, and (2) methyl mercury was assumed not to be
applicable. Bv values for mercuric chloride (dry weight basis) were obtained from U.S. EPA (1997).
It should be noted that uptake of mercury from air into the aboveground plant tissue is primarily in the
divalent form. A part of the divalent form of mercury is assumed to be converted to the methyl mercury
form once in the plant tissue.
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering C-8
-------
Screening Level Ecological Risk Assessment Protocol
Appendix C; Media-To-Receptor BCF Values August 1999
Bacci E., D. Calamari, C. Gaggi, and M. Vighi. 1990. "Bioconcentration of Organic Chemical Vapors
in Plant Leaves: Experimental Measurements and Correlation." Environmental Science and
Technology. Volume 24. Number 6. Pages 885-889.
Bacci E., M. Cerejeira, C. Gaggi, G. Chemello, D. Calamari, and M. Vighi. 1992. "Chlorinated Dioxins:
Volatilization from Soils and Bioconcentration in Plant Leaves." Bulletin of Environmental
Contamination and Toxicology. Volume 48. Pages 401-408.
Baes, C.F., R.D. Sharp, A.L. Sjoreen, and R.W. Shor. 1984. "Review and Analysis of Parameters and
Assessing Transport of Environmentally Released Radionuclides through Agriculture." Oak Ridge
National Laboratory. Oak Ridge, Tennessee.
Belcher, G.D., and C.C. Travis. 1989. "Modeling Support for the RURA and Municipal Waste
Combustion Projects: Final Report on Sensitivity and Uncertainty Analysis for the Terrestrial
Food Chain Model." Interagency Agreement No. 1824-A020-A1. Office of Risk Analysis, Health
and Safety Research Division. Oak Ridge National Laboratory. Oak Ridge, Tennessee. October.
Bintein, S., J. Devillers, and W. Karcher. 1993. "Nonlinear Dependence of Fish Bioconcentrations on n-
Octanol/Water Partition Coefficients." SAR and QSAR in Environmental Research. Vol. 1.
Pages 29-39.
Holcombe, G.W., D.A. Benoit, E.N. Leonard, and J.M. McKim, 1976. "Long-term Effects of Lead
Exposure on Three Generations of Brook Trout (Salvenius fontinalis)." Journal, Fisheries
Research Board of Canada. Volume 33. Pages 1731-1741.
Isensee, A.R., P.C. Kearney, E.A. Woolson, G.E. Jones, and V.P. Williams. 1973. "Distribution of
Alkyl Arsenicals in Model Ecosystems." Environmental Science and Technology. Volume 7,
Number 9. Pages 841-845.
Lorber, M. 1995. "Development of an Air-to-plant Vapor Phase Transfer for Dioxins and Furans.
Presented at the 15th International Symposium on Chlorinated Dioxins and Related Compounds".
August 21-25, 1995 in Edmonton, Canada. Abstract in Organohalogen Compounds.
24:179-186.
Lorber, M., and P. Pinsky. 1999. "An Evaluation of Three Empirical Air-to-Leaf Models for
Polychlorinated Dibenzo-p-Dioxins and Dibenzofurans." National Center for Environmental
Assessment (NCEA). U. S. EPA, 401 M St. SW, Washington, DC. Accepted for Publication in
Chemosphere.
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering C-9
-------
Screening Level Ecological Risk Assessment Protocol
Appendix C; Media-To-Receptor BCF Values August 1999
McCrady, J.K., S.P. Maggard. 1993. "Uptake and Photodegradation of
2,3,7,8-Tetrachlorodibenzo-p-dioxin Sorbed to Grass Foliage." Environmental Science and
Technology. 27:343-350.
Pietz, R.I., J.R. Peterson, J.E. Prater, and D.R. Zenz. 1984. "Metal Concentrations in Earthworms From
Sewage Sludge-Amended Soils at a Strip Mine Reclamation Site." J. Environmental Qual.
Vol. 13, No. 4. Pp 651-654.
Southworth, G.R., J.J. Beauchamp, and P.K. Schmieder. 1978. "Bioaccumulation Potential of Polycyclic
Aromatic Hydrocarbons in Daphnia Pulex." Water Research. Volume 12. Pages 973-977.
Travis, C.C., and A.D. Arms. 1988. "Bioconcentration of Organics in Beef, Milk, and Vegetation."
Environmental Science and Technology. 22:271-274.
U.S. EPA. 1993. Review Draft Addendum to the Methodology for Assessing Health Risks Associated
with Indirect Exposure to Combustor Emissions. Office of Health and Environmental
Assessment. Office of Research and Development. EPA-600-AP-93-003. November 10.
U.S. Environmental Protection Agency (U.S. EPA). 1994a. Draft Report Chemical Properties for Soil
Screening Levels. Prepared for the Office of Emergency and Remedial Response. Washington,
D.C. July 26.
U.S. EPA. 1994b. Estimating Exposure to Dioxin-Like Compounds. Draft Report. Office of Research
and Development. Washington, D.C. EPA/600/6-88/005Ca,b,c. June.
U.S. EPA. 1995a. Review Draft Development of Human Health-Based and Ecologically-Based Exit
Criteria for the Hazardous Waste Identification Project. Volumes I and JJ. Office of Solid
Waste. March 3.
U.S. EPA. 1995b. Great Lakes Water Quality Initiative Technical Support Document for the Procedure
to Determine Bioaccumulation Factors. EPA-820-B-95-005. Office of Water, Washington, D.C.
March.
U.S. EPA. 1997. Mercury Study Report to Congress, Volumes I through VIII. Office of Air Quality
Planning and Standards and ORD. EPA/452/R-97-001. December.
U.S. EPA. 1998. Human Health Risk Assessment Protocol for Hazardous Waste Combustion Facilitites.
External Peer Review Draft. U.S. EPA Region 6 and U.S. EPA OSW. Volumes 1-3.
EPA530-D-98-001A. July.
Veith, G.D., K.J. Macek, S.R. Petrocelli, and J. Carroll. 1980. "An Evaluation of Using Partition
Coefficients and Water Solubility to Estimate Bioconcentration Factors for Organic Chemicals in
Fish." Pages 116-129. In J. G. Eaton, P. R. Parrish, and A. C. Hendricks (eds.), Aquatic
Toxicology. ASTM STP 707. American Society for Testing and Materials, Philadelphia.
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering C-10
-------
Screening Level Ecological Risk Assessment Protocol
Appendix C; Media-To-Receptor BCF Values August 1999
Welsch-Pausch, K.M. McLachlan, and G. Umlauf. 1995. "Determination of the Principal Pathways of
Polychlorinated Dibenzo-p-dioxins and Dibenzofurans to Lolium Multiflorum (Welsh Ray Grass)".
Environmental Science and Technology. 29: 1090-1098.
Weast, R.C. 1986. Handbook of Chemistry and Physics. 66th Edition. Cleveland, Ohio. CRC Press.
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering C-l 1
-------
Screening Level Ecological Risk Assessment Protocol
Appendix C: Media-To-Receptor BCF Values August 1999
MEDIA-TO-RECEPTOR BCF VALUES
Screening Level Ecological Risk Assessment Protocol
August 1999
C-l SOIL-TO-SOIL INVERTEBRATE BIOCONCENTRATION FACTORS C-15
C-2 SOIL-TO-PLANT AND SEDIMENT-TO- PLANT BIOCONCENTRATION
FACTORS C-29
C-3 WATER-TO-AQUATIC INVERTEBRATE BIOCONCENTRATION FACTORS ... C-36
C-4 WATER-TO-ALGAE BIOCONCENTRATION FACTORS C-54
C-5 WATER-TO-FISH BIOCONCENTRATION FACTORS C-66
C-6 SEDEMENT-TO-BENTfflC INVERTEBRATE BIOCONCENTRATION
FACTORS C-85
C-7 AIR-TO-PLANT BIOTRANSFER FACTORS C-96
REFERENCES C-99
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering C-13
-------
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TABLE C-1
JRATE BIOCONCENTRATION F
et tissue) / (mg COPC/kg dry soil)
(Page 6 of 14)
NH i
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Experimental Parameters
References
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for a structurally-sir
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or for a structurally-
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i (U.S. EPA 1994b).
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TABLE C-1
KTEBRATE BIOCONCENTRATION
:/kg wet tissue) / (mg COPC/kg dry soil
(Page 8 of 14)
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s 1
11
available for carbon tetri
<„„ - 1.146 (Southworth,
tH OO
0 0
s —
=a **
ra ^
- »
"3 d
•c "
o CC
0 00
Z. .2
VD
O\
i5
"3
U
n
•g
T3
g
a
g
o
achlorobenzene
X
K
•y
3
O
C
1
C
o
1
u
c
_o
CO
OO
2
1?
j
i2
U
.S
•3
1
imilar surrogate compound. The BCF was calcul
978), where log K^, = 5.503 (U.S. EPA 1994b).
CO »— <
structurally-
Schmieder
T3
S |
§1
i §
c u
^ CQ
available for hexachloro
K,,,, - 1.146 (Southworth,
^ oo
& -^
"ca ^
— °°
"3 d
•n ii
1 pa
o oo
Z 2
*o
en
u
3
"3
tt,
O
09
•o
§
g
g
0
achlorobutadiene
X
u
EC
•a
c
3
g
O
U
c
_o
!
£
.2
*co
en
O
60
c
1
Ig
u
J3
00
'S
3
1
JS
^
-similar surrogate compound. The BCF was calci
978) where log K^, = 4.731 (U.S. EPA 1994b).
i structural!;
Schmieder
~ -o
a §
g $
u 5
ll
•3 i
3 «
J CQ
available for hexachloro
KDW- 1.1 46 (Southworth,
1- Ol
^ "**
« !x:
*- ON
"° OC
"« o
:^i
§ cc
J*
U
"3
B
CQ
•a
u
1
C
8
:achlorocyclopentadiene
K
(U
p~*
•y
c
3
0
Q.
1
U
g
3
3
cy
u
'«
CA
K
00
00
'1
JD
1
1
00
*co
3
T3
3
•3
o
•3
u
Cfl
turally-similar surrogate compound. The BCF wa
1978), where log K^ = 4.907 (U.S. EPA 1994b).
CJ ^^
or for a strui
Schmieder
X
*S3
«
*2
ni
r *.
0
t-^
Q
tig the geometric mean of 13 laboratory values for
ight using a conversion factor of 5.99a.
.»* u
alculated us
over dry wi
0 V
BCF was
wet weigl
J3 -2
P "8
DDE were not available.
3ish (1980) were conver
^ . "Q
~- C
"^r rt
O flj
.,
« u
-a TJ
5 ca
:s i?
a, t-~
g 2
W C-
1
c2
fc
1
.S
'C
1
Chronic exposure
Davis (1971)
o\ —
d d
oo o\
O C-.
d d
-------
cc
PS
B
U
<
fe
^ s^
ll
H -^
3 ^
^1 >H
TABLE C-1
ATE BIOCONCENTR
tissue) / (mg COPC/kg <
Page 9 of 14)
& ~ -
M V
w s
w *
H Sf
OS <£
(3 U
z" o
HH r *i
iJ ec
^•4 M
8^
6
H
j
0
t»
w
_!
"5
v.
|
a
Experimental P,
eferences
A
"«
u
9
"e3
>•
•o
w
I*
O
p;
s
W
S
Aporrectodea trapezoides
Aparrectodea turgida
Allolobophora chlorotica
Lumbricus terrestris
hronic exposure
U
ON
f— <
'Xrf'
•9
5
1
8
>-.
o
n
f>
00
d
Not specified
hronic exposure
U
/— N
OO
vo
CN
la
•a
§
£
to
0>
£
o o o
(N VO >O
— Tt — '
in O O
oo •*<•
£
Svo
^r
O rfj
o
•*
— ;
u
Recommended BCF Valu
eptachlor
E
-o
c
D
O
o,
o
O
to wet
•o
u
S
^
c
o
o
in Beyer and Gish (1980) was
*o
c
I
1M
u
3
"3
>
u
o
•o
.tory value for heptachlor epo>
ra
|
•O
J2
—
00
C
"oo
S
1
JS
3
BCF was calc
99".
liable. The
factor of 5.'
5 e
£ .2
ll
M
> C3
g g>
l!
ex -^
u oo
-= •«
^ >•
^5 ?
<*" >,
s £
M ^
•o S
S °
13 £
£X M
S w
a &
Aporrectodea trapezoides
Aparrectodea turgida
Allolobophora chlorotica
Lumbricus terrestris
hronic exposure
U
y^S
8
2
tn
5
T3
i
u
n
o
•*
o
t--
<*„
8
u
Recommended BCF Valu
S
1
1
2
u
03
S
ac
-b
c
3
O
tx
1
U
wing regression equation:
0
2
1
00 ^
.g vi
3 2
1 «
•2 R
g J
— -a
3 ^
U CB
ate compound. The BCF was
re log K™ = 7.540 (Karickoff
bo o
s •§
5
H gf
— 0\
1?
i*^
ll
or for a struct
:hamp, and Sc
II
f™
H
J3 O
s I
x -S
U 3
-C 0
£ S£
« yo
jj -q-
X) *~i
_« -^
03 J^
O
1— CD
> .2
« x
P3
*-t {•*.
C3 2
•° x
It
C "
"5, Q-i
g U
u CQ
O OC
2 ^
Inorganics
S
d
T3
« S
minum \v
copper, I
-i E
u. 3
O "c
<•-' E
S S
ta j:
T3 0
"S E
tl
II
fM
oo
S g
o!
§1
:imony wi
copper, I
1 E
>-, 3
o "5
<" C
5 8
a x>
"O o
"3 p"
rj C
1 1
11
,— *
,— i
d
i>
Recommended BCF Valu
_0
"H
u
tn
-5
T3
C
D
a
i
-------
x
o
H
u
^j
ta
51
M !*>
< •«
e »
fig
- H sr
i CJ IT ^
w ol -g
N S ^L o
J qj" »H
flfi u *i cu
< H « UD
fid ^^ ^^*
^2 4>
MH jk.
W ^
If
^^. C^
z o
.. w
M ^
o S
W5 ^"^
6
H
J
S
J
"S
a,
cfl
i
'S
i
1
Experimental 1
Reference:
eft
1
~a
^-
•8
O
D.
«
N
b*
s
£
00
1
Si
?
o
"u
0
1
00
00
ON
J
•o
h«
g
g
53
u
•S
1
elow. The values repoi
i
•-H
e«
o3
O
"5
<§
u
_p3
C3
C*
I
V!
O
g
u
E •
ca
O A
•S Oi
fi ON
« in
8»
| 1
ulated using
conversion !
u &
~a so
u c
s 3
0. •§)
iC b1
P -8
Eisenia foetida
exposure
"V
00
id Lee (1988
§
•>
u.
55
•f
u
s
o r^
d d
2 2 o
d d d
"3
n
Recommended
Barium
•o
c
3
O
O,
1
U
g"
"E
•o
IS
u
(S
'S
u
cn
O
1
'3
empirical data <
C1
TJ
§'"
oo
}M
O
C
U
cn
1
Ui
£
cn
U
f the recommended val
o
Sea
o
'£3
H
1
o
5
cn
B-
U
03
•s
recommends
and zinc).
o 73
E *^
" .y
o 1
is
> o
* 6
|!
|-i
3 ju
^ 1^
i i
•a
*C3 C
U 3
'.5 5
£ !
UJ 13
tN
tN
d
o
°3
a-,
U
CO
Recommended
Beryllium
•y
c
1
o
rj
o
'E
CA
c3
u
3
ca
"3
ca
th empirical dai
*!T
cn
ca
o1
.£
u
cn
O
J3
1
U
>
i of the recommended '
a
u
o
*s
u
1
W
P"\
no ^
.S
'S 4^1
"O g
be recommei
iry, nickel, a
*"* S
d>
4> G
1|
03 03
> op
o §
C •"*
g «"
beryllium w
nn, copper, 1
^ 3
<2 E
ca o
"3 ^
T3 O
g--|
W o
VO
ON
d
u
3
•3
B.
U
Recommended
Cadmium
•6
c
§
&
|
U
u
>
/— V
cn
00
ON
u
J
•g
ca
"S
id Simmers, Rhi
K
OO
00
c
u
J
•a
G
ed
w
E
E
5i
'alues reported in Rhett
i*-
U
•
B
3
'g
T3
ca
u
l-t
cS
S ON
3 ON
•3 uS
> (M
£* bi
Q O
of 22 labora
nversion fac
g 8
u ca
E oo
o .£
•S S
Si
o .op
oo S£
0 *
.sf
3 O
•0 —
4i iM
« .SP
3 ^
^ s
"3 •?;
0 g
cn >
> °
Bl
oa S
£i
H 8
Eisenia foetida
exposure
i?
•a
00
o
a
S
£
tN ON m w^
o o o o
cn »r> c^ o
O O CO O
« *
g '$
S <*>
•^ *u
% ^ &
a, c o s -r s
! l> | j -g | §
1
u
1
U
^^
00
2
u
^
1
4J-
t>
S
E
E
5>
O t^ ^O t*~ v> O O
in r~ OO NO ON »/^ <—
O oc r^ NO m — ' fN
co ON m r- •— ^* ON
<-< (N CM «-< --< o cn
O O — > O O 00 •*
o
d
u
3
"3
B
pa
Recommended
,_^
"3
S
Chromium
•o
c
3
O
n.
o
U
oo
'o
•S
•o
U|
>
0
1
'53
£
I
n
ere converted t<
>
00
00
c
0
1-1
"g
1
cn"
E
E
55
I
•a
u
1
cn
U
J3
"3
1
E
3
'g
1
U
g
<*.
O
3
CO
^
£*
1
?
g
U
E
u
•fi
u
1
00
0 .•
« a
ulated using
[factor of 5.<
0 S3
•3 .2
CC fl>
ca >
j c
& 8
pa M
a .s
H 3
-------
I
H
fa
Z S
TABLE C-l
IRATE BIOCONCENTRATIO
et tissue) / (mg COPC/kg dry so
(Page 11 of 14)
3 *
H M
W U
^^ C^
Z 0
^•* ^^
N-9 OJD
ol
i
o
H
S
en
GQ
«
a,
£
«u
Experimental Parameti
g
1
«
"
tt.
U
«
•o
u
•a
B
U
H
8
(2
fcn
(U
o«
o
U
•a
c
1
1
00
"S
^
"S
o
n
'S
^
0
o
•o
^
u
o
u
i£
oo"
00
^,
"O
m
The values reported in Rhett, Simmers, i
^
g-
u
g
CQ
3
•a
^
O
1
1
"o
c
CO
0>
S
u
1
§
••* t(-H
I I
-£i o
•3-f
•a1.!
O CO
i >
? c
u, S
U Cd
m oo
D _C
1
O O CS O
d d d d
.3
1
*J»
-^
•3
Chronic exposure
^
00
CT\
cd
d
-------
u
s
CO
<
H
M
TH
H
V
o.
ce
I
su
3
s
a
n
I
i
a*
1
^
dJ
tS
O
i
(N
•-'
0
"3
CM
U
CQ
Recommended
1
1
u"
T3
Compoun
E"
E
T3
ia
u
o"
'£
u
CO
5-
U
3
BJ
'3
cd
:h empirical data
.a
S
c
'i
o
•3
1
M
"e3
1
•o
c
tic mean of the recomme
u
«
Jt
•2 T3
&(2
ra
n^-
ai
T) J2
-8 -1
if
l|
ii"
.,- s
were not available
lorganic mercury, i
^ *—
"O "^.
"c *o
rt rt
>» J^
O
g S3"
rt Cli
•a "
Empirical
chromiuin
S
d
u
_3
"3
J>
BU
U
CQ
Recommended
cd
J
•a
Compoun
2
•a
•g
u
e
o
u
S
u
£
^^,
J^
ON
^^
1
e
C3
•§
IS
00
IS
S
0?
00
o\
5
•o
I
g
1
„
te values reported in Rhe
S
"i
"s
5
CQ
>>
1
II
<" IN
2
C O
Sod
ta o
IThe BCF
wet weigh
Eiseniafoetida
28-day exposure
oo
00
o\
•a
§
S3
E
VO
CN O r-
O O O
odd
Not specified
Chronic exposure
Ma (1987)
o\
d
Not specified
oo
o\
IS
CM
d
Alabophera sp.
Lumbricus sp.
Octolasium sp.
Chronic exposure
^
ON
N-"
1
1
en
O
d
s
d
o
3
"3
tt.
Recommended
ric chloride
3
I
•ii
Compoun
1-
S3
i,
'S
*-
(U
?
2
T3
1988) were conv
and Lee (
2"
e
V)
i
g
t>
Q
O.
; chloride. The values re
1
«3
1
JM
CQ
^3
1
o
I
3
V)
•s
u
E
sing the geometric
factor of 5.99*.
3 S
"S -I
"3 g
^— o
CO (J
KJ OJ)
^ C
IThe BCF
weight us:
Eiseniafoetida
8 |
1^1 "s
O £
d « «
\/ o
... uT o
^ > u
111
•g co" "^
0 -2 "§
8 g g .
28-day exposure; tissue
reported for the first thi
concentration of 0.05 w
conservative BCF valui
00
00
o\
u
•g
§
0?
I
1
S3
d d
sss
odd
o
00
u
_3
"3
p-
U
CQ
Recommended
1 mercury
f
1
•y
Compoun
S3
§
t .
00
"S
1
^
—
g
o
f
1
snt (1985) were e
and Momi
o"
!*
•§
„ JS
11
CQ S
•S 1
1J K
1 below. The values repo
'eight to result in the vah
! b
8 *
2 2
8 I
•i °
CO
>> IS
0 £
§!,
•S 'S
fla j^
O cc
II
£
sing the geometric
rcent soil moisture
3 O
0) O
"3 ~S
~5 *
0 ri
eg -g,
^ "S
IThe BCF
soil wet w
Eiseniafoetida
1
2
VO
oo
^T
u
1
•o
§
3
1
CQ
c^ ro ON
OO 00 00
-------
S»M
fifi
"*
pa
?!
Oft
O
•3
U
ft
6
"S
fat
£
1
g
s
•S
i
t3
References
a
|| 27Reported V
S
o
o
>
a.
U
CQ
1
Recommen
o
2
Compound:
g>
3
i>
'5
•S
>
o
00
'§
s
1
converted to
£
u
oo"
oo
2
N_^
1
ea
1
J
'(»
£
^
1%
B
•rt
S
Q
&
tfi
J3
"3
u
=e
^
1
B
<2
1
"3
f
_«
o
B
U
E
the geometric
ilated using
of 5.99".
IThe BCF was calci
a conversion factor
1
Eiseniafoe,
Q
CO
s.
U
I?
•0
OO
ts
oo
2
J
1
S£
u
Rhett, Simm
m ^H •*•
O O o
odd
04
d
u
j3
"3
0
CQ
•O
•8
Recommen
Selenium
Compound:
^
o
u
>5-
u
IS
'§
M
•o
•ith empirical
^
CA
U
'S
ca
£?
O
1
<2
en
U
3
1
"S
I
B
|
y
»H
u
2
o
§
c
o
'•§
•i
u
•5
en
e recommended BCF
try, nickel, and zinc).
H 5i
E
:re not availab
ead, inorganic
selenium we
m, copper, 1
1 Empirical data for
cadmium, chromiu
CN
d
u
"3
OH
U
m
"8
T3
Recommen
1
&5
1 Compound:
g"
3
"i
T3
03
U
'S
JB
2
JS
'3
ca
empirical dat
j2
•|
u
'S
ea
f
o
:S
.2
1
"3
•o
u
•o
B
U
E
4$
O
•8
e
S
s
u
0
J
•5
u
^commended BCF is t
and zinc).
* T3
P e
not available.
mic mercury, i
II
S T3
1 Empirical data for
chromium, copper,
04
d
o
"3
CL,
U
ra
1
Recommen
Thallium
Compound:
E'
_3
E'
T3
03
U
.a
C
sS'
t)
1
'3
ca
ca
n
•o
ith empirical
>
.3
§
BO
Q
U
O
•S
.2
1
"3
"8
e
u
E
cj
£
U
•S
0
B
ca
4)
E
u
'•S
u
"i
•s
09
; recommended BCF
, and zinc).
H-3
~ o
,j-s
re not availabl
inic mercury,
II
S "^
Empirical data for
1 chromium, copper,
55
o
-------
tj
S
DC
ce
V
1
o.
1/1
£
*J
b
£
3
I
1
a,
S
as
0)
u
i
Q>
tiS
«
B8(
a
en
V
S
5
>
^
V
•"
w
o
a
si
ex
fS]
VO
«n
d
o
3
13
b
O
ca
Recommended
o
B
N
•a
c
D
o
a.
J
o
•a
£
I
§
D
U
/•— \
^f
2
Sw^
•g
o
C
Kl
>•
1
y— \
£S
o\
C3
S
0?
oo
2
«L>
,2
•a
rt
S
u
_E
C/3
S
S
^
tn
1
Q
&
CO
a>
3.
"3
>
w
jS
o
.S
N
5
S
!
>~»
i
J«
§s
os in
«"S
•g |
§tj
**2
SI
the geometri
ng a convers
00 w
C 3
*S5 **
s-a
11
*3 -^
.a -o
ca t.
0 0
CO >
cs O
? *•*
tt. ~Sb
0 "5
CQ £
5 «
P -S
Eisenia foetida
1
CO
0
S
it?
*O
00
C4
/— N
OO
oo
2
J
T3
g
"
i
3
o
S
— VO CX3
^ O in
odd
Not specified
1
CO
O
a,
d
u
'S
P
Ma (1987)
&,
r-
d
»— i
Alabophera sp.
Luntbricus sp.
Octolasium sp.
C4
2
u
'2
^
^^
S
r^
o\
Van Hook
oo
fN
CO
*J
O
•»- O
s b
II
00
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Makela, Petanei
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X «
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TABLE C-3
WATER-TO-AQUATIC INVERTEBRATE BIOCONCENTRA
(mg COPC / kg wet tissue) / (mg dissolved COPC / L
(Page 18 of 18)
en
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Experimental Parameters
Reference
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ngle, Hissong, Katz, and Mulawka
>68)
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kill
presented as the amount of COPC in invertebrate tissue divided by the amount of CO
-eight over amount of COPC in water, they were converted to wet weight by dividing
ss an invertebrate's total weight is 83.3 percent moisture, which is based on the moisl
is calculated as follows:
rnnvmjm fader- 1-° *ram (*> invertebrate total weigh
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1.0 ^r«m (g) invertebrate total weight - 0.833 g iwver
organic COPCs are assumed to be total COPC concentration in water and, therefore,
Dm U.S.EPA (1995b):
(total) /fw)-l
1) = BCF based on dissolved concentration of COPC in water
JCF based on the field derived data for total concentration of COPC in water
f COPC that is freely dissolved in the water
1 / [1 + ((DOC x K,,w) / 10) + (POC x K™)]
= Dissolved organic carbon, kilograms of organic carbon / liter of water (2.0 x Ifr06
= Octanol-water partition coefficient of the COPC, as reported in U.S. EPA (1994b)
= Paniculate organic carbon, kilograms of organic carbon / liter of water (1.5 x 10 w
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1 '111
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TABLE C-4
/^N
fSI
1-H
•s
v>
V
I
S2
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s
0.
B?
SS
V
*•»
Experimental Paran
leference
I*
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o>
—
>.
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e
c.
01
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tory values as follows:
2
o
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B
«
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o
00
B
calculated us:
je was
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>
n
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e
8
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a
1
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1
exposure duration
g>
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s
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ed
1
s
r, Viswanaths
1)
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0
S
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g
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u
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6
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y exposure duration
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rgren (1982)
1
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a.
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1.
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1
8
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i
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c
S
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1 :
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o
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y exposure duration
itile Organic Compounds
i •§ "3
CO ^
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III
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<4-l ~
s i £
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8
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1
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ing the following regression equatio:
, where log K,,w = -0.222 (Karickoff
3 00
1 -
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l jj: t/3
i a, "9
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(Southworth,
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Laboratory
log BCF =
oo
ci
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ing the following regression equatio
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3 0?
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as calcul
chmiede
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log BCF =
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d
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3
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U
BQ ,
1
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8
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n
o
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5
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3
in
^
ing the following regression equatio
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• =» ^
3 °°
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11
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& °"
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51
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ta oo
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Compound
Laboratory
log BCF =
2
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3
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EQ
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ited using the following reg
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1.146 (Southworth, Beauchan
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Besser, Canfield, £
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1
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Fisher, Bohe, and '
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Baudin (1974)
0
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Fucus serratus
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18
TABLE C-5
FISH BIOCONCENTRAT
wet tissue) / (mg dissolved
(Page 7 of 19)
3?
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Pimephales promela
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U.S. EPA (1987)
8
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Freshwater fish
Recommended BCF
i
|
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; ' en
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U.S. EPA (1980h)
Oliver and Niimi (1988)
llorobutadiene
lue was calculated using the geome
1 >
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0 «n "c
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c ~ ~~ ~~~
08
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VO
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>
Gambusia affinis
Recommended BCF
1
I
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1 6
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11 i
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0
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Laska, Bartell, Laseter (1976)
llorocyclopentadiene
lue was calculated using the geome
ca ™
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00
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les promelas
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lue was calculated using the geoi
Banerjee, Suggatt, and O'Grad;
Bruggeman, Oppenhuizen, Wijl
Hutzinger (1984)
0 i ra
S u
a, £
-o
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c
3
a
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follows:
laboratory values as
8
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e
CO
J"
5
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I
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ue was calculated using the j
cS
>
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u
m
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1
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|
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1 -day exposure du
i
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,
i
i
Garten and Trabalka (1983)
Gates and Tjeerdema (1993
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3 !
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ided BCF val
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rn
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1
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b
Garten and Trabalka (1983
«•> o)
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Oncorhynchus mykiss
dnmhuvin nfftniv
C
1
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X
4.
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M ! ^
1 1
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Hamelink and Waybrant (1
Metcalf. Sanuha. and Kane
°. o" vo - ' r
V~l — ' O 00 ^
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Oncorhynchus mykiss
Pimephales promelas
1
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Not reported
Not reported
28-day exposure duration
Id values.
Field samples. The field values reported in Saiki,
Castleberry, May, Martin, and Ballard (1995) were
converted to wet weight using a conversion factor of
5.0°. The field values are also based on mean values
calculated for each of the 4 fish species.
i °
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issolved COPC concentrations is from U.S. EPA (1995a) as follows:
"O
o
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icentrations in field san
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^
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U
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5 logK,,,, = 1.49
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3 53
U gj
The BCF was cal
:hamp, and Schmi
M
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1,3-Dinitrobenze
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2,4-Dinitrotoluet
Compound:
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BCF value was b;
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c
The recommf
i
1
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s
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1
4-day exposur
1 Pearson (1983)
s
§
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n
3
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log BCF = 0.
r^
ci
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3
1
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PQ
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«
Nitrobenzene
Compound:
21
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jfg:
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Following regre!
elogK^l.8
« J
a-g
00 -
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*j «3
"3 "5
o ••?*
The BCF was cal
champ, and Schm
3
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r this compc
Southworth,
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Pentachloronitrol
Compound:
i
2~
^^
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.1 <
|B|
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e log K..-4.6.
•hthalate Estei
-II
co oo
5 t^*
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3 T3
— O
The BCF was ca
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Compound:
f
B -
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following regression
; log Kow = 5.503 (U.
u S3
•£ J3
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U
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1.1
s §
5 BCF was
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compound wen:
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Compound:
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log BCF = 0.
t**l
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73
§
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£
Compound;
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The recomrm
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Screening Level Ecological Risk Assessment Protocol
Appendix C; Media-To-Receptor BCF Values August 1999
Adams, W.C. 1976. The Toxicity and Residue Dynamics of Selenium in Fish and Aquatic Invertebrates.
Ph.D. Thesis. Michigan State University. East Lansing, Michigan.
Adams, W.J., G.M. DeGraeve, T.D. Sabourin, J.D. Cooney, and G.M. Mosher. 1986. "Toxicity and
Bioconcentration of 2,3,7,8-TCDD to Fathead Minnows (Pimephales promelas)." Chemosphere.
Volume 15, Numbers 9-12. Pages 1503-1511.
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Trace Substances in Environmental Health XIII. University of Missouri, Columbia.
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Species of Freshwater Fish: Salmo gairdneri, Rainbow Trout; Lepomis macrochirus, Bluegill;
Micropterus salmoides, Largemouth Bass; Ictalurus punctatus, Channel Catfish." Prepared for
U.S. Nuclear Regulatory Commission, NUREG/CR-0893, Prepared by Pacific Northwest
Laboratory, PNL-3046.
Andryushchenko, V. V., and G.G. Polikarpov. 1973. "An Experimental Study of Uptake of Zn65 and DDT
by Ulva rigid from Seawater Polluted with Both Agents." Hydrobiological Journal. Volume 4.
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contamination of bluegill (Lepomis macrochirus) from two Indiana lakes." Transactions,
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Center for Combustion Science and Engineering C-99
-------
Screening Level Ecological Risk Assessment Protocol
Appendix C; Media-To-Receptor BCF Values August 1999
Barrows, M.E., S.R. Petrocelli, K.J. Macek, and J. Carroll. 1978. "Bioconcentration and Elimination of
Selected Water Pollutants by Bluegill Sunfish." Preprints of Papers Presented at the 176th
National Meeting, American Chemical Society, Miami Beach, Florida, September 10-15, 1978
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Activities as Biomarkers in Lymnaea palustris Mollusca, Gastropoda) Exposed to Atrazine and
Hexachlorobenzene in Freshwater Mesocosms." Environmental Toxicology and Chemistry.
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Wofford, H.W., C.D. Wilsey, G.S. Neff, C.S. Giam, and J.M. Neff. 1981. "Bioaccumulation and
Metabolism of Phthalate Esters by Oysters, Brown Shrimp, and Sheepshead Minnows."
Ecotoxicology and Environmental Safely. Volume 5. Pages 202-210.
Wood, L.W., P. O'Keefe, and B. Bush. 1997. "Similarity Analysis of PAH and PCB Bioaccumulation
Patterns in Sediment-Exposed Chironomus teutons Larvae." Environmental Toxicology and
Chemistry. Volume 16, Number 2. Pages 283-292.
Yockim, R.S., A.R. Isensee, and G.E. Jones. 1978. "Distribution and Toxicity of TCDD and 2,4,5-T in
an Aquatic Model Ecosystem." Chemosphere. Volume 7, Number 3. Pages 215-220.0
Zaroogian, G.E., and S. Cheer. 1976. "Accumulation of Cadmium by the American Oyster, Crassostrea
virginica." Nature. Volume 261. Pages 408-410.
Zaroogian, G.E., G. Morrison, and J.F. Heltshe. 1979. "Crassostrea virginica as an Indicator of Lead
Pollution." Marine Biology. Volume 52. Pages 189-196.
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering C-l 16
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APPENDIX D
BIOCONCENTRATION FACTORS (BCFs)
FOR WILDLIFE MEASUREMENT RECEPTORS
Screening Level Ecological Risk Assessment Protocol
August 1999
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Appendix D; Wildlife Measurement Receptor BCF Values August 1999
APPENDIX D
TABLE OF CONTENTS
Section Page
D-1.0 GENERAL GUIDANCE D-l
D-l.l BIOTRANSFER FACTORS FOR MAMMALS (Bamamma^ D-3
D-1.2 BIOTRANSFER FACTORS FORBIRDS (Babird) D-5
REFERENCES: APPENDIX D TEXT D-9
TABLES OF WILDLIFE MEASUREMENT RECEPTOR BCF VALUES D-ll
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Appendix D; Wildlife Measurement Receptor BCF Values August 1999
APPENDIX D
WILDLIFE MEASUREMENT RECEPTOR BCFs
Appendix D provides recommended guidance for determining values for compound-specific, media to
receptor, bioconcentration factors (BCFs) for wildlife measurement receptors. Wildlife measurement
receptor BCFs should be based on values reported in the scientific literature, or estimated using physical
and chemical properties of the compound. Guidance on use of BCF values in the screening level
ecological risk assessment is provided in Chapter 5.
Section D-1.0 provides the general guidance recommended to select or estimate compound BCF values for
wildlife measurement receptors. Sections D-1.0 through D-1.3 further discuss determination of BCFs for
specific media and receptors. References cited in Sections D-l.l through D-1.3 are located following
Section D-1.3.
For the compounds commonly identified in risk assessments for combustion facilities (identified in Chapter
2) and the mammal and bird example measurement receptors listed in Chapter 4, BCF values have been
determined following the guidance in Sections D-1.0 through D-1.3. BCF values for these limited number
of compounds and pathways are included in this appendix (see Tables D-l through D-3) to facilitate the
completion of screening ecological risk assessments. However, it is expected that BCF values for
additional compounds and receptors may be required for evaluation on a site specific basis. In such cases,
BCF values for these additional compounds could be determined following the same guidance
(Sections D-1.0 through D-1.3) used in determination of the BCF values reported hi this appendix. For the
calculation of BCF values for measurement receptors not represented in Sections D-l.l through Dl-3 (e.g.,
amphibians and reptiles), an approach consistent to that presented in this appendix could be utilized by
applying data applicable to those measurement receptors being evaluated.
For additional discussion on some of the references and equations cited in Sections D-1.0 through D-1.3,
the reader is recommended to review the Human Health Risk Assessment Protocol (HHRAP) (U.S. FJPA
1998) (see Appendix A-3), and the source documents cited in the reference section of this appendix.
D-1.0 GENERAL GUIDANCE
This section describes general procedures for developing compound-specific BCFs from biotransfer
factors (Ba) for assessing exposure of measurement receptors. A biotransfer factor is the ratio of the
compound concentration in fresh (wet) weight animal tissue to the daily intake of compound by the
animal through ingestion of food items and media (soil, sediment, surface water). Therefore, as
discussed in Chapter 5, biotransfer factors and receptor-specific ingestion rates can be used to calculate
food item- and media-to-animal BCFs. This approach provides an estimate of biotransfer of compounds
from applicable food items and media to measurement receptors ingesting these items.
Biotransfer factors could also be used directly in equations to calculate dose to measurement receptors.
However, in order to promote consistency in evaluating exposure across all trophic levels within complex
food webs, BCFs calculated from Ba values are recommended in this guidance for evaluating
measurement receptors. The use of Ba values to determine BCF values, and the use of BCF values in
general, for the estimation of compound concentrations in measurement receptors may introduce
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Appendix D; Wildlife Measurement Receptor BCF Values August 1999
uncertainty. Major factors that influence the uptake of a compound by an animal, and therefore
uncertainty, include bioavailability, metabolic rate, type of digestive system, and feeding behavior.
Uncertainties also should be considered regarding the development of biotransfer values in comparison to
how they are being applied for estimating exposure. For example, biotransfer values may be used to
estimate contaminant uptake to species from items ingested that differ from the species and intakes used
to empirically develop the values. Also, biotransfer data reported in literature may be specific to tissue or
organ analysis versus whole body. As a result, BCFs may be under- or over-estimated to an unknown
degree.
BCFs for Measurement Receptors Ingesting Food Items BCF values for measurement receptors
ingesting food items (plants or prey) can be calculated using the compound specific Ba value applicable
to the animal (e.g., mammal, bird, etc.) and the measurement receptor-specific ingestion rate as follows:
BCFF_A = BaA • IRF Equation D-1-1
where
BCFF.A = Bioconcentration factor for food item (plant or prey)-to-animal
(measurement receptor) [(mg COPC/kg FW tissue)/(mg COPC/kg FW
food item)]
BaA = COPC-specific biotransfer factor applicable for the animal
(day/kg FW tissue)
IRF = Measurement receptor food item ingestion rate (kg FW/day)
As an example of applying the above equation, BCF values for plants-to-wildlife measurement receptors
listed in Chapter 4 are provided in Table D-l at the end of this appendix. Measurement-receptor specific
ingestion rates used to calculate BCFs are presented in Table 5-1. Ba values applicable to the mammal
and bird measurement receptors in Table D-l are discussed in Sections D-l.l and D-l.2, respectively.
BCFs for Measurement Receptors Ingesting Media BCF values for measurement receptors in trophic
levels 2, 3, and 4 ingesting media (i.e., soil, surface water, and sediment) can be calculated using the
compound specific Ba value applicable to the animal (e.g., mammal, bird, etc.) and the measurement
receptor-specific ingestion rate as follows:
BCFM A = BaA ' IRu Equation D-l-2
where
BCFM.A = Bioconcentration factor for media-to-animal (measurement receptor)
[(mg COPC/kg FW tissue)/(mg COPC/kg WW or DW media)]
BaA = COPC-specific biotransfer factor applicable for the animal
(day/kg FW tissue)
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Appendix D; Wildlife Measurement Receptor BCF Values August 1999
IRU = Measurement receptor media ingestion rate (WW or DW kg/day)
Equation D-l-2 assumes that BaA provides a reasonable estimate of the uptake of a compound from
incidental ingestion of abiotic media during foraging.
As an example of applying the above equation, BCF values for various wildlife measurement receptors
listed in Chapter 4 are provided in Table D-2 (water) and Table D-3 (soil and sediment).
Measurement-receptor specific ingestion rates used to calculate BCFs are presented in Table 5-1. Ba
values applicable to the mammal and bird measurement receptors for which values were calculated are
discussed in Sections D-l.l and D-1.2, respectively.
BCFs for Dioxins and Furans As discussed in Chapter 2, the BCF values for PCDDs and PCDFs are
calculated using bioaccumulation equivalency factors (BEFs). Consistent with U.S. EPA (1995b), BEFs
are expressed relative to the BCF for 2,3,7,8-TCDD as follows:
BCFj = BCF2^TCDD • BEFj Equation D-l-3
where
BCFj = Food item-to-animal or media-to-animal BCF foryth PCDD or
PCDF congener for food item-to-animal pathway [(mg
COPC/kg FW tissue)/(mg COPC/kg FW plant)]or media-to-
animal pathway [(mg COPC/kg FW tissue)/(mg COPC/kg WW
media)]
BCF2,3j,8-TCDD = Food item-to-animal or media-to-animal BCF for 2,3,7,8-TCDD
BEFj = Bioaccumulation equivalency factor for/th PCDD or PCDF
congener (unidess)
The use of BEFs for dioxin and furan congeners is further discussed in Chapter 2.
D-l.l BIOTRANSFER FACTORS FOR MAMMALS (Bamammal)
As discussed in Section D-1.0, calculation of BCF values to be used in pathways for mammals ingesting
food items and media requires the determination of COPC-specific biotransfer factors for mammal
measurement receptors (Bamammc^. This section discusses selection of the fiOn^m^ values used to
calculate the COPC and measurement receptor specific BCF values presented in Tables D-l through D-3.
Organics For organics (except PCDDs and PCDFs), the following correlation equation from Travis and
Arms (1988) was used to derrive Bammmal values on a FW basis:
l°SBamammal =-7.6 + \ogKow Equation D-l-4
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Appendix D; Wildlife Measurement Receptor BCF Values August 1999
where
Bamammai = Biotransfer factor for mammals (day/kg FW tissue)
Kow = Octanol-water partition coefficient (unitless)
To calculate the values presented in Tables D-l through D-3, COPC-specific Km values were obtained
from Appendix A-2.
Biotransfer factors obtained from Travis and Arms (1988) were derived from correlation equations
developed from data on experiments conducted with beef cattle ingesting food items and media
containing compound classes such as DDT, pesticides, PCDDs, PCDFs, and PCBs. As further literature
is developed for other species and compounds, the Travis and Arms (1988) correlation equation should
be compared for applicability to species and compound, and best fit correlation for estimation of uptake.
PCDDs and PCDFs Bamammal values for PCDD and PCDFs were derrived from Ba values for cattle as
presented in:
• U.S. EPA 1995a. "Further Studies for Modeling the Indirect Exposure Impacts from
Combustor Emissions." Memorandum from Matthew Lorber, Exposure Assessment
Group, and Glenn Rice, Environmental Criteria and Assessment Office, Washington,
D.C. January 20.
U.S. EPA (1995a) determined Ba values for cattle from McLachlan, Thoma, Reissinger, and Hutzinger
(1990). These empirically determined Ba values were recommended by U.S. EPA (1995a) over the
Travis and Arms (1988) correlation equation for dioxins and furans.
Inorganics For metals (except cadmium, mercury, selenium, and zinc), Ba values on a fresh weight
basis were obtained from Baes, Sharp, Sjoreen, and Shor (1984). For cadmium, selenium, and zinc, U.S.
EPA (1995a) indicated that Ba values were derived by dividing uptake slopes [(g compound/kg DW
tissue)/(g compound/kg DW feed)], obtained from U.S. EPA (1992), by a daily consumption rate of
20 kilograms DW per day by cows.
For use in calculating BCF values presented in Tables D-l through D-3 of this appendix, dry weight Ba
values were converted to fresh weight basis by assuming a tissue moisture content (by mass) of
70 percent for cows. Moisture content information was obtained from the following:
• U.S. EPA. 1997a. Exposure Factors Handbook. "Food Ingestion Factors". Volume H
EPA/600/P-95/002Fb. August.
• Pennington, J.A.T. 1994. Food Value of Portions Commonly Used. Sixteenth Edition.
J.B. Lippincott Company, Philadelphia.
Mercuric Compounds Based on assumptions made regarding speciation and fate and transport of
mercury from stack emissions (as discussed in Chapter 2), elemental mercury is assumed not to deposit
onto soils, water, or plants. Therefore, it is also not available in food items or media for ingestion and
subsequent uptake by measurement receptors. As a result, no BCF values for elemental mercury are
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Screening Level Ecological Risk Assessment Protocol
Appendix D; Wildlife Measurement Receptor BCF Values August 1999
presented in Tables D-l through D-3 of this appendix. If site-specific field data suggest otherwise, Ba
values for elemental mercury can be derived from uptake slope factors provided in U.S. EPA (1992) and
U.S. EPA (1995a), using the same consumption rates as were discussed earlier for the metals like
cadmium, selenium, and zinc.
Bammmat values for mercuric chloride and methyl mercury were derived from data in U.S. EPA (1997b).
U.S. EPA (1997b) provides Ba values for mercury in cows, but does not specify the form of mercury. To
obtain the Ba values for mercuric chloride and methyl mercury presented in Tables D-l through D-3 of
this guidance, consistent with U.S. EPA (1997b) total mercury was assumed to be composed of
87 percent divalent mercury (as mercuric chloride) and 13 percent methyl mercury in herbivore animal
tissue. Also, assuming that the Ba value provided in U.S. EPA (1997b) is for the total mercury in the
animal tissue, then biotransfer factors in U.S. EPA (1997b) can be determined for mercuric chloride and
methyl mercury, as follows:
• The default Ba value of 0.02 day/kg DW for total mercury obtained from U.S. EPA
(1997b) was converted to a fresh weight basis assuming a 70 percent moisture content in
cow tissue (U.S. EPA 1997a; Pennington 1994). The fresh weight Ba value for total
mercury was multiplied by 0.13 to obtain a Bamammal value for methyl mercury, and
by 0.87 to obtain a Bamammal value for mercuric chloride.
D-1.2 BIOTRANSFER FACTORS FOR BIRDS
As discussed in Section D-1.0, calculation of BCF values to be used in pathways for birds ingesting food
items and media requires the determination of COPC-specific biotransfer factors for bird measurement
receptors (Bahini). This section discusses selection of the Babird values used to calculate the COPC and
measurement receptor specific BCF values presented in Tables D-1 through D-3.
Oreanics Babird values for organic compounds (except PCDDs and PCDFs) were derived from Bamamtal
values by assuming that the lipid content (by mass) of birds and mammals is 15 and 19 percent,
respectively. Therefore, Babird values presented in Tables D-l through D-3 were determined by
multiplying Bamammal values by the bird and mammal fat. content ratio of 0.8 (15/19).
Notable uncertainties associated with this approach include (1) extent to which specific organic
compounds bioconcentrate in fatty tissues, and (2) differences in lipid content, metabolism, and feeding
characteristics between species.
PCDDs and PCDFs Babird values presented in Tables D-l through D-3 for PCDD and PCDF congeners
were derrived from data provided in the following:
• Stephens, R.D., M. Petreas, and G.H. Hayward. 1995. "Biotransfer and
Bioaccumulation of Dioxins and Furans from Soil: Chickens as a Model for Foraging
Animals." The Science of the Total Environment. Volume 175. Pages 253-273.
Stephens, Petreas, and Hayward (1995) conducted experiments to determine the bioavailability and the
rate of PCDDs and PCDFs uptake from soil by foraging chickens. Three groups of White Leghorn
U.S. EPA Region 6 U.S. EPA
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Screening Level Ecological Risk Assessment Protocol
Appendix D: Wildlife Measurement Receptor BCF Values August 1999
chickens were studied—control group, low exposure group, and high exposure group. Eggs, tissues
(liver, adipose, and thigh), feed, and feces were analyzed.
Congener specific BaUrd values were derrived from the Stephens, Petreas, and Hayward (1995) study by
dividing estimated whole body bioconcentration values for the high exposure group by a daily
consumption rate of soil. If congener specific BCF values were not reported for the high exposure group,
then estimated whole body values were determined using reported data for the low exposure group, if
available. A default consumption rate of soil by chicken of 0.02 kg DW/day was determined as follows:
(1) Consumption rate of feed by chicken was obtained from U.S. EPA (1995a), which cites a
value of 0.2 kg (DW) feed/day obtained from various literature sources.
(2) The fraction of feed that is soil (0.1) was obtained from Stephens, Petreas, and
Hayward (1995).
(3) Feed consumption rate of 0.2 kg/day was multiplied by fraction of feed that is soil (0.1),
to obtain the soil consumption rate by chicken of 0.2 x 0.1 = 0.02 kg DW soil/day.
Inorganics For metals (except cadmium, selenium, and zinc), Babird values were not available in the
literature. For cadmium, selenium, and zinc, U.S. EPA (1995a) cites Ba values that were derived by
dividing uptake slopes [(g compound/kg dry DW tissue)/(g compound/kg DW feed)], obtained from U.S.
EPA (1992), by a daily ingestion rate of 0.2 kilograms DW per day by poultry. To determine BCF
values presented in Tables D-l through D-3 in this appendix, reported dry weight Ba values were
converted to fresh weight basis by assuming a tissue moisture content (by mass) of 75 percent for
poultry (U.S. EPA 1997a; Pennington 1994).
Mercuric Compounds Based on assumptions made regarding speciation and fate and transport of
mercury from stack emissions (as discussed in Chapter 2), elemental mercury is assumed not to deposit
onto soils, water, or plants. Therefore, it is also not available in food items or media for ingestion and
subsequent uptake by measurement receptors. As a result, no BCF values for elemental mercury are
presented in Tables D-l through D-3 of this appendix. If site-specific field data suggest otherwise, Ba
values for elemental mercury can be derived from uptake slope factors provided in U.S. EPA (1992) and
U.S. EPA (1995a), using the same consumption rates as were discussed earlier for the metals like
cadmium, selenium, and zinc.
Babird values for mercuric chloride and methyl mercury were derived from data in U.S. EPA (1997b).
U.S. EPA (1997b) provides Ba values for mercury in poultry, but does not specify the form of mercury.
To obtain the Ba values for mercuric chloride and methyl mercury presented in Tables D-l through D-3
of this guidance, consistent with U.S. EPA (1997b) total mercury was assumed to be composed of
87 percent divalent mercury (as mercuric chloride) and 13 percent methyl mercury in herbivore animal
tissue. Also, assuming that the Ba value provided in U.S. EPA (1997b) is for the total mercury in the
animal tissue, then biotransfer factors in U.S. EPA (1997b) can be determined for mercuric chloride and
methyl mercury, as follows:
U.S. EPA Region 6 U.S. EPA
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Screening Level Ecological Risk Assessment Protocol
Appendix D; Wildlife Measurement Receptor BCF Values August 1999
• The default Ba value of 0.02 day/kg DW for total mercury obtained from U.S. EPA
(1997b) was converted to a fresh weight basis assuming a 75 percent moisture content in
poultry tissue (U.S. EPA 1997a; Pennington 1994). The fresh weight Ba value for total
mercury was multiplied by 0.13 to obtain a Babird value for methyl mercury, and by 0.87
to obtain a Babird value for mercuric chloride.
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering D-7
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Appendix D; Wildlife Measurement Receptor BCF Values August 1999
Baes, C.F., R.D. Sharp, A.L. Sjoreen, and R.W. Shor. 1984. "Review and Analysis of Parameters and
Assessing Transport of Environmentally Released Radionuclides through Agriculture."
Oak Ridge National Laboratory. Oak Ridge, Tennessee.
McLachlan, M.S., H. Thoma, M. Reissinger, and O. Hutzinger. 1990. "PCDD/F in an Agricultural
Food Chain. Parti: PCDD/F Mass Balance of a Lactating Cow." Chemosphere. Volume 20.
Pages 1013-1020.
Pennington, J.A.T. 1994. Food Value of Portions Commonly Used. Sixteenth Edition. J.B. Lippincott
Company, Philadelphia.
Stephens, R.D., M. Petreas, and G.H. Hayward. 1995. "Biotransfer and Bioaccumulation of Dioxins and
Furans from Soil: Chickens as a Model for Foraging Animals." The Science of the Total
Environment. Volume 175. Pages 253-273.
Travis, C.C., and A.D. Arms. 1988. "Bioconcentration of Organics in Beef, Milk, and Vegetation."
Environmental Science and Technology. 22:271-274.
U.S. EPA. 1992. Health Reassessment of Dioxin-Like Compounds, Chapters 1 to 8. Workshop Review
Draft. OHEA. Washington, D.C. EPA/600/AP-92/001a through OOlh. August.
U.S. EPA. 1994. "Draft Guidance for Performing Screening Level Risk Analyses at Combustion
Facilities Burning Hazardous Wastes. Attachment C, Draft Exposure Assessment Guidance for
RCRA Hazardous Waste Combustion Facilities." April 15.
U.S. EPA 1995a. "Further Studies for Modeling the Indirect Exposure Impacts from Combustor
Emissions." Memorandum from Matthew Lorber, Exposure Assessment Group, and Glenn Rice,
Indirect Exposure Team, Environmental Criteria and Assessment Office, Washington, D.C.
January 20.
U.S. EPA. 1995b. Great Lakes Water Quality Initiative Technical Support Document for the Procedure
to Determine Bioaccumulation Factors. EPA-820-B-95-005. Office of Water, Washington, D.C.
March.
U.S. EPA. 1997a. Exposure Factors Handbook. "Food Ingestion Factors". Volume H
EPA/600/P-95/002Fb. August.
U.S. EPA. 1997b. Mercury Study Report to Congress, Volumes I through VIII. Office of Air Quality
Planning and Standards and ORD. EPA/452/R-97-001. December.
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering D-9
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Screening Level Ecological Risk Assessment Protocol
Appendix D; Wildlife Measurement Receptor BCF Values August 1999
TABLES OF MEASUREMENT RECEPTOR BCF VALUES
Screening Level Ecological Risk Assessment Protocol
August 1999
D-l PLANTS TO WILDLIFE MEASUREMENT RECEPTORS D-13
D-2 WATER TO WILDLIFE MEASUREMENT RECEPTORS D-16
TABLE D-3 SOIL/SEDIMENT TO WILDLIFE MEASUREMENT RECEPTORS D-22
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering D-l 1
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APPENDIX E
TOXICITY REFERENCE VALUES
Screening Level Ecological Risk Assessment Protocol
August 1999
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Screening Level Ecological Risk Assessment Protocol
Appendix E; Toxicity Reference Values August 1999
APPENDIX E
TABLE OF CONTENTS
Section Page
E-1.0 TRVs FOR COMMUNITY MEASUREMENT RECEPTORS IN SURFACE WATER,
SEDIMENT, AND SOIL E-l
E-2.0 TRVs FOR WILDLIFE MEASUREMENT RECEPTORS E-5
REFERENCES: APPENDIX E TEXT E-7
TABLES OF TOXICITY REFERENCE VALUES E-9
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Penmitting Division Office of Solid Waste
Center for Combustion Science and Engineering E-i
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Appendix E: Toxicity Reference Values August 1999
APPENDIX E
TOXICITY REFERENCE VALUES
Appendix E presents implementation of the recommended approach (described in Chapter 5) for identifying
toxicity reference values (TRVs) for measurement receptors. Discussion is provided for determining
compound-specific TRY values for community and wildlife measurement receptors.
Following the guidance in Sections E-1.0 through E-1.2, U.S. EPA OSW has identified default TRY values
for the measurement receptors of the seven example food webs (listed in Chapter 4) and the compounds
commonly identified in ecological risk assessments for combustion facilities (identified in Chapter 2).
Section E-1.0 describes the determination of TRY values for surface water, sediment, and soil community
measurement receptors in the example food webs. Section E-2.0 describes determination of TRY values fen-
wildlife measurement receptors in the example food webs. Tables E-l through E-8 present the default TRY
values selected, the basis for selection of each value, and the references evaluated in determination of each
value.
TRY values for a limited number of compounds are included in this appendix (see Tables E-l through E-3)
to facilitate the completion of screening ecological risk assessments. However, it is expected that TRV
values for additional compounds and receptors may be required for evaluation on a site specific basis. In
such cases, TRV values for these additional compounds could be determined following the same guidance
used in determination of the 77?V values reported in this appendix. For the determination of TRV values for
measurement receptors not specifically represented in Sections E-1.0 through E-2.0 (e.g., amphibians and
reptiles), an approach consistent to that presented in this appendix could be utilized by applying data
applicable to those measurement receptors being evaluated.
The default TRVs provided in Tables E-l through E-8 are based on values reported in available scientific
literature. Toxicity values identified in secondary reference sources were verified, where possible, by
reviewing the primary reference source. As noted in Chapter 5, TRV values may change as additional
toxicity research is conducted and the availability of toxicity data in the scientific literature increases. As a
result, U.S. EPA OSW recommends evaluating the latest toxicity data before completing a risk assessment
to ensure that the toxicity data used in the risk assessment is the most current. If more appropriate TRV
values can be documented, they should be used presented to the respective permitting authority for
approval.
TR Vs were not identified for amphibians and reptiles because of the paucity of lexicological information on
these receptors. Additional guidance on determination and use of TRV values in the screening level
ecological risk assessment is provided in Chapter 5.
E-1.0 TRVs FOR COMMUNITY MEASUREMENT RECEPTORS IN SURFACE WATER,
SEDIMENT, AND SOIL
TRV values provided in this appendix for community measurement receptors in surface water, sediment,
and soil were identified from screening toxicity values developed and/or adopted by federal and/or state
regulator^' agencies. As discussed in Chapter 5, these screening toxicity values are generally provided in
the form of standards, criteria, guidance, or benchmarks. For compounds with no available screening
toxicity value, TRVs were determined using toxicity values from available scientific literature. The
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering E-l
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Appendix E; Toxicity Reference Values August 1999
equilibrium partitioning (EqP) approach was used to compute several sediment TR Vs. Uncertainty factors
(UFs) were applied to toxicity values, as necessary, to meet the TRY criteria discussed in Chapter 5. The
following sections discuss determination of 77?V values for community receptors in surface water,
sediment, and soil.
Freshwater TRVs Freshwater TRVs should be used for freshwater and estuarine ecosystems with a
salinity less than 5 parts per thousand. Freshwater 77? Vs, based on the dissolved concentration of the
compound in surface water, are listed in Table E-l. 77?Vs were identified using the following hierarchy:
1. Federal chronic ambient water quality criteria (AWQC) calculated for with no final
residue value (U.S. EPA 1999; 1996b). Federal AWQC for cadmium, copper, lead,
nickel, and zinc were multiplied by a chemical-specific conversion factor to determine a
TWbased on dissolved concentration (U.S. EPA 1999; 1996b).
2. Final chronic values (FCV) for COPCs for which their AWQC included a final residue
value (U.S. EPA 1996b).
3. If inadequate data (insufficient number of families of aquatic life with toxicity data) were
available to compute an AWQC or FCV, U.S. EPA (1999; 1996b) also reported
secondary chronic values (SCV) calculated using the Tier II method in the Great Lakes
Water Quality Initiative (GLWQI) (reported in 40 CFR Part 122). This method is similar
to the procedures for calculating an FCV. It uses statistically-derived "adjustment factors"
to address deficiencies in available data. The adjustment factor decreases as the number of
representative families increases.
4. If an AWQC, FCV, or GLWQI Tier n SCV value were not available, toxicity values cited
by U.S. EPA (1987) were identified. These toxicity values represent the lowest available
values. Further, additional toxicity values available from the AQUIRE database in U.S.
EPA's ECOTOXicology Database System (U.S. EPA 1996a) were identified. If collected
from a secondary source (such as AQUIRE), original studies were obtained and reviewed
for accuracy. The toxicity values reported in Table E-l represent the lowest (most
conservative), ecologically relevant, available value.
5. If toxicity data were unavailable, a surrogate TRY from a COPC with a similar structure
was identified.
6. If no surrogate was available, a TRV was not listed. The potential toxicity of a COPC
with no 77? V should be addressed as an uncertainty (see Chapter 6)
Standard AQUIRE report summaries on tests were screened for duration, endpoint, effect, and
concentration. Studies were also screened for ecologically relevant effects by focusing on studies that
evaluated effects on survival, reproduction, and growth. Aspects of endpoint, duration, and test organism
in each toxicity study were evaluated to identify the most appropriate study. Several compounds, most
notably metals, had a large number of toxicity values based on various endpoints, organisms, and exposure
durations. In these instances, best scientific judgment was used to identify the most appropriate toxicity
value (see Chapter 5).
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
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Appendix E; Toxicity Reference Values _ August 1999
Chronic NOAEL-based values were not adjusted, but rather were carried through unchanged to become the
TRY. Toxicity values identified as "less than" a particular concentration were divided by 2 to represent an
average value because the true value is unknown, and it occurs between 0 and the noted concentration.
UFs discussed in Chapter 5 were applied to toxicity values not meeting TRY criteria.
Saltwater TRVs Saltwater TRVs are applicable to marine water bodies and estuarine systems with a
salinity greater than 5 ppt. Saltwater TRVs are listed in Table E-2. Saltwater water 77? V development
followed the same procedure as described above for freshwater receptors, except no GLWQI Tier n SCVs
were available. In addition, if no saltwater 37? V for a surrogate compound was available, the
corresponding freshwater TRY was adopted.
Freshwater Sediment TRVs Freshwater sediment TRVs are listed in Table E-3. They are applicable to
water bodies with a salinity less than 5 ppt. Freshwater sediment TRVs were identified from various sets of
screening values and ecotoxicity review documents. The lowest available screening values among the
following sources were identified:
1. No effect level (NEL) and lowest effect level (LEL) values from "Ontario's Approach to
Sediment Assessment and Remediation" (Persaud et al. 1993)
2. Apparent effects threshold (AET) values for the amphipod, Hyallela azteca, reported in
"Creation of Freshwater Sediment Quality Database and Preliminary Analysis of
Freshwater Apparent Effects Thresholds" (Washington State Department of Ecology
1994)
3. Sediment effect concentrations jointly published by the National Biological Service and the
U.S. EPA (Ingersoll et al. 1996).
If a screening value was not available in the sources listed above, toxicity studies and other values compiled
and reported by Jones, Hull, and Suter (1997) were reviewed to identify possible 77?Vs. Relevant studies
were prioritized based on the criteria listed in Chapter 5, and uncertainty factors were applied, as
applicable, based on criteria presented (see Chapter 5).
If a screening or sediment toxicity value was not available for an organic COPC, a freshwater sediment
77? V was computed, using the EqP approach (see Chapter 5), from the compounds corresponding
freshwater 77? V and KK value. The U.S. EPA Office of Water utilizes the EqP approach to develop
sediment quality criteria for nonionic (neutral) organic chemicals (U.S. EPA 1993). The EqP approach
assumes that the toxicity of a compound in sediment is a function of the concentration in pore water and
that to be nontoxic, the pore water must meet the surface water final chronic value. The EqP approach also
assumes that the concentration of a compound in sediment pore water depends on the carbon content of the
sediment and the compound's organic carbon partitioning coefficient (U.S. EPA 1993). A 77? V may be
calculated using the following equation (U.S. EPA 1993):
TRVsed = Koc ' foe • rav«, Equation E-l
where
TRVsed = Sediment TRV (|ag/kg)
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
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Appendix E; Toxicity Reference Values August 1999
Koc = Organic carbon partition coefficient (L/kg)
foc = Fraction of organic carbon in sediment (unitless)—default value = 4%
(0.04)
TRVm = Corresponding surface water TRY (ug/L)
Marine Sediment TRVs Marine sediment TRVs are listed in Table E-4. They are applicable to sediments
of marine water bodies and estuarine systems with a salinity greater than 5 ppt. Marine sediment TRVs
were developed following the procedures used to identify the freshwater sediment TRVs. Screening values
were compiled from the following sources:
1. No observed effect level (NOEL) sediment quality assessment guidelines for State of
Florida coastal waters (MacDonald 1993).
2. Marine and estuarine effects range low (ERL) values from "Incidence of Adverse
Biological Effects Within Ranges of Chemical Concentrations in Marine and Estuarine
Sediments" (Long et al. 1995)
3. ERL values from "The Potential for Biological Effects of Sediment-Sorbed Contaminants
Tested in the National Status and Trends Program" (Long and Morgan 1991)
4. Marine sediment quality criteria from "Sediment Management Standards" (Washington
State Department of Ecology 1991)
Screening values were adopted directly as 77? Vs. If a screening value was not available in the sources
listed above, toxicity values from a search of the scientific literature and those compiled and reported by
Hull and Suter (1994) were reviewed to identify possible TRVs. Original studies were obtained, where
possible, and toxicity values were verified. Relevant studies were prioritized based on the criteria listed in
Chapter 5, and uncertainty factors were applied, as appropriate, based on criteria (see Chapter 5). If a
screening or ecologically relevant sediment toxicity value from the scientific literature were not available
for an organic COPC, a marine sediment 77?V was computed, using the EqP approach, from the COPC's
corresponding saltwater TRVand Koc value (see Equation E-l).
Terrestrial Plant TRVs The terrestrial plant TRVs listed in Table E-5 are based on bulk soil exposures.
Available terrestrial plant toxicity values from the scientific literature were used to develop presented TR V
values. Toxicity values were first identified from the following secondary sources:
1. Studies cited in Toxicological Benchmarks for Screening Potential Contaminants of
Concern for Effects on Terrestrial Plants: 1997 Revision (Efrovmson, Will, Suter, and
Wooten 1997). Available studies were obtained and reviewed for accuracy of toxicity
values. UFs were applied depending on study endpoint and available information.
2. Toxicity values in the Phytotox database in U.S. EPA's ECOTOXicology Database
System. Available studies were obtained and toxicity values were verified. UFs were
applied depending on study endpoint and available information.
3. Toxicity values in U.S. EPA Region 5 Ecological Data Quality Levels (EDQL) Database
(PRC 1995). The database contains media-specific EDQLs for the RCRA Appendix IX
constituents (40 CFR Part 264). The EDQLs represent conservative media concentrations
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering E-4
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Appendix E: Toxicity Reference Values August 1999
protective of media receptors and wildlife that might be exposed through food chains based
in these media. Available studies were obtained and toxicity values were verified. UFs
were applied depending on study endpoint and available information.
Original studies were obtained, where possible, and prioritized based on criteria listed in Chapter 5.
Uncertainty factors were applied, as appropriate, based on criteria (discussed in Chapter 5) to develop TRY
values. For COPCs without toxicity data, the TRY for a surrogate COPC was adopted. If an appropriate
surrogate TRY was not available, no TRY value was identified. Generally, review of toxicity data available
in the scientific literature indicates that limited TRVs are available for organic compounds; while TRVs for
metals are available.
Soil Invertebrate TRVs The soil invertebrate TRVs listed in Table E-6 are based on bulk soil exposures.
Available soil invertebrate toxicity values from the scientific literature were used to develop TRVs for these
receptors. Soil invertebrate toxicity values were first identified from the following secondary sources:
1. Studies cited in Toxicological Benchmarks for Potential Contaminants of Concern for
Effects on Soil and Litter Invertebrates and Heterotrophic Process (Will and Suter n
1995a). Available studies were obtained and toxicity values were verified. UFs were
applied depending on study endpoint and available information.
2. Scientific literature was searched for toxicity values for outstanding compounds. Relevant
studies were obtained, toxicity values were verified, and UFs were applied as described
Original studies were obtained, where possible, and prioritized based on criteria listed in Chapter 5.
Uncertainty factors were applied, as appropriate, based on criteria to develop TRVs. If no toxicity value
was available for a COPC, the TRY for a surrogate COPC was adopted.
E-2.0 TRVs FOR WILDLIFE MEASUREMENT RECEPTORS
TRY values for wildlife measurement receptors are listed in Tables E-7 (mammals) and E-8 (birds). TRVs
were not developed for each avian and mammalian measurement receptor in the seven example food webs
because of the paucity of species-specific data. Rather, U.S. EPA OSW focused on identifying a set of
avian TRVs and a set of mammalian TRVs for the classes of compounds listed in Section 2.3. U.S. EPA
OSW assumed that, among the literature reviewed for a particular guild, the lowest available toxicity value
across orders in class Aves and across orders in class Mammalia would provide a conservative estimate of
toxicity. Available mammalian and avian toxicity values from the scientific literature were used to develop
TRVs for these receptors. Also, as previously noted, TRY values were not identified for amphibians and
reptiles because of the paucity of lexicological information on these receptors. Wildlife measurement
receptors TRV values were first identified from the following secondary sources:
1. Toxicity values compiled in Toxicological Benchmarks for Wildlife: 1996 Revision
(Sample, Opresko, and Suter 1996).
2. Toxicity values listed in the Terretox database of U.S. EPA's ECOTOXicology Database
System (U.S. EPA 1996b) were screened to identify studies potentially meeting the criteria
listed in Chapter 5.
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering E-5
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Appendix E; Toxicity Reference Values August 1999
Original studies were compiled, where possible, and reviewed to verify their accuracy based on criteria
listed in Chapter 5. In many cases, best scientific judgement was used to screen out studies with poor
experimental design (see Chapter 5). Uncertainty factors were applied, as appropriate, to develop TRVs
based on criteria presented in Chapter 5.
Conversions Some avian and mammalian toxicity data are expressed in terms of compound concentration
in the food of the test organism. To convert to daily dose, it is necessary to determine the exposure
duration and organism body weight. If the study does not report this information, the results should not be
used to compute a 77? V. If information on exposure duration and organism body weight is available,
dietary concentration can be computed to dose using the following generic equation:
C ' IR
DTI/ Equation E-2
BW
where
DD = COPCdose(mgCOPC/kgBW/day)
C = Concentration of COPC in diet (mg COPC/kg food)
IR - Food ingestion rate (kg/day)
BW = Test organism body weight (kg)
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering E-6
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Screening Level Ecological Risk Assessment Protocol
Appendix E: Toxicity Reference Values
August 1999
Efroymson, R.A., M.E. Will, G.W. Suter H, and A.C. Wooten. 1997. Toxicological Benchmarks for
Screening Contaminants of Potential Concern for Effects on Terrestrial Plants: 1997 Revision.
Oak Ridge National Laboratory, Oak Ridge, TN. 128 pp. ES/ER/TM-85/R3. November.
Ingersoll, C.G., P.S. Haverland, E.L. Brunson, TJ. Canfield, F.J. Dwyer, C.E. Henke, N.E. Kemble, D.R.
Mount, and R.G. Fox. 1996. "Calculation and Evaluation of Sediment Effect Concentrations for
the Amphipod Hyallela azteca and the Midge Chironomous riparius." International Association
of Great Lakes Research. Volume 22. Pages 602-623.
Jones, D.S., G.W. Suter n, and R.N. Hull. 7997. Toxicological Benchmarks for Screening Contaminants
of Potential Concern for Effects on Sediment-Associated Biota: 1997 Revision. Oak Ridge
National Laboratory, Oak Ridge TN. 34 pp. ES/ER/TM-95/R4. November.
Long, E.R., and L.G. Morgan. 1991. The Potential for Biological Effects of Sediment-Sorbed
Contaminants Tested in the National Status and Trends Program. National Oceanic and
Atmospheric Administration (NOAA) Technical Memorandum No. 5, OMA52, NOAA National
Ocean Service. August.
Long, E.R., D.D. MacDonald, S.L. Smith, and F.D. Calder. 1995. "Incidence of Adverse Biological
Effects Within Ranges of Chemical Concentrations in Marine and Estuarine Sediments."
Environmental Management. Volume 19. Pages 81-97.
MacDonald, D.D. 1993. Development of an Approach to the Assessment of Sediment Quality in Florida
Coastal Waters. Florida Department of Environmental Regulation. Tallahassee, Florida.
January.
Persaud, D., R. Jaaguagi, and A. Hayton. 1993. Guidelines for the Protection and Management of
Aquatic Sediment Quality in Ontario. Ontario Ministry of the Environment. Queen's Printer of
Ontario. March.
Sample, B.E., D.M. Opresko, and G.W Suter H. 1996. Toxicological Benchmarks for Wildlife: 1996
Revision. Oak Ridge National Laboratory, Oak Ridge, TN. 227 pp. ES/ER/TM-86YR3. June.
U.S. EPA. 1987. Quality Criteria for Water—Update #2. EPA 440/5-86-001. Office of Water
Regulations and Standards. Washington, D.C. May.
U.S. EPA. 1996a. ECOTOX. ECOTOXicology Database System. A User's Guide. Version 1.0. Office
of Research and Development. National Health and Environmental Effects Research Laboratory.
Mid-Continent Ecology Division. Duluth, MN. March.
U.S. EPA Region 6
Multimedia Planning and Permitting Division
Center for Combustion Science and Engineering
U.S. EPA
Office of Solid Waste
E-7
-------
Screening Level Ecological Risk Assessment Protocol
Appendix E; Toxicity Reference Values August 1999
U.S. EPA. 1996b. "Ecotox Thresholds." ECO Update. EPA 540/F-95/038. Office of Emergency and
Remedial Response. January.
U.S. EPA. 1999. National Recommended Water Quality Criteria-Correction. EPA 822-Z-99-001.
Office of Water. April.
Washington State Department of Ecology. 1991. Sediment Management Standards. Washington
Administrative Code 173-204.
Washington State Department of Ecology. 1994. Creation and Analysis of Freshwater Sediment Quality
Values in Washington State. Publication No. 97-32-a. July.
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering E-8
-------
Screening Level Ecological Risk Assessment Protocol
Appendix E; Toxicity Reference Values August 1999
TABLES OF TOXICITY REFERENCE (TRV) VALUES
Screening Level Ecological Risk Assessment Protocol
August 1999
E-l FRESHWATER TOXICITY REFERENCE VALUES E-ll
E-2 MARINE/ESTUARINE SURFACE WATER TOXICITY REFERENCE VALUES .. E-19
E-3 FRESHWATER SEDIMENT TOXICITY REFERENCE VALUES E-27
E-4 MARINE/ESTUARINE SEDIMENT TOXICITY REFERENCE VALUES E-34
E-S TERRESTRIAL PLANT TOXICITY REFERENCE VALUES E-42
E-6 SOIL INVERTEBRATE TOXICITY REFERENCE VALUES E-57
E-7 MAMMAL TOXICITY REFERENCE VALUES E-69
E-8 BIRD TOXICITY REFERENCE VALUES E-84
U.S. EPA Region 6 U.S. EPA
Multimedia Planning and Permitting Division Office of Solid Waste
Center for Combustion Science and Engineering E-9
-------
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and calculated as folio
m,. = 0.7852 and bc = -
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mc = 1.273 and bc = -4.705. Criterion was converted to dissolved
concentration using the following conversion factor: 1.46203-[(ln
hardness)(0.145712]. A assumed hardness of 100 mg/L and a
conversion from mg/L to /ug/L were used to calculate the displayed
value.
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concentration using a conversion factor of 0.997. A assumed
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used to calculate the displayed value.
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(Page 7 of 8)
FRESHWA
dized Procedure." Z. Wasser Abwasser Forsch. 15.
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REFERENCES
utants on Daphnia magna Straus
Toxic Action of Water Poll
"8
£
g
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Fish." Annals NewYork Academy of Sciences.
_c
in Relation to Disea!
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UH CA GO
^ £ £
•— >
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13
u
ihes." Journal of Hazardous Materials. Volume
VJ
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S
i to Fresh and Saltwa
13
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te Toxicity of 47 Industrial Chem
u
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2
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ai
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for the Evaluation of Acute Toxi<
iment of Bioassay Methods
h abstract).
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;, with Englis
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Reproduction Test." Water Research. Volume 23.
>>
Q
phnia magna in the 2
Q
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nful Effects of Water Pollutants tt
1989. "Results of the Harr
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988. "Toxicity and Bioconcentration of
'. Volume 7. Pages 47-62.
- C
il
Coyle, and W.J. Adai
I Toxicology and Che
-.- s
^ s
i, D.L. Stalling, G.M. DeGraeve,
in in Rainbow Trout." Environnu
ll, J.D. Petty, P.H. Petermai
7,8-Tetrachlorodibenzofura
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Potential Contaminants of Conce
me.
Benchmarks for Screening
Oak Ridge, Tennessee. Jv
Toxicological
il Laboratory.
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No saltwater data were available, therefore, corresponding
toxicity value was used (rainbow trout, Oncorhynchus myki
Mehrle et al. (1988). 2,3,4,5-TCDD toxicity value used.
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Rossi and Neff (1978) evaluated toxicity of three HMW (th
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LC50 of each HMW PAH exceeded 50 vgfL. This TRY she
assessing the risk of total HMW PAHs.
in
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Rossi and Neff (1978). Toxicity value for polychaete (N.
arenaceodentata).
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t or more of the test animals lifetime expectancy. Acute exposures represent single exposures or multiple
e following general guidelines were used. For invertebrates and other lower trophic level aquatic biota:
rom 3 to 6 days, and (3) acute duration lasted 2 days or less. For fish: (1) chronic duration lasted for more
duration lasted less than 2 weeks.
L TRV. See Chapter 5 (Section 5.4) of the SLERAP for a discussion of the use of uncertainty factors.
:or.
tations are provided at the end of this appendix.
;ction 5.4. 1 .2) for a discussion of the use of best scientific judgement. Factors evaluated include test
:ty of toxicity data.
in
U
1
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Lethal concentration for 100 percent of the test organisms.
Lowest Observed Effect Concentration
n n n
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Lowest Observed Effect Level
Lethal threshold concentration for 50 percent of the test organ
n n
W 8
35
No Observed Adverse Effect Level
No Observed Effect Level
n II
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< w
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Secondary Chronic Value
Toxicity Reference Value
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> >
0 g
vi H
cu
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TABLE E-2
ENCE VALUES
K
W
&
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^^
U
RINE/ESTUARINE SURFACE WATER TOXI
(Page 7 of 8)
<
S
REFERENCES
uatic Organisms." Environmental
O"
rs to Representative A
5
t Phthalate Esl
ti_.
d J. W. Gorsuch. 1995. "A Summary of the Acute Toxicity oi
. Pages 1569-1574.
§ 2
U
rS *o
•§>
"ft
11
S •«
oo U
11
03 ^
7; §>
Oi -S
d 8
-f i
R
c/r
1
'O
<
Diseases in Fish."
o
ts in Relation
I
13
1
"a
_o
JS
y
f^
s;
l-M
i
f
3
d
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bj*
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>'
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M^
^^
i-T
D
«
cu
£
'S
M
J
t-T
"c5
o
£
<£
H
*.
ed
W
c
I
ii
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the First 50 Multicentre Evaluation of I
78.
C4M ^1
ative Acute Toxicity o
Volume 26. Pages 65
£3
i1!
£ i
i|
ON g
.- s
98. Pages 535-546. Calleja, M.C., G. Persoone, and P. Gelad
: Non- Vertebrates." Archives of Environmental Contaminatio
CN .a
2 M
II
> 0
Y of Sciences. '
ity Chemicals t
s "
1 0
C n
" 1,
t°
o £
« 5
r
^
"S
g
•«;
ma/ of Hazardous Materials. Volume
a
Saltwater Fishes." Jo.
•a
As to Fresh an
3
id E. Rider. 1977. "The Acute Toxicity of 47 Industrial Chen
g
'%
o
•a
fi
Q
vi
.f
C
C 00
0> ^H
*""* f^l
J S
< s
•• «
»^' D
^ oe
- O3
0 a-
c£
o
Crt
S
03
Q
\ates)". Aquatic Toxicology and Risk
so
>ws (Cyprinodon varit
c
eepshead Min
w ^
atory Comparison of the Early Life-Stage Toxicity Test Using
Philadelphia, PA. Pages 354-375. As cited in AQUIRE 1991
s *•
.0 ts
(B T-I
IE
f5 00
a|
2^
i~
G -^
U>
^ W
d §
•o 5
C
!<§
w 5
'5
shiuchi. 1981.
54. (Japanese, \
2^
. t-~
> S
OI
T3 „
g 0
CS OB
- S3
> C1-
2 ^
"o
15
CA
rt
K
Ironmental Toxicology and Chemistry.
^
'athead Minnow." Ew
u-
o
J=
T3
g
«
1
.C
Dnic Toxicity of Di-n-butyl and Di-n-octyl Phthalate to Daphm
i
P
ui
oe
Whitmore. 19!
;s 167-179.
v 2P
A C4
_• cu
Q
•0 Tf
!l
U." —
j>°
H
y
u
s
icity and Bioconcentration of
7. Pages 47-62.
X u
J.Adams. 1988. "To
id Chemistry. Volumi
> 5
1. Coyle, and \
'al Toxicology
-> §
ith, J.D. Petty, P.H. Peterman, D.L. Stalling, G.M. DeGraeve,
3,7,8-Tetrachlorodibenzofuran in Rainbow Trout." Environm
E ..
5* rr.
•icity of 140 Substances to the Brown Shrimp and Other Marh
m-Crouch, Essex, and Fish Exp. Station Conway, North Wales
S T
Ex E
n
— m
r- .
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H
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Nl
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Federation. Volume 46. Pages 63-77.
ater Pollution Control
£
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1*.
2
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03
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. "Brine Shrimp Bioassay and Seawater BOD of Petrochemic
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%.«=•
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calculated
organic co
a "=3
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as!
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Volatile orgar
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using EqP
ntent of 0.
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a. a
11
2 "3
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ca
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1
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ca
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en
en
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using EqP
ntent of 0.
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11
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* §
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Formaldehyde
ca
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3
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using EqP
ntent of 0.
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1
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>
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S
—
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1
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1
1
2
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ca
60
c
'i
3
en
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1
1
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using EqP
ntent of 0.
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u "
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11
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cQ
O
^^
^^
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d
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u
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ca
Hexachlorobut
ca
00
c
E
3
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CQ
ca
/-^
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n
>— '
1
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&s
using EqP
ntent of 0.
O ^
^s W
J 00
ca k,
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en *-a
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11
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e
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cj
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Q
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gj
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-------
r •>
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u
Reference and Notes
"£
is Zl* /-^
4! ' *E
*j oi 1
«
fli
S
J
*
Bt
S
•+*
*i
£
•O
i
o
u
ca
993), assuming
as calculated using EqP approach (EPA 1
lal organic content of 0.04.
st *-•
f o
II
^.
8
00
r-f
o
c
1
.0
o
Pentachlor
<*-<
+^
c
i
i
o
ta
an AET value for H. azteca (Washington
j 1994).
.2 eg
> —
<-'
u
3
ca
u
1
ca
1
0
3
S
1
cd
1
_^
o
c
1
o
Pentachlor
^^
C
a.
Pesticides
-DDE used as a
an LEL value (Persaud et al. 1993). p,p*
w
1
>n
u
3
S
1
1
o
2
o
"g.
ca
1
W
Q
Q
u
en
S
S
JO
^3
^5
13
on
an NEL value (Persaud et al. 1993). The
i was available.
cfl ^J
la
en
O
u
3
S
t
ca
1
JB
u
1
ca
-5
Heptachloi
ca
993), assuming
as calculated using EqP approach (EPA 1'
lal organic content of 0.04.
* §
gj
H *
S
en
crT
VO
p
g"
(w
oo
00
00
u
c
!
n
Hexachlon
D£
"la
,§.
Inorganic:
>,
•0
00
tN
C
0
T3
O
en
ca
X!
1
an ERL value calculated by Ingersoll et a
:a toxicity tests.
•2 5;
> c
0
S
JJ
3
CB
U
1
Z
u
3
.§
"S.
a.
ca
1
Aluminum
1
8
m
Department of 1
an AET for H. azteca (Washington State
.S3
H 2
O
S
u
3
S
1
1
_o
3
ca
u
1
ca
-8
Z
Antimony
an LEL value (Persaud et al. 1993).
.2
^
p
0
2
a
1
ca
1
u
2
.a
"E.
o.
ca
1
Arsenic
1
1
^
w ^
„ a
classification oJ
nts for open wai
a U.S. EPA Region 5 guideline value for
irmining the suitability of dredged sedime
1, as cited in Hull and Suter H (1994).
v> H ca
III
8
U
3
S
1
CO
1
3
.§
"E,
o.
cd
I
Barium
:ory or toxicity value not available.
ca
1
u
1
I
1
tu
3
ca
u
1
1
_o
3
S
"I
cd
1
5
u
n
an LEL value (Persaud et al. 1993).
yi
|
0
u
3
u
1
1
0
2
s
I
I
|| Cadmium
o
en
-------
«
S
«
g
t^
•s
V)
u
ference and Notes
•g ^
§ fa **•*
** *O 53
^ >f
1* *
"s
"3
£
*!
|
4J
1
9-
•S
u
fa
•a
B
§
a
0
U
en"
2
'S
•u
TRY is an LEL value (Persau
8
JO
3
S
1
1
2
"a
u
•a
TRY is an LEL value (Persau
S
o
3
cd
O
1
%
U
2
s
I
2
IH
O,
U
1
*3
O Lj
"o g
O c
O O
'K S
C3 CA
"o S
guideline value for
r of dredged sedime
Suter 11(1994).
TRY is a U.S. EPA Region 5
for determining the suitability
disposal, as cited in Hull and
o
u
I
"E,
£
0
2
3
1
1
u
•o
'5
>,
r)
S
f
"3
•o
TRY is an LEL value (Persau
tn
JO
1
1
1
o
3
S
1
S
3
s §
U »-g
w >
1^
I~H ^"
>>.2
3 >•
" £H
S
divalent inorganic i
inorganic mercury.
No toxicity data available for
used as surrogate for divalent
(Persaud et al. 1993).
ON
Cg 1— 1
g t3
>> "2
kH 3
s te
E fe.
2 3
Jj
No toxicity data available for
surrogate for methylmercury.
r.
O
o
3
cd
1
1
JO
3
eg
U
1
1
>,
3
IM
O
s
^^
_c
o
f?
o\
"is
T3
TRY is an LEL value (Persau
— •
o
1
u
I
o
JO
3
s
1
1
'w
Z:
^
^2
1
"8
4->
c
u
E
13
&
Q
(Washington State
TRY is an AET for H. azteca
\ 1994).
o
u
1
3.
&
1
u
3
.2
1
I
£
3
'E
,
^
8
u
"8
^
B
U
I
!a
&
Q
(Washington State
TRY is an AET for H. azteca
1994).
•n
•*'
u
1
1
Z
JO
3
CO
o
"E,
&
1
S
33
alue not available.
Regulatory value or toxicity v
JO
3
ja
1
2
o
1
1
^
u
3
ctt
U
1
1
E
3
"3
•o
oc
IN
C
o
•o
u
cfl
S
^^,
I
.
ted by Ingersoll et a
TRY is an ERL value calculai
H. azteca toxicity tests.
o
-<
JO
3
2
1
1
u
3
S
1
2
u
s
CO
n
-------
1
'>
a
O
*
V
ec
is per kilogram (,wg/kg) and milligrams per kilograms (mg/kg) for organic and inorganic constituents, respecti
Coc = Organic carbon normalized sorption coefficient. References and equations used to calculate K^. values
RV was identified. Complete reference citations are provided below.
3wing equation:
|^
If
S '"*'
*1 S
o S
reference values are in units
ire in units of liters per kilogr
.t2 so
O 4>
*rp _^
o a
H >
H
u
r«
i
IS
x A.
rences refer to the study from
*•-• a}
o u
n. u
O. JC
< H
2
u
•5
5
ter sediment TRV calculated
eg
JB
W
U.
TRV (Table E-1)* K,,c * foc,bs
S
cd
j=
o
£
Freshwater sediment TRV =
xiefficient, and
m in bed sediment, assumed to be 4 percent = 0.04.
— o
11
la •-
a. i
C M
o b
where,
K,,;. = organic carb
fOT bs= fraction of c
><
•3
c
u
1
c
CO
S
o
CO
•3
CO
U
~a
Apparent Effects Threshold
n
1
if
OJ
a
n
Equilibrium Partitioning
n
High molecular weight
Lowest Effect Level
u n
£
J3
ts
S
a
o
II
Toxicity Reference Value
n
u
-------
w u
S *
I e
H H
I
REFERENCES
lala
ill!
1-8 8
1 S j§g
O 3 3 U
" ca " u
S * 1 &
"S j_» ro ^-
TO •£; A ^
* S 5* «
•C C * 00
CA C IH e
S S .2 -8
•Sill
s 2>l s
0 .S > «
o, fc >> _e?
?* 3 -s s
"S ^ 'S 2
§^-2 g
S-TS £ "
E h 3 op
p 3 a s
^ cs r^u *s
«\ c cd 5
O C TO Q
8 'S S 2
O *j C
« U en H
= 2 1 |
£ a -2 £
fe J3 . 3
^- *- co -S
00 -g fe
3:' .S - =
ll 3-3
S § TS g1
.O ^_> S* U
•a 2 i; .»
S •% ° <
C X CA (V
1 § !&
a.-5 S g>
& *^ CA S
o, S^ o "5
the three sets of freshwater toxicity value;
aes were not used because of the compexi
xicity to benthic invertebrates. Among th
torn the corresponding freshwater TRV u
ivater habitats were identified from
ific literature, available toxicity vali
e, and organic carbon content) in to
tses, a default TRV was calculated 1
^ -r~; Q. TO
1 §££
l~ •« .« r;
* ^ -5 «
.£ " C
i2 ** -a A
g .s|
£ co 3 >
•|s "i ^
w rs -^ ID
fe 5 § -B
£ rt £ »> ~
"o
w ^
T3
§ -s
c ^
1 §
•3 S
rt S
3 ^
0 i,
?i
£ 1
2$
. 'fe
>< 6*
«2|
o .§
o« ^
«l
C8 "
, C.E. Henke, N.E. Kemble, D.R. Mount,
ge Chironomous riparius." International
Brunson, T.J. Canfield, F.J. Dwyer
ihipod Hyallela azteca and the Mid,
H|
flj <
- 0)
•§5
CO LH
— S
il *
u
>• c«
CO C
K •§
W3 S
oi s
ori
uc5
"S
S
co
&
u
c
'£
e«
"e
u
u
a
1
u
S
1
u
5
<4-H
o
^
t-l
03
*s
§
o
"i
1
o
8
6
-S
&•
'c
O)
c
ection and Management of Aquatic Sedim
ton. 1993. Guidelines for the Prat
>,
£
<
"§ .e
3 u
* 1
'&S
a.
c
§ '3
i— i s
*£
Q "5
•a
3
cs
CV3
,8
g
1
£
«5
4
1
00
S
5
o
^,
*
S
a
Oo
£?
O
_tj
•s
c
u
03
"$>
S
_o
1
g
a;
1
^
la for Nonionic Organic Contaminants fo
r Deriving Sediment Quality Criten
R-93-011. September.
.t§
1^
— BJ
c
.§ c
c u
•s |
r
-------
en
U
z
u
w
J
CO
$
00
V
I
Reference and Notes c
•8 Hi
flS S3 ^^ "3
« p* *
<» H
u
S
1
>•
tJ
1 ».
"§ •-
3 £ •
| gg
£ *c
S »5
S
T3
a
1
S
u
^
2P
M
3
6C
e
1
"?
|
V
^o
*o
•a
1
S™*
2
1
a.
TRV was calculated using EqP approach (EPA 1993
assuming a fractional organic content of 0.04. d
^
d
C*}
!3
5\
VD
oo
tn
§
d
g
u
H
oe
rn
3
S
•<
ft,
**i^
en
03
5
fc-
£
_o
*rf
a
S
£
ce
i.
es
V
^J
1
"o
p.
^ VI
Recommended NOEL for Florida Department of
Environmental Regulation (DER) (MacDonald 1993
This TRV may be used in risk of total HMW PAHs i
assessed.
^
OO
jQ
•4-* A
O O
*!
2
S
1
S
Z
^T1
5
CU
£^*
^1
a
tii.
«
eo
'S
^
ra
"3
0
42
i
^*
.2?
"s
^
o\
Recommended NOEL for Florida DER (MacDonald
o
C*4
o
JTi
'S S
*1
—
CS
U
1
s
z
u
c
u
£,
jx
re
¥
g
03
^
§\
Recommended NOEL for Florida DER (MacDonald
S
J^l
"S S
zl
S
s
"S.
s
Z
fti
C
o
1
J2,
c
u
n
TRV was calculated using EqP approach (EPA 1993
assuming a fractional organic content of 0.04.
I
oo"
^
oo
d
s
r"
'c
2
O
•3
e
^
S
n
TRV is a LEL value from Persaud et al. (1993).
0
O"4
3
3 S
z'l
o
3
S
1
0
z
0
c
•£
c
I
^v
^
I
C
u
n
ff>
S
Recommended NOEL for Florida DER (MacDonald
C*J
_o
JO
« s
^ 12
1
*2
2
1
o
Z
c
a
f
U
^
1
Recommended NOEL for Florida DER (MacDonald
CO
2
3 S
2|
u
3
S
1
C3
Z
u
c
-------
u
z
u
0!
H
H
J
3
H
00
v
J
5
Reference and No
« £®
nil
«£ *
1
13
>
tJ
1*
|||
"i 3
SM
•a
|
S
o
U
3
S
fe.
c
u
5"
*c
•e
«
£
"C
0
I
•3
&.
"3
o
on
S
1
•alue for Total PCB 1
^
2
w
c
ii
r-
S
V
3
3 S
1
u
23
en
u
I
z
0
1— i
Aroclor
o
|
A
•alue for Total PCB i
^
5
W
C
ii
f;
JS
'o S
3* -— •
1
o
id
u
^
es
^^
Aroclor
^^
^«.
K
i
o
1 Nitroar
en
2
S- o
•6 «s
ted using EqP appro
onal organic content
CQ *rt
11
u ca
TRY was
assuming
p
VO
o
oo
o
c
o
c
1
*-
'c
Q
en~
2
ll
ted using EqP appro
onal organic content
W *rj
"3 ^
o ca
TRY was
assuming
00
>r>
^
»/^
R
m
u
c
u
3
"3
o
*-
'c
S
4
^
o\
II
•S "s
ted using EqP appro
onal organic content
— -5
o 2
S a
TRY was
assuming
i
VO
°1
*— '
R
u
c
"3
o
*^
'E
5
vq
of
en
2
S d
1*8
ted using EqP appro
onal organic content
CO *^*
1|
3 ed
TRY was
assuming
o
00
en
o\
^
00
u
c
u
r~.
Nitrobei
x
o\
ii
1o
ted using EqP appro
onal organic content
cd **^
||
u ed
TRY was
assuming
vo
en
§
oo
I/I
O
ID
C
(D
R
O
o
1
o
Pentach
W
-------
U
w
00
fO
Reference and Notes c
.iii
* J sT -2°
w H *
|
^
^£
V
S u
C8 ^N
3 I? «
^ « ^
^> w ^!
C 5
"C g
S CO
•g
i
i
5
u
^
^
ok
^
^— "
t
a>
en
jlj
_«
SJ
A
£
TRY was calculated using OC-based marine sediment
quality criterion from Washington State Department of
Ecology (1991) and fractional organic carbon content of
0.04, as follows:
TRY = 47 mg/kg * 0.04 * 1000 /^g/mg.
o
S
D.
CO
0
£
8
"E.
D.
ca
O
1
"a
^2
r~t
CL.
^
X
-C
^t
.c
V
d
en
m
TRY was calculated using OC-based marine sediment
quality criterion from Washington State Department of
Ecology (1991) and fractional organic carbon content of
0.04, as follows:
TRY = 58 mg/kg * 0.04 * 1000 //g/mg.
o
oo
•n
0
||
ro
4>
2
§
"5.
a.
a
S
o
^d
"3
^
-a
"5-,
*^
g
•^
Q
3
*e
G
n,
£
0
u
u
C
3i
o
&
!Z>
"3
^
TRY was calculated using EqP approach (EPA 1993),
assuming a fractional organic content of 0.04. d
00
00
s
o
f *
ts
o
c
c
1
TRY was calculated using EqP approach (EPA 1993),
assuming a fractional organic content of 0.04.
00
oo
06
ts
cs
I
JU
i-4
C
JD
*
TRY was calculated using EqP approach (EPA 1993),
assuming a fractional organic content of 0.04.
oo
0
Tl
§0
T— 1
S
>-
£
o
o
S
No TRY was calculated because no Koc or Kow value was
identified.
•a
o
jo
1
!S
ts
z
f«1
^^
I)
•o
J3
•a
CS
c
o
*-i
8
TRY was calculated using EqP approach (EPA 1993),
assuming a fractional organic content of 0.04.
00
s
g
d
•^
\c
C
re
c
.S
Q
-
TRY was calculated using EqP approach (EPA 1993),
assuming a fractional organic content of 0.04.
ts
!/•>
VO
N
vq
^£
Cl
|
HJ
-a
ra
£
1
-------
Reference and Notes c
^g,^
•g J ^-§
K S
01 H
U
s
• 41
Is
tf *"*
3 5 •
| s|
•c 1
•B
§
a.
g
ij
TRY was calculated using EqP approach (EPA 1993),
assuming a fractional organic content of 0.04. d
f;
J^
-.
^
oo
oo
rn"
2
^
j^
^
3
^^
M
a
b
'v
V
'S
"C
_o
*«
u
u
X
O
TRY was calculated using OC-based marine sediment
quality criterion from Washington State Department of
Ecology (1991) and a fractional OC content of 0.04, as
follows: TRY = 0.38 mg/kg * 0.04 * 1000 Mg/mg.
vi
*""*
u
-1
0 0
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REFERENCES
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. Suter n. 1994. Toxicological Benchmarks for Screening Contaminants of Potential
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e, Florida. January.
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