census data for crop production at the same county level of resolution.
The product is a listing of federally listed species that are located
within counties known to produce the crop upon which the pesticide will
be used.  Because the Level I screening assessment considers both direct
and indirect effects across generic taxonomic groupings, it is not
possible to exclude any taxonomic group from a LOCATES database run for
a screening risk assessment.

Because chloropicrin is registered for preplant use on all
“terrestrial food crops” (as well as ornamental and other sites),
essentially all use sites from LOCATES would have to be selected.  As
indicated above, for a screen for both direct and indirect effects, all
taxonomic groups would also have to be selected.  Thus, a printout would
essentially include all known federally-listed species for all taxonomic
groups in all counties with agriculture.  If the registrants are able to
limit labels to a more narrow set of crops, a more narrow set of
counties and species can be developed.  If this is not done, the
species-specific analysis will have to include virtually all known
federally-listed species for all taxonomic groups in all counties with
agriculture.

The registrants must provide information on the proximity of
federally-listed mammals, birds, fish, aquatic invertebrates,
terrestrial invertebrates, and plants to the registered use sites.  This
requirement may be satisfied in one of three ways: 1) having membership
in the FIFRA Endangered Species Task Force (Pesticide Registration [PR]
Notice 2000-2); 2) citing FIFRA Endangered Species Task Force data; or
3) independently producing these data, provided the information is of
sufficient quality to meet FIFRA requirements.  The information will be
used by the OPP Endangered Species Protection Program to develop
recommendations to avoid adverse effects to listed species.

V. Literature Cited  TC \l1 "V. Literature Cited

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CARB (California Air Resources Board).2005. Report for Air Monitoring
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CARB (California Air Resources Board). 2003a. Ambient Air Monitoring for
Chloropicrin and Breakdown Products of Metam Sodium in Kern County ,
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Carr, R. S.  1987.  Memorandum: 71 pp. (ECOTOX Reference #17308).

CDC (Center for Disease Control). 2004. Brief Report: Illness Associated
with Drift of Chloropicrin Soil Fumigant into a Residential Area -- Kern
County, California, 2003. Morbidity and Mortality Weekly Report. Aug.
20, 2004. 53:740-742.   HYPERLINK
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the period of January 1, 2003 through June 30, 2003. CEPA Dept. Of
Pesticide Registration, Sacramento,    HYPERLINK http://
http://www.cdpr.ca.gov/docs/canot/ca03-4.htm

CEPA (California Air Resources Board). 2003b. Report for Air Monitoring
Around a Bed Fumigation of Chloropicrin Fall 2001.  California
Environmental Protection Agency Air Resources Board, Sacramento, Ca. htt
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http://www.cdpr.ca.gov/docs/empm/pubs/tac/studies/chlrpicrin.htm
p://www.cdpr.ca.gov/docs/empm/pubs/tac/studies/chlrpicrin.htm

Chickos J.S. and W. E. Acree. 2003. Enthalpies of vaporization of
organic and organometallic compounds. 1880-2002. J Phys Chem Ref Data
32: 519-853.

Ecotoxnet. 2001. Chloropicrin.   HYPERLINK
http:/pmep.cce.cornell.edu/profiles/extoxnet/carbaryl-dicrotophos/chloro
picrin.
http:/pmep.cce.cornell.edu/profiles/extoxnet/carbaryl-dicrotophos/chloro
picrin.

Fuller, E. N., P. D. Schettler and J.C. Giddings. 1966. A new method for
prediction of binary gas-phase diffusion coefficients. Ind Eng Chem 58:
19-27.

Gan, J., S.R. Yates, F.F. Ernst, and W.A. Jury. 2000. Degradation and
volatilization of the fumigant chloropicrin after soil treatment. J.
Environ. Qual. 29:1991-1397.

Grosjean, D. 1991. Atmospheric chemistry of toxic contaminants. Four
saturated halogenated aliphatics:methyl bromide, epichlorohydrin,
phosgene. J Air Waste 1:56-61.

Helas, G. And S. Wilson, 1992. On sources and sinks of phosgene in the
troposphere. Atmos. Envir. 26A:2975-2982

Kawamoto, K. and K. Uraro. 1989. Parameters for predicting fate of
organochlorine pesticides in the environment (II) Adsorption constant to
soil. Chemosphere 19: 1223-1231.

Kollman, W.S. 1990. Literature review of the Environmental Fate of
Chloropicrin. Memorandum to R.S. Segawa, Environmental Hazards
Assessment Program , California Dept. Of Food and Agriculture. 9 pp.

Lee, S., R. McLaughlin, M. Hardly, R. Gunier, and Richard Kreutzer.
2002. Community Exposures to Airborne Agricultural Pesticides in
California: Ranking of Inhalation Risks. Environmental Health
Perspectives. 110:1175 - 1184.

Maddy, K.T., D. Gibbons, D.M. Richmond, and A.S. Fredrickson. 1983. A
study of the levels of methyl bromide and chloropicrin in the air
downwind from a field during and after a preplant fumigation (shallow
injection) - a preliminary report. CDFA, Division of Pest Management,
Environmental Protection and Worker Safety, Worker Health and Safety
Unit. Report No. HS-1061

Maddy, K.T., D. Gibbons, D.M. Richmond, and A.S. Fredrickson. 1984.
Additional monitoring of the concentrations of methyl bromide and
chloropicrin in the air downwind from a field during and after a
preplant fumigation (shallow injection) - a preliminary report. CDFA,
Division of Pest Management, Environmental Protection and Worker Safety,
Worker Health and Safety Unit. Report No. HS-1183

Manoque, W. And R. Pigford. 1960. The kinetics of the absorption of
phosgene into water and aqueous solutions. A.I. Ch. E, Journal
6:494-500.

Merck Index - Encyclopedia of Chemicals, Drugs and Biologicals.
Budavari, S (ed.).  Rahway, NJ; Merck and Co., Inc., 1989. 333.

MRID# 05007865. Moilanen, K.W., D.G. Crosby, J.R. Humphrey, and J.W.
Giles. 1978.  Vapor phase photodecomposition of chloropicrin
(trichloronitromethane).  Tetrahedron. 34:3345-3349.

MRID# 42900201. Moreno, T., and H. Lee.  1993.  Photodegradation of
chloropicrin.  Laboratory Project ID: BR 389.1:93.  Unpublished study
performed by Bolsa Research Associates, Inc., Hollister, CA, and
submitted by Chloropicrin Manufacturers Task Force.

MRID# 43022401. Chang, T. 1989.  Hydrolysis study with chloropicrin as a
function of pH at 25̊C.  Laboratory Project ID.: B.R. 51:89.
Unpublished study performed by Bolsa Research Associates, Hollister, CA,
and submitted by The Chloropicrin Industry Panel, West Lafayette, IN

MRID# 43085101. Ivancovich, A.  1987.  Chloropicrin - Field dissipation
study.  Laboratory Project ID: BR11:87.1.  Unpublished study performed
by Bolsa Research Associates, Hollister, CA, and submitted by the
Chloropicrin Industry Panel.

MRID# 43613901 Hatton C., K. Shepler, and L. Ruzo.  1995.  Aerobic soil
metabolism of [14C]chloropicrin.  PTRL Report No.:  448W-1.  PTRL
Project No.:  448W.  Unpublished study performed by PTRL West Inc.,
Richmond, CA; and submitted by Chloropicrin Manufacturers Task Force,
c/o Niklor Chemical company, Long Beach, CA.

MRID# 43759301. Hatton, C., K. Shepler, and L. Ruzo.  1995.  Anaerobic
aquatic metabolism of [14C]chloropicrin.  PTRL Report No.:  449W-1.
PTRL Project No.:  449W.  Unpublished study performed by PTRL West,
Inc., Richmond, CA; and submitted by Chloropicrin Manufacturers Task
Force, c/o Niklor Chemical Company, Long Beach, CA.

MRID# 43798601. Skinner, W., and N. Jao.  1995.  Laboratory volatility
of [14C]chloropicrin.  PTRL Report No.:  450W-1.  PTRL Project No.:
450W.  Unpublished study performed by PTRL West, Inc., Richmond, CA; and
submitted by The Chloropicrin Manufacturers Task Force, c/o Niklor
Chemical Company, Long Beach, CA.

MRID# 44191301.  Skinner, W.  1996.  Soil column leaching of
[14C]chloropicrin in four soil types.  PTRL Report No.:  587W-1.  PTRL
Project No.:  587W.  Unpublished study performed by PTRL West, Inc.
Richmond, CA; and submitted by The Chloropicrin Manufacturers Task
Force, c/o Niklor Chemical Company, Long Beach, CA.

NASS (National Agricultural Statistics Service) 2005. Year 2002 Usage
statistics for chloropicrin   HYPERLINK
http://www.pestmanagement.info/nass/
http://www.pestmanagement.info/nass/

Pe4 Shell.  2004.  Environmental Fate and Effects Division, Office of
Pesticide Programs, U.S. Environmental Protection Agency, Washington,
D.C.  Information downloaded from the website   HYPERLINK
http://www.epa.gov/oppefed1/models/water/
http://www.epa.gov/oppefed1/models/water/

Sadtler Research Laboratories.1980. Standard Spectra Collection. Sadtler
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Philadelphia, Pa.

Scheer, V., A. Frenzel, W. Behnke, C. Zetzsch, L. Magi, Ch. George, and
Ph. Mirabel. 1997.Uptake of Nitrosyl Chloride (NOCL) by Aqueous
Solutions. J. Phys. Chem. 101:9359 - 9366.

Selala, M., et. al.  1989.  An improperly labeled container with
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42: 202-208.

Singh H.B. 1976. Phosgene in the ambient air. Nature. 264:428-429.

Shorter, J.H., C.E. Kolb, and P.M. Crill. 1995. Rapid Degradation of
Atmospheric Methylbromide in Soils. Nature. 377:717-719.

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VI. Appendices  TC \l1 "VI. Appendices

	Appendix A.  Environmental Fate and Transport Data  TC \l2 "Appendix A.
 Environmental Fate and Transport Data

161-1 Hydrolysis (MRID# 43022401)

Chloropicrin, at approximately 100 ppm, did not hydrolyze in sterile
aqueous buffered solutions adjusted to pH 5, 7, and 9, that were
incubated in the dark at 25̊C.During the 28 day study, chloropicrin
ranged from 106.4 to 113.8 ppm in the pH 5 acetate buffer solution, from
97.3 to 113.7 ppm in the pH 7 phosphate buffer solution, and from 101.6
to 111.1 ppm in the pH 9 phosphate buffer solution.  No pattern of
decline was noted in any set of samples.  In all samples, inorganic
chloride was <1.5 ppm.  The pH of the buffer solutions remained stable
throughout the study.

161-2	Aqueous Photolysis (MRID# 42900201)

This study provides very limited supplemental information.  A new study
is required. However, the study provides some information about the
nature of the photolysis products of chloropicrin.  Major problems were
found in this study related to the material balance.

Chloropicrin, at 164 mg/L, photodegraded with a registrant-calculated
half-life of 31.1 hours (1.29 days) in sterile aqueous solutions
buffered at pH 7 at 25̊C, irradiated with a xenon arc lamp (at about
twice the intensity of natural sunlight in April in Hollister,
California) on a 12 hour photoperiod.  In contrast, the dark controls
did not appear to hydrolyze substantially during the test period.

                           hv

CCl3NO2    --------------------->    3Cl-     +     NO2-      +
NO3-       +        CO2         +        H+

                           H2O
                                   (HCO3- + CO22-)

Chloride increased to up to 0.00240 M (80%) after 108 hours.  CO2
increased to up to 0.000143 M (14.3%) after 108 hours.  The bicarbonate
ion increased to 0.000573 M after 108 hours.  Other products were
nitrate and nitrite, at maximum of 0.000347 M and 0.000143 M, at 108
hours, respectively.  The chloride ion reached 0.00205 M after 108
hours.

161-3 Photodegradation on Soil (Waived)

This study was waived because chloropicrin is used by soil injections,
therefore, no substantial soil photolysis is expected.

161-4 Photolysis in Air (MRID# 05007865)

The photolytic half-life of chloropicrin vapor is about 20 days at
25-30̊C.  The photolysis rate decreased markedly after 20 days.  The
photodegradation appears to be dependent on the presence of oxygen.  The
initial photoproducts and the incorporation of 18O2 suggest an
intramolecular rearrangement involving the trioxazole N-oxide as an
intermediate.  In the dark control, the concentration of chloropicrin
decreased slightly over 70 days.

Chloropicrin vapor is readily photodegraded to phosgene (COCl2) and
nitrosyl chloride (NOCl) under simulated sunlight.  COCl2 is not further
degraded, but NOCl subsequently is photodegraded to nitrous oxide (NO)
and chlorine (Cl2).  A portion of the NO is oxidized to nitrogen dioxide
(NO2) and dinitrogen tetraoxide (N2O4).

A degradation pathway was postulated by the registrant:  In nitrogen
atmosphere, chloropicrin was stable to irradiation, indicating that O2
is required for photodecomposition, and suggesting that an intermediate,
trioxazole N-oxide, was involved, that decomposes to COCl2, NOCl, and
O2.

162-1 Aerobic Soil Metabolism (MRID# 43613901)

This aerobic soil metabolism study is scientifically valid and provides
useful information on the aerobic soil metabolism of chloropicrin.  The
study is acceptable as it followed the previously approved protocol for
the data requirement.  No new study is required.The  registrant is
required to address the following problems found in the study:

	Maintenance of aerobic conditions and moisture at the water holding
capacity (WHC) throughout the experiment;

	Effects of chloropicrin on soil viability;

	Location of the PUF trap in relation to the KOH trap; and

	The target thickness, in inches, of the soil to be treated in th field
and its vertical location in the soil profile.

[14C]chloropicrin, at nominal application rates of 310-329 ppm, or
equivalent field rates of nearly 550-600 lb a.i/acre, degraded in the
laboratory with calculated half-life of 8 to 11 days in Baywood sandy
loam soil adjusted to 78% of 0.33 bar moisture and incubated in the dark
at 25±1oC for up to 21 and 24 days.

The study was performed using three samples sets which were not treated
at the same rate or incubated simultaneously.  The study indicates that
biotic transformation into CO2 is the most important process that had
governed the fate of chloropicrin under the stated laboratory
conditions. Initially, parent escaped biodegradation by volatilization
but later was subject to biodegradation and to binding, into the soil,
in a non-extractable form.

Evolved 14CO2 increased to 72.2% at 24 days posttreatment.
Chloronitromethane, nitromethane, and bicarbonate were the only three
minor degradates identified (a total of <6% of the applied
radioactivity).  Degradates were formed by substitution of Cl by H and
were mainly detected in association with the soil in extractable and
later in nonextractable forms.

This aerobic soil study was conducted without supplying the system with
continuous flow to remove volatile materials. This type of system do not
closely mimic field condition where volatilized materials are relatively
free to escape.

Reexamination of the study results reveals that volatilization, in the
soil environment, will be the major dissipation route of chloropicrin.
Due to the fact that volatilization is significant and occurs rapidly,
the importance of other competing processes such as leaching,
biodegradation, and adsorption to the soil particles will certainly
depend on expected field volatility. This is because volatility
determines the amount of chloropicrin left for other processes and its
residence time in the soil system.

162-3 Anaerobic Aquatic Metabolism (MRID# 43759301, supplemental)

This study provides useful supplemental information about the anaerobic
aquatic metabolism of chloropicrin.  The study does not meet Subdivision
N Guidelines for the fulfillment of EPA data requirements for the
following reasons:

	The test water was not representative of that found at an intended use
site (purified deionized water was utilized to flood the soil samples).

	The analytical methods were inadequate for the characterization of
residues in water samples removed at later sampling intervals.  The HPLC
column recoveries for the water phase samples were 103-104% at 0-1.5
hours posttreatment, decreased to 83.6% by 5 days posttreatment, and
were 24.1% at 54 days posttreatment.  The study authors did not provide
an explanation for this decrease.

Radiolabeled [14C]chloropicrin, at a nominal application rate of 313 ±
14.4 µg/g, degraded with a calculated half-life of 1.3 hours (r2 = 1.0;
0- to 4-hour data only) in anaerobic flooded sandy loam soil that was
incubated in darkness at 25 ± 1̊C for up to 54 days.

All data are reported as percentages of the nominal application.
Degradate data are reported in parent equivalents.  The parent was
initially present in the total soil/water system at 96.3% of the applied
radioactivity, decreased to 45.5% by 1.5 hours and 11.2% by 4 hours, was
1.7-2.2% at 1-2 days, was not detected from 5 to 12 days, and was last
detected at 0.1% (one of two replicates) at 26 days posttreatment.  The
parent was mostly associated with the water phase.

The major degradate nitromethane was a maximum of 53.4% at 1 day, and
was last detected at 16.9% (one of two replicates) at 26 days
posttreatment.

The major degradate chloronitromethane increased to 51.5% by 4 hours,
and was last detected at 0.1% (one of two replicates) at 54 days
posttreatment.

Nonextractable [14C]residues increased to a maximum of 32.0% at 54 days
posttreatment; [14C]residues associated with the fulvic and humic acid
fractions were 24.4% and 1.3% of the applied, respectively, at 54 days
posttreatment.

[14C]Volatiles in the KOH traps reached 45.7% at 54 days posttreatment.
Based on BaCl2 precipitation of KOH traps, evolved 14CO2 accounted for
4.1% at 54 days posttreatment.

[14C]Organic volatiles were a maximum of 8.8% of the applied
radioactivity at 1.5 hours, were 2.5-4.9% at 1-5 days, and were 0.6% at
54 days posttreatment.  Based on HPLC analysis of the foam plug extract,
the parent accounted for 8.1% of the applied radioactivity at 1.5 hours
and was 1.1-1.8% at 1-2 days posttreatment.  Radioactivity in the
headspace was 10.9% of the applied radioactivity at 1.5 hours and was
0.1-0.7% at 1-54 days posttreatment; the parent accounted for 10.7% of
the applied at 1.5 hours posttreatment.

163-1 Mobility - Column Leaching (MRID# 44191301)

This study is considered acceptable and it meets Subdivision §N
Guidelines for the fulfillment of the mobility data requirement (column
leaching) of chloropicrin.  However, data were variable for the silty
clay loam soil and the loamy sand soil, precluding definitive mobility
determinations for the compound in those soils.

The column leaching of [14C]chloropicrin, at a nominal rate equivalent
to 345 lb/A or 362 lb/A was studied in sandy loam, loamy sand, silt
loam, and silty clay loam soil columns which were leached with CaCl2
over a period of 17-138 hours, 1-1.5 hours, 126-132 hours, and 101-116
hours, respectively.  Based on the results of this study, it was
observed that chloropicrin is very mobile in all four soils tested.

In the Baywood sandy loam soil, most of the [14C]residues retained in
the soil column following leaching were detected in the 30- to 36-cm
(4.6%), 36- to 42-cm (5.7%), and 42- to 48-cm (5.7%) depths.  The parent
was 4.0% of the applied radioactivity in the 12- to 24-cm depth (12- to
18-cm and 18- to 24-cm depths combined), was 6.9% in the 24- to 36-cm
depth (24- to 30-cm and 30- to 36-cm depths combined), and was 11.2% in
the 36- to 48-cm depth (36- to 42-cm and 42- to 48-cm depths combined).
The minor degradates dichloronitromethane, and nitromethane were
detected once each.  Nonextractable [14C]residues were 1.0% of the
applied radioactivity in the 12- to 18-cm depth, and were 0.4-0.5% in
each of the 18- to 24-cm, 30- to 36-cm, 36- to 42-cm, 24- to 30-cm, and
42- to 48-cm depths.  Total [14C]residues in the leachate solution were
30.8% of the applied radioactivity.  The parent was 17.2% of that
radioactivity; the minor degradates dichloromethylhydroxylamine,
dichloronitromethane, and nitromethane were ≤7.3% of the applied
radioactivity.  [14C]Organic volatiles (bottom of the column) were 32.8%
of the applied radioactivity; the parent accounted for 32.4% of the
applied.

In the Baywood loamy sand soil, most of the [14C]residues retained in
the soil column following leaching were detected in the 12- to 18-cm
(22.6%) depth.  The parent was 36.6% (two of three columns) of the
applied radioactivity in the 12- to 24-cm depth (12- to 18-cm and 18- to
24-cm depths combined) and was 8.6% (two of three columns) in the 24- to
48-cm depth (24- to 30-cm, 30- to 36-cm, 36- to 42-cm, and 42- to 48-cm
depths combined).  Degradates were not detected.  Nonextractable
[14C]residues were 0.1% of the applied radioactivity in each of the 18-
to 24-cm, 24- to 30-cm, 30- to 36-cm, 36- to 42-cm, and 42- to 48-cm
depths. Total [14C]residues in the leachate solution were 43.7% of the
applied radioactivity.  The parent was 42.7% of the applied
radioactivity.  The minor degradates dichloronitromethane and
dichloromethyl hydroxylamine were each ≤0.77% of the applied
radioactivity.  [14C]Organic volatiles (bottom of the column) were 12.2%
of the applied radioactivity; the parent accounted for 12.2% of the
applied.

In the Congaree silt loam soil, most of the [14C]residues retained in
the soil column following leaching were detected in the 36- to 42-cm
(6.6%) and 42- to 48-cm (6.9%) depths.  The parent was 0.1% of the
applied radioactivity in each of the 12- to 30-cm (combined), 30- to
42-cm (combined), and 42- to 48-cm depths.  The minor degradates
dichloromethylhydroxylamine, dichloronitromethane, and nitromethane were
detected at ≤0.1% of the applied radioactivity.  Nonextractable
[14C]residues were 0.4% of the applied radioactivity in the 6- to 12-cm
depth, were 2.5-4.5% in each of the 12- to 18-cm, 18- to 24-cm, and 24-
to 30-cm depth, and were 5.0-5.7% in each of the 30- to 36-cm, 36- to
42-cm, and 42- to 48-cm depths; [14C]residues associated with the humic
acid, fulvic acid, and humin fractions of a selected soil column were
0.19-0.38%, 0.94-2.8%, and 1.9-4.1% of the applied, respectively, in
each of the 12- to 18-cm, 18- to 24-cm, 24- to 30-cm, 30- to 36-cm, 36-
to 42-cm, and 42- to 48-cm depths.  Total [14C]residues in the leachate
solution were 31.6% of the applied radioactivity.  The parent was 1.1%
of the applied radioactivity.  The major degradate
dichloromethylhydroxylamine was 16.4% of the applied radioactivity.  The
major degradate dichloronitromethane was 10.9% of the applied
radioactivity.  The minor degradate nitromethane was 2.5% of the applied
radioactivity.  [14C]Organic volatiles (bottom of column) were 17.8% of
the applied radioactivity; the parent and dichloronitromethane accounted
for 13.8% and 3.3% of the applied, respectively.

In the Lowell silty clay loam soil, most of the [14C]residues retained
in the soil column following leaching were detected in the 12- to 18-cm
(24.3%) depth.  Characterization data were variable between the two soil
columns.  In Column 1, the parent was 0.1% of the applied radioactivity
in each of the 12- to 30-cm, 30- to 42-cm, and 42- to 48-cm depths.  In
Column 2, the parent was 49.3% of the applied radioactivity in the 12-
to 24-cm depth, was 1.3% in the 24- to 36-cm depth, and was not detected
in the 36- to 48-cm depth.  The minor degradates dichloronitromethane,
and dichloromethylhydroxylamine were ≤1.5% of the applied
radioactivity.  Nonextractable [14C]residues were ≤2.2% of the applied
radioactivity in each of the soil depth from 6- to 42-cm; [14C]residues
associated with the humic acid, fulvic acid, and humin fractions of
combined soil columns (12 to 48-cm depth) were 0.5%, 6.3%, and 6.0% of
the applied, respectively. Total [14C]residues in the leachate solution
were 20.5% of the applied radioactivity.  The parent compound was
present at 1.5% (one of two column leachates) of the applied
radioactivity.  The major degradate dichloronitromethane was 12.0% of
the applied radioactivity.  The minor degradates
dichloromethylhydroxylamine, and nitromethane were ≤5.5% of the
applied radioactivity.  [14C]Organic volatiles (bottom of column) were
19.4% of the applied radioactivity; the parent accounted for 14.5% (one
of two columns) of the applied.  The major degradate
dichloronitromethane was detected at 10.3% of the applied radioactivity.
 The minor degradate nitromethane was 1.5% of the applied radioactivity.
 The minor degradate dichloromethyl-hydroxylamine was 0.6% of the
applied radioactivity.

163-2 Laboratory Volatility (MRID# 43798601)

This study is acceptable as it meets Subdivision N Guidelines for the
fulfillment of EPA data requirements on laboratory volatility.  This
laboratory volatility study is scientifically valid. It provides useful
information on the volatility of chloropicrin in a sandy loam soil.
However, it appears that the flow exchange rate is high compared to
actual use conditions.

The registrant is required to address the following:

	Time zero analysis of treated soil was not conducted;

	Was the trapping efficiencies of charcoal, methanol, and KOH traps
determined? if so give the results.

	Need to relate the 100 mL/min flow rate or corresponding air changes/hr
to total exchanges during actual practice under greenhouse, and field
conditions (specified wind speeds).

	Limits of detection were reported but limits of quantitation were not;

	What is the vapor pressure at 25 oC? Other references give 23.8 mm Hg;
Is this accurate?

Although [14C]chloropicrin was applied through sub-surface injection, it
volatilized within few to nearly 30 hours from non-tarped and tarped
soil surfaces, respectively. By the end of the 8-day laboratory
experiment, 80-87% of the applied parent volatilized from the soil
surface as parent, 5-8% volatilized as CO2, 5-7% bound to the soil, and
<1% degraded into chloronitromethane. The results indicate that
volatilization as parent, is expected to be the most important route of
dissipation for chloropicrin in the soil environment. Data on non-tarped
and tarped covered soil surfaces indicate that covering the soil surface
with plastic tarp caused a change in the pattern and rates of
volatilization during the first 60 hours of the experiment.

[14C]chloropicrin, at a nominal application rate of 300 ppm, volatilized
from sandy loam soil (uncovered and tarp-covered) adjusted to 60% of
0.33 bar soil moisture content and incubated in darkness at 25.0 ± 1̊C
for up to 8 days with an air flow (>90% relative humidity) rate of
approximately 100 mL/min.

In the uncovered (no tarp) soil, the maximum volatility of the parent
was 342 µg/cm2/hr and the maximum air concentration of the parent was
1.0 × 104 µg × 103/m3 (2-6 hour interval).  Total [14C]volatiles
accounted for 92.6% of the applied radioactivity at 8 days
posttreatment.  Organic [14C]volatiles detected in the methanol, water
vapor, and charcoal traps were 86.0%, 1.5%, and 0.08% of the applied
radioactivity, respectively, at 8 days posttreatment; evolved 14CO2 was
5.1% of the applied.  The parent was initially (2 hours) present in the
methanol trap at 0.8% of the applied radioactivity, increased to 16.3%
by 6 hours and 65.4% by 24 hours, and was 81.5-85.5% at 46-116 hours
posttreatment.  The degradate dichloronitromethane was detected in the
methanol trap at 0.4% of the applied radioactivity.  In the soil,
extractable and nonextractable [14C]residues were 0.4% and 4.3% of the
applied radioactivity, respectively, at 8 days posttreatment.

In tarp covered soil, the pesticide stayed within the soil system for
relatively longer period of time than in non-tarped soil. This resulted
in a slightly higher pesticide bio-degradation and binding to the tarped
compared to non-tarped soil as inferred from the observed higher
concentrations of  CO2 and soil bound residue.  In the tarp-covered
soil, the maximum volatility of the parent was 205 µg/cm2/hr and the
maximum air concentration of the parent was 5918 µg × 103/m3 (23-25
hour interval; interval in which the tarp was punctured).  Total
[14C]volatiles accounted for 89.3% of the applied radioactivity at 8
days posttreatment.  Organic [14C]volatiles detected in the methanol,
water vapor, and charcoal traps were 79.9%, 1.2%, and 0.09% of the
applied radioactivity, respectively, at 8 days posttreatment; evolved
14CO2 was 8.2% of the applied.  The parent was initially (4 hours)
present in the methanol trap at 1.9% of the applied radioactivity,
increased to 38.7% by 23 hours and 67.2% by 47 hours, and was 79.1% at
144 hours posttreatment.  The degradate dichloronitromethane was
detected in the methanol trap at 0.7% of the applied radioactivity.  In
the soil, extractable and nonextractable [14C]residues were 1.1% and
6.1% of the applied radioactivity, respectively, at 8 days
posttreatment.

164-1 Terrestrial Field Dissipation (MRID# 43085101, supplemental)

This study provides limited supplemental information about the
terrestrial field dissipation of chloropicrin.  Several problems were
found in the study:

	samples were taken only of the soil air and analyzed only for
chloropicrin (and methyl bromide), no soil samples were taken;

	the test soils were not completely characterized;

	the site description was incomplete and not adequately characterized;

	the field maintenance practices used before and after application were
not provided.

Chloropicrin dissipated with half-lives of 11.6, 16.4, and 33.4 hours
from the soil air at the 3-, 6-, and 12-inch depths, respectively,
following treatment with 665 lb a.i./A chloropicrin (TRI-CLOR: 99%
purity) of a tarped clay loam soil in California in July, 1987.  The
chloropicrin was applied by chisel injection at a depth of 6-8 inches,
the soil surface was covered with a polyethylene tarp for 48 hours, and
sampling was initiated after removal of the tarp.  Chloropicrin was
found at maximum concentration of 755-781 ppm in the soil air from the
upper 12 inches at 51 hours posttreatment (3 hours after removal of the
tarp). Concentrations at the 24-, 36-, and 48-inch depths were never
exceeded 30, 8.6, and 5.8 ppm, respectively, and declined to below
background levels by the termination of the study (291 hours
posttreatment).  Background levels of chloropicrin (as determined by
analysis of soil air from the untreated check plot located 15 feet away
from the treated plot) ranged from 0.2 to 8.5 ppm (average 2.9 ppm).

Chloropicrin dissipated with half-lives of 18.0, 20.3, and 28.7 hours
from the soil air at the 3-, 6-, and 12-inch depths, respectively,
following treatment with 792 lb a.i./A chloropicrin (TRI-CLOR: 99%
purity) of a tarped sand soil in California in August, 1987.  The
chloropicrin was applied by chisel injection at a depth of 6-8 inches,
the soil surface was covered with a polyethylene tarp for 48 hours, and
sampling was initiated after removal of the tarp.  Chloropicrin was
found at maximum concentrations of 554.0, 930.0, and 1185.0 ppm in the
3-, 6-, and 12-inch soil depths, respectively, at 51 hours posttreatment
(3 hours after removal of the tarp). Concentrations at the 24-, 36-, and
48-inch depths increased to a maxima of 593.0, 230.5, and 75.2 ppm,
respectively; times of maximum concentration were 12, 12, and 48 hours,
respectively, after removal of the tarp.  By the termination of the
study (240 hours posttreatment), concentrations at 24-, 36-, and 48-inch
depths had decreased to 31.8, 37.1, and 16.8 ppm, respectively.
Background levels of chloropicrin (as determined by analysis of soil air
from the untreated check plot located 15 feet away from the treated
plot) ranged from 0.3 to 8.5 ppm (average 1.9 ppm).

	Appendix B. Aquatic Exposure PRZM/EXAMS Modeling  TC \l2 "Appendix B.
Aquatic Exposure PRZM/EXAMS Modeling

	This appendix documents the output from PRZM / EXAMS simulations for
each of six  location/crop scenarios: California / Onion and Tomato,
Florida / Strawberry and Tomato, and North Carolina / Tobacco and sweet
potato.  The settings for each model run are presented first, followed
by the raw data sorted by year and sorted in descending order by EEC.
Values represent the estimated environmental concentrations (EECs) in
units of micrograms per liter (μg/L) or parts per billion (ppb).  The
1-in-10 year summary statistics for each run are presented at the very
end of the sorted results in the row assigned a probability level of
0.10.  This summary statistic was generated from a linear interpretation
of the raw data plotted using Weibull plotting positions.  This approach
is further described at the end of the appendix B-6.

B.1.1 Florida Strawberry

stored as FLStrawb.out

Chemical: Chloropicrin

PRZM environment: FlstrawberryC.txt, Modified Monday, 30 June 2003 at
08:19:10

EXAMS environment: pond298.exv, Modified Thuday, 29 August 2002 at
16:33:30

Metfile: w12842.dvf, Modified Wedday, 3 July 2002 at 09:04:28

Water segment concentrations (ppb)

Year	Peak	96 hr	21 Day	60 Day	90 Day	Yearly

1961	4.62	3.11	1.38	0.57	0.39	0.10

1962	84.41	57.97	21.99	8.16	5.45	1.34

1963	33.19	22.05	8.17	3.42	2.30	0.57

1964	3.16	2.18	1.15	0.53	0.36	0.09

1965	104.00	69.55	26.30	9.81	6.55	1.62

1966	5.05	3.58	2.12	0.91	0.61	0.15

1967	6.91	4.70	2.87	1.18	0.79	0.20

1968	8.70	5.98	2.72	1.19	0.81	0.20

1969	12.37	8.54	3.85	1.59	1.09	0.27

1970	9.06	6.21	2.81	1.18	0.80	0.20

1971	6.26	4.40	2.64	1.05	0.71	0.17

1972	8.03	6.09	2.53	1.24	0.83	0.20

1973	12.09	8.28	4.75	2.08	1.40	0.35

1974	6.28	4.33	2.06	0.84	0.56	0.14

1975	14.37	9.83	4.59	1.98	1.33	0.33

1976	9.72	6.82	3.89	1.91	1.29	0.32

1977	60.94	44.11	17.73	6.73	4.49	1.11

1978	9.81	6.99	4.60	1.86	1.24	0.31

1979	16.43	13.15	6.33	2.49	1.67	0.41

1980	8.42	6.11	2.81	1.14	0.77	0.19

1981	24.23	18.26	8.82	3.67	2.46	0.61

1982	49.07	36.61	16.95	6.34	4.23	1.04

1983	8.85	6.38	3.01	1.46	0.98	0.24

1984	3.25	2.25	1.53	0.67	0.45	0.11

1985	5.84	4.05	2.61	1.41	0.95	0.23

1986	12.51	9.87	4.56	1.74	1.17	0.29

1987	5.41	3.94	1.83	0.75	0.50	0.12

1988	9.87	6.79	3.38	1.69	1.14	0.28

1989	10.91	7.70	3.38	1.55	1.05	0.26

1990	3.08	2.24	1.32	0.50	0.33	0.08

Sorted results

	Prob.	Peak	96 hr	21 Day	60 Day	90 Day	Yearly

0.03	104.00	69.55	26.30	9.81	6.55	1.62

0.06	84.41	57.97	21.99	8.16	5.45	1.34

0.10	60.94	44.11	17.73	6.73	4.49	1.11

0.13	49.07	36.61	16.95	6.34	4.23	1.04

0.16	33.19	22.05	8.82	3.67	2.46	0.61

0.19	24.23	18.26	8.17	3.42	2.30	0.57

0.23	16.43	13.15	6.33	2.49	1.67	0.41

0.26	14.37	9.87	4.75	2.08	1.40	0.35

0.29	12.51	9.83	4.60	1.98	1.33	0.33

0.32	12.37	8.54	4.59	1.91	1.29	0.32

0.35	12.09	8.28	4.56	1.86	1.24	0.31

0.39	10.91	7.70	3.89	1.74	1.17	0.29

0.42	9.87	6.99	3.85	1.69	1.14	0.28

0.45	9.81	6.82	3.38	1.59	1.09	0.27

0.48	9.72	6.79	3.38	1.55	1.05	0.26

0.52	9.06	6.38	3.01	1.46	0.98	0.24

0.55	8.85	6.21	2.87	1.41	0.95	0.23

0.58	8.70	6.11	2.81	1.24	0.83	0.20

0.61	8.42	6.09	2.81	1.19	0.81	0.20

0.65	8.03	5.98	2.72	1.18	0.80	0.20

0.68	6.91	4.70	2.64	1.18	0.79	0.20

0.71	6.28	4.40	2.61	1.14	0.77	0.19

0.74	6.26	4.33	2.53	1.05	0.71	0.17

0.77	5.84	4.05	2.12	0.91	0.61	0.15

0.81	5.41	3.94	2.06	0.84	0.56	0.14

0.84	5.05	3.58	1.83	0.75	0.50	0.12

0.87	4.62	3.11	1.53	0.67	0.45	0.11

0.90	3.25	2.25	1.38	0.57	0.39	0.10

0.94	3.16	2.24	1.32	0.53	0.36	0.09

0.97	3.08	2.18	1.15	0.50	0.33	0.08

0.10	59.75	43.36	17.65	6.69	4.47	1.10

Average of yearly averages:	0.38

Inputs generated by pe4.pl - 8-August-2003

Data used for this run:

Output File: FLStrawb

Metfile:	w12842.dvf

PRZM scenario:	FLstrawberryC.txt

EXAMS environment file: pond298.exv

Chemical Name:	Chloropicrin

Description	Variable Name	Value	Units	Comments

Molecular weight	mwt	164.4	g/mol

	Henry's Law Const.	henry	0.00205	atm-m^3/mol

Vapor Pressure	vapr	23.8	torr

	Solubility	sol	1621	mg/L

	Kd	Kd

mg/L

	Koc	Koc	36.05	mg/L

	Photolysis half-life	kdp	1.3	days	Half-life

Aerobic Aquatic Metabolism	kbacw	31.42	days	Halfife

Anaerobic Aquatic Metabolism	kbacs	0.05	days	Halfife

Aerobic Soil Metabolism	asm	15.71	days	Halfife

Hydrolysis:	pH 7	0	days	Half-life

Method:	CAM	8	integer	See PRZM manual

	Incorporation Depth:	DEPI	25	cm

	Application Rate:	TAPP	392	kg/ha

	Application Efficiency:	APPEFF	1	fraction

	Spray Drift	DRFT	0	fraction of application rate applied to pond

Application Date	Date	15-9	dd/mm or dd/mmm or dd-mm or dd-mmm

Record 17:	FILTRA

IPSCND	1

	UPTKF

	Record 18:	PLVKRT

PLDKRT

FEXTRC	0

Flag for Index Res. Run	IR	Pond

Flag for runoff calc.	RUNOFF	none	none, monthly or total(average of
entire run)

B.1.2 Florida Tomato

stored as FLTomato.out

Chemical: Chloropicrin

PRZM environment: FltomatoC.txt, Mmodified Satday, 12 October 2002 at
16:44:04

EXAMS environment: pond298.exv, Mmodified Thuday, 29 August 2002 at
16:33:30

Metfile: w12844.dvf, Modified Wedday, 3 July 2002 at 09:04:30

	Water segment concentrations (ppb)

Year	Peak	96 hr	21 Day	60 Day	90 Day	Yearly

1961	1.97	1.31	0.69	0.45	0.30	0.07

1962	106.00	79.75	29.59	10.54	7.03	1.73

1963	77.19	53.35	30.82	12.70	8.47	2.09

1964	56.35	38.79	19.41	7.97	5.33	1.31

1965	20.89	15.09	6.21	3.20	2.15	0.53

1966	24.46	17.68	7.92	3.41	2.27	0.56

1967	69.80	48.03	20.98	8.44	5.63	1.39

1968	55.26	44.23	24.24	9.56	6.37	1.57

1969	55.05	37.46	18.79	7.41	4.95	1.22

1970	31.83	21.15	9.60	3.46	2.31	0.57

1971	4.84	3.30	1.22	0.73	0.49	0.12

1972	1.49	1.03	0.36	0.13	0.09	0.02

1973	10.10	6.95	3.58	1.92	1.28	0.32

1974	21.65	12.56	6.02	2.28	1.53	0.38

1975	134.00	91.32	35.73	12.86	8.58	2.11

1976	4.26	2.83	1.16	0.69	0.47	0.11

1977	29.54	20.72	7.30	2.61	1.76	0.43

1978	12.72	8.86	3.67	1.58	1.06	0.26

1979	30.37	22.90	10.76	4.22	2.82	0.69

1980	13.06	8.86	2.94	1.29	0.87	0.21

1981	57.10	43.42	14.60	5.39	3.61	0.89

1982	20.74	14.47	6.84	2.64	1.76	0.43

1983	108.00	72.53	27.05	10.10	6.75	1.66

1984	64.45	46.78	21.74	7.87	5.29	1.30

1985	78.82	55.70	24.52	8.96	5.98	1.47

1986	4.07	2.68	0.84	0.55	0.38	0.10

1987	71.64	48.12	20.39	7.73	5.16	1.27

1988	4.06	2.68	0.85	0.32	0.21	0.05

1989	42.45	27.53	9.17	3.63	2.42	0.60

1990	198.00	132.00	46.46	16.59	11.06	2.73

Sorted results

	Prob.	Peak	96 hr	21 Day	60 Day	90 Day	Yearly

0.03	198.00	132.00	46.46	16.59	11.06	2.73

0.06	134.00	91.32	35.73	12.86	8.58	2.11

0.10	108.00	79.75	30.82	12.70	8.47	2.09

0.13	106.00	72.53	29.59	10.54	7.03	1.73

0.16	78.82	55.70	27.05	10.10	6.75	1.66

0.19	77.19	53.35	24.52	9.56	6.37	1.57

0.23	71.64	48.12	24.24	8.96	5.98	1.47

0.26	69.80	48.03	21.74	8.44	5.63	1.39

0.29	64.45	46.78	20.98	7.97	5.33	1.31

0.32	57.10	44.23	20.39	7.87	5.29	1.30

0.35	56.35	43.42	19.41	7.73	5.16	1.27

0.39	55.26	38.79	18.79	7.41	4.95	1.22

0.42	55.05	37.46	14.60	5.39	3.61	0.89

0.45	42.45	27.53	10.76	4.22	2.82	0.69

0.48	31.83	22.90	9.60	3.63	2.42	0.60

0.52	30.37	21.15	9.17	3.46	2.31	0.57

0.55	29.54	20.72	7.92	3.41	2.27	0.56

0.58	24.46	17.68	7.30	3.20	2.15	0.53

0.61	21.65	15.09	6.84	2.64	1.76	0.43

0.65	20.89	14.47	6.21	2.61	1.76	0.43

0.68	20.74	12.56	6.02	2.28	1.53	0.38

0.71	13.06	8.86	3.67	1.92	1.28	0.32

0.74	12.72	8.86	3.58	1.58	1.06	0.26

0.77	10.10	6.95	2.94	1.29	0.87	0.21

0.81	4.84	3.30	1.22	0.73	0.49	0.12

0.84	4.26	2.83	1.16	0.69	0.47	0.11

0.87	4.07	2.68	0.85	0.55	0.38	0.10

0.90	4.06	2.68	0.84	0.45	0.30	0.07

0.94	1.97	1.31	0.69	0.32	0.21	0.05

0.97	1.49	1.03	0.36	0.13	0.09	0.02

0.10	107.80	79.03	30.70	12.48	8.33	2.05

	Average of yearly averages:	0.87

Inputs generated by pe4.pl - 8-August-2003

	Data used for this run:

	Output File: FLTomato

	Metfile:	w12844.dvf

PRZM scenario:	FLtomatoC.txt

EXAMS environment file:	pond298.exv

Chemical Name:	Chloropicrin

Description	Variable Name	Value	Units	Comments

Molecular weight	mwt	164.4	g/mol

	Henry's Law Const.	henry	0.00205	atm-m^3/mol

Vapor Pressure	vapr	23.8	torr

	Solubility	sol	1621	mg/L

	Kd	Kd

mg/L

	Koc	Koc	36.05	mg/L

	Photolysis half-life	kdp	1.3	days	Half-life

Aerobic Aquatic Metabolism	kbacw

	31.42

	days

	Halfife

Anaerobic Aquatic Metabolism	kbacs	0.05	days	Halfife

Aerobic Soil Metabolism	asm	15.71	days	Halfife

Hydrolysis:	pH 7	0	days	Half-life

Method:	CAM	8	integer	See PRZM manual

	Incorporation Depth:	DEPI	25	cm

	Application Rate:	TAPP	392	kg/ha

	Application Efficiency:	APPEFF	1	fraction

	Spray Drift	DRFT	0	fraction of application rate applied to pond

Application Date	Date	15-9	dd/mm or dd/mmm or dd-mm or dd-mmm

Record 17:	FILTRA

IPSCND	1

	UPTKF

	Record 18:	PLVKRT

PLDKRT

FEXTRC	0

Flag for Index Res. Run	IR	Pond

Flag for runoff calc.	RUNOFF	none	none, monthly or total(average of
entire run)

B.2.1 California Tomato

stored as CATomato.out

Chemical: Chloropicrin

PRZM environment: CAtomatoC.txt	Modified Wedday, 2 February 2005 at
12:45:10

EXAMS environment: pond298.exv, Modified Thuday, 29 August 2002 at
16:33:30

Metfile: w93193.dvf, Modified Wedday, 3 July 2002 at 09:04:24

	Water segment concentrations (ppb)

Year	Peak	96 hr	21 Day	60 Day	90 Day	Yearly

1961	0.28	0.23	0.15	0.06	0.04	0.01

1962	0.44	0.34	0.15	0.05	0.04	0.01

1963	1.77	1.43	0.77	0.40	0.28	0.07

1964	2.50	1.90	0.91	0.36	0.24	0.06

1965	0.11	0.09	0.05	0.02	0.02	0.01

1966	0.52	0.46	0.27	0.13	0.09	0.02

1967	0.24	0.19	0.10	0.04	0.03	0.01

1968	2.23	1.75	0.85	0.49	0.34	0.09

1969	0.17	0.15	0.08	0.03	0.02	0.01

1970	0.28	0.22	0.13	0.06	0.04	0.01

1971	0.12	0.10	0.04	0.02	0.01	0.00

1972	0.50	0.42	0.26	0.11	0.07	0.02

1973	1.73	1.35	0.60	0.25	0.18	0.04

1974	6.62	5.11	2.42	1.00	0.67	0.17

1975	1.31	1.03	0.52	0.21	0.14	0.04

1976	4.19	3.30	1.48	0.63	0.43	0.11

1977	0.72	0.58	0.25	0.09	0.06	0.02

1978	0.25	0.21	0.10	0.05	0.03	0.01

1979	0.35	0.29	0.14	0.06	0.04	0.01

1980	0.02	0.02	0.01	0.00	0.00	0.00

1981	0.20	0.15	0.08	0.04	0.02	0.01

1982	3.79	2.93	1.87	0.84	0.61	0.16

1983	0.80	0.58	0.25	0.17	0.13	0.03

1984	0.68	0.54	0.27	0.16	0.13	0.03

1985	0.66	0.52	0.26	0.18	0.12	0.03

1986	0.14	0.12	0.05	0.02	0.01	0.01

1987	0.21	0.16	0.08	0.05	0.03	0.01

1988	0.13	0.11	0.06	0.03	0.02	0.01

1989	0.14	0.10	0.04	0.01	0.01	0.00

1990	0.07	0.05	0.03	0.02	0.01	0.00

Sorted results

	Prob.	Peak	96 hr	21 Day	60 Day	90 Day	Yearly

0.03	6.62	5.11	2.42	1.00	0.67	0.17

0.06	4.19	3.30	1.87	0.84	0.61	0.16

0.10	3.79	2.93	1.48	0.63	0.43	0.11

0.13	2.50	1.90	0.91	0.49	0.34	0.09

0.16	2.23	1.75	0.85	0.40	0.28	0.07

0.19	1.77	1.43	0.77	0.36	0.24	0.06

0.23	1.73	1.35	0.60	0.25	0.18	0.04

0.26	1.31	1.03	0.52	0.21	0.14	0.04

0.29	0.80	0.58	0.27	0.18	0.13	0.03

0.32	0.72	0.58	0.27	0.17	0.13	0.03

0.35	0.68	0.54	0.26	0.16	0.12	0.03

0.39	0.66	0.52	0.26	0.13	0.09	0.02

0.42	0.52	0.46	0.25	0.11	0.07	0.02

0.45	0.50	0.42	0.25	0.09	0.06	0.02

0.48	0.44	0.34	0.15	0.06	0.04	0.01

0.52	0.35	0.29	0.15	0.06	0.04	0.01

0.55	0.28	0.23	0.14	0.06	0.04	0.01

0.58	0.28	0.22	0.13	0.05	0.04	0.01

0.61	0.25	0.21	0.10	0.05	0.03	0.01

0.65	0.24	0.19	0.10	0.05	0.03	0.01

0.68	0.21	0.16	0.08	0.04	0.03	0.01

0.71	0.20	0.15	0.08	0.04	0.02	0.01

0.74	0.17	0.15	0.08	0.03	0.02	0.01

0.77	0.14	0.12	0.06	0.03	0.02	0.01

0.81	0.14	0.11	0.05	0.02	0.02	0.01

0.84	0.13	0.10	0.05	0.02	0.01	0.01

0.87	0.12	0.10	0.04	0.02	0.01	0.00

0.90	0.11	0.09	0.04	0.02	0.01	0.00

0.94	0.07	0.05	0.03	0.01	0.01	0.00

0.97	0.02	0.02	0.01	0.00	0.00	0.00

0.10	3.66	2.83	1.42	0.61	0.42	0.10

	Average of yearly averages:	0.03

Inputs generated by pe4.pl - 8-August-2003

	Data used for this run:

	Output File: CATomato

	Metfile:	w93193.dvf

PRZM scenario:	CAtomatoC.txt

EXAMS environment file:	pond298.exv

Chemical Name:	Chloropicrin

Description	Variable Name	Value	Units	Comments

Molecular weight	mwt	164.4	g/mol

	Henry's Law Const.	henry	0.00205	atm-m^3/mol

Vapor Pressure	vapr	23.8	torr

	Solubility	sol	1621	mg/L

	Kd	Kd

mg/L

	Koc	Koc	36.05	mg/L

	Photolysis half-life	kdp	1.3	days	Half-life

Aerobic Aquatic Metabolism	kbacw

	31.42

	days

	Halfife

Anaerobic Aquatic Metabolism	kbacs	0.05	days	Halfife

Aerobic Soil Metabolism	asm	15.71	days	Halfife

Hydrolysis:	pH 7	0	days	Half-life

Method:	CAM	8	integer	See PRZM manual

	Incorporation Depth:	DEPI	25	cm

	Application Rate:	TAPP	392	kg/ha

	Application Efficiency:	APPEFF	1	fraction

	Spray Drift	DRFT	0	fraction of application rate applied to pond

Application Date	Date	15-9	dd/mm or dd/mmm or dd-mm or dd-mmm

Record 17:	FILTRA

IPSCND	1

	UPTKF

	Record 18:	PLVKRT

PLDKRT

FEXTRC	0

Flag for Index Res. Run	IR	Pond

Flag for runoff calc.	RUNOFF	none	none, monthly or total(average of
entire run)

B.2.2 California Onion

stored as CAOnion.out

	Chemical: Chloropicrin

PRZM environment: CAonionC.txt	Modified Monday, 23 December 2002 at
06:48:48

EXAMS environment: pond298.exv, Modified Thuday, 29 August 2002 at
16:33:30

Metfile: w23155.dvf, Modified Wedday, 3 July 2002 at 09:04:20

	Water segment concentrations (ppb)

Year	Peak	96 hr	21 Day	60 Day	90 Day	Yearly

1961	0.02	0.02	0.01	0.00	0.00	0.00

1962	0.00	0.00	0.00	0.00	0.00	0.00

1963	15.87	11.74	4.63	1.73	1.15	0.28

1964	0.19	0.14	0.06	0.02	0.02	0.00

1965	0.06	0.05	0.02	0.01	0.01	0.00

1966	0.06	0.05	0.03	0.02	0.01	0.00

1967	0.10	0.09	0.05	0.02	0.02	0.00

1968	0.49	0.39	0.19	0.08	0.06	0.01

1969	0.04	0.03	0.01	0.00	0.00	0.00

1970	0.06	0.04	0.02	0.01	0.01	0.00

1971	0.01	0.00	0.00	0.00	0.00	0.00

1972	0.29	0.23	0.10	0.06	0.04	0.01

1973	0.01	0.01	0.01	0.00	0.00	0.00

1974	5.68	4.26	1.70	0.65	0.44	0.11

1975	0.01	0.00	0.00	0.00	0.00	0.00

1976	0.50	0.35	0.13	0.05	0.03	0.01

1977	0.03	0.02	0.00	0.00	0.00	0.00

1978	0.02	0.01	0.01	0.00	0.00	0.00

1979	0.00	0.00	0.00	0.00	0.00	0.00

1980	0.00	0.00	0.00	0.00	0.00	0.00

1981	1.94	1.48	0.61	0.23	0.15	0.04

1982	2.16	1.56	0.60	0.24	0.17	0.04

1983	0.09	0.07	0.03	0.02	0.01	0.00

1984	0.06	0.04	0.02	0.01	0.01	0.00

1985	0.35	0.28	0.13	0.06	0.04	0.01

1986	0.03	0.02	0.01	0.01	0.00	0.00

1987	1.44	1.15	0.53	0.20	0.14	0.03

1988	0.00	0.00	0.00	0.00	0.00	0.00

1989	1.09	0.68	0.20	0.07	0.05	0.01

1990	0.00	0.00	0.00	0.00	0.00	0.00

Sorted results

	Prob.	Peak	96 hr	21 Day	60 Day	90 Day	Yearly

0.03	15.87	11.74	4.63	1.73	1.15	0.28

0.06	5.68	4.26	1.70	0.65	0.44	0.11

0.10	2.16	1.56	0.61	0.24	0.17	0.04

0.13	1.94	1.48	0.60	0.23	0.15	0.04

0.16	1.44	1.15	0.53	0.20	0.14	0.03

0.19	1.09	0.68	0.20	0.08	0.06	0.01

0.23	0.50	0.39	0.19	0.07	0.05	0.01

0.26	0.49	0.35	0.13	0.06	0.04	0.01

0.29	0.35	0.28	0.13	0.06	0.04	0.01

0.32	0.29	0.23	0.10	0.05	0.03	0.01

0.35	0.19	0.14	0.06	0.02	0.02	0.00

0.39	0.10	0.09	0.05	0.02	0.02	0.00

0.42	0.09	0.07	0.03	0.02	0.01	0.00

0.45	0.06	0.05	0.03	0.02	0.01	0.00

0.48	0.06	0.05	0.02	0.01	0.01	0.00

0.52	0.06	0.04	0.02	0.01	0.01	0.00

0.55	0.06	0.04	0.02	0.01	0.01	0.00

0.58	0.04	0.03	0.01	0.01	0.00	0.00

0.61	0.03	0.02	0.01	0.00	0.00	0.00

0.65	0.03	0.02	0.01	0.00	0.00	0.00

0.68	0.02	0.02	0.01	0.00	0.00	0.00

0.71	0.02	0.01	0.01	0.00	0.00	0.00

0.74	0.01	0.01	0.00	0.00	0.00	0.00

0.77	0.01	0.00	0.00	0.00	0.00	0.00

0.81	0.01	0.00	0.00	0.00	0.00	0.00

0.84	0.00	0.00	0.00	0.00	0.00	0.00

0.87	0.00	0.00	0.00	0.00	0.00	0.00

0.90	0.00	0.00	0.00	0.00	0.00	0.00

0.94	0.00	0.00	0.00	0.00	0.00	0.00

0.97	0.00	0.00	0.00	0.00	0.00	0.00

0.10	2.14	1.55	0.61	0.24	0.17	0.04

Average of yearly averages:	0.02

Inputs generated by pe4.pl - 8-August-2003

	Data used for this run:

	Output File: CAOnion

	Metfile:	w23155.dvf

PRZM scenario:	CAonionC.txt

EXAMS environment file: pond298.exv

Chemical Name:	Chloropicrin

Description	Variable Name	Value	Units	Comments

Molecular weight	mwt	164.4	g/mol

	Henry's Law Const.	henry	0.00205	atm-m^3/mol

Vapor Pressure	vapr	23.8	torr

	Solubility	sol	1621	mg/L

	Kd	Kd

mg/L

	Koc	Koc	36.05	mg/L

	Photolysis half-life	kdp	1.3	days	Half-life

Aerobic Aquatic Metabolism	kbacw	31.42	days	Halfife

Anaerobic Aquatic Metabolism	kbacs	0.05	days	Halfife

Aerobic Soil Metabolism	asm	15.71	days	Halfife

Hydrolysis:	pH 7	0	days	Half-life

Method:	CAM	8	integer	See PRZM manual

	Incorporation Depth:	DEPI	25	cm

	Application Rate:	TAPP	392	kg/ha

	Application Efficiency:	APPEFF	1	fraction

	Spray Drift	DRFT	0	fraction of application rate applied to pond

Application Date	Date	15-9	dd/mm or dd/mmm or dd-mm or dd-mmm

Record 17:	FILTRA

IPSCND	1

	UPTKF

	Record 18:	PLVKRT

PLDKRT

FEXTRC	0

Flag for Index Res. Run	IR	Pond

Flag for runoff calc.	RUNOFF	none	none, monthly or total(average of
entire run)

B.3.1 North Carolina Tobacco

stored as NCTobac.out

Chemical: Chloropicrin

PRZM environment: NctobaccoC.txt, modified Satday, 12 October 2002 at
17:13:36

EXAMS environment: pond298.exv, modified Thuday, 29 August 2002 at
16:33:30

Metfile: w13722.dvf,modified Wedday, 3 July 2002 at 09:05:50

	Water segment concentrations (ppb)

Year	Peak	96 hr	21 Day	60 Day	90 Day	Yearly

1961	0.67	0.49	0.18	0.07	0.04	0.01

1962	0.03	0.02	0.01	0.01	0.00	0.00

1963	0.61	0.46	0.21	0.08	0.05	0.01

1964	0.02	0.01	0.00	0.00	0.00	0.00

1965	0.14	0.11	0.04	0.02	0.01	0.00

1966	0.91	0.67	0.26	0.11	0.07	0.02

1967	0.97	0.70	0.41	0.17	0.12	0.03

1968	0.08	0.06	0.02	0.01	0.01	0.00

1969	0.07	0.05	0.03	0.01	0.01	0.00

1970	0.29	0.21	0.08	0.03	0.02	0.00

1971	0.25	0.18	0.08	0.04	0.02	0.01

1972	0.55	0.40	0.22	0.08	0.06	0.01

1973	1.68	1.26	0.48	0.18	0.12	0.03

1974	0.29	0.22	0.12	0.05	0.04	0.01

1975	0.07	0.06	0.02	0.01	0.01	0.00

1976	0.19	0.14	0.06	0.02	0.02	0.00

1977	0.07	0.05	0.02	0.01	0.01	0.00

1978	2.70	2.01	0.85	0.31	0.21	0.05

1979	0.08	0.06	0.04	0.03	0.02	0.00

1980	0.44	0.33	0.13	0.05	0.03	0.01

1981	0.19	0.14	0.06	0.02	0.01	0.00

1982	0.80	0.60	0.24	0.10	0.07	0.02

1983	0.05	0.04	0.02	0.01	0.01	0.00

1984	0.77	0.64	0.27	0.11	0.08	0.02

1985	1.26	0.93	0.36	0.14	0.09	0.02

1986	0.09	0.07	0.03	0.01	0.01	0.00

1987	0.01	0.01	0.00	0.00	0.00	0.00

1988	1.69	1.27	0.50	0.20	0.13	0.03

1989	1.67	1.22	0.47	0.17	0.12	0.03

1990	0.60	0.43	0.18	0.07	0.05	0.01

Sorted results

	Prob.	Peak	96 hr	21 Day	60 Day	90 Day	Yearly

0.03	2.70	2.01	0.85	0.31	0.21	0.05

0.06	1.69	1.27	0.50	0.20	0.13	0.03

0.10	1.68	1.26	0.48	0.18	0.12	0.03

0.13	1.67	1.22	0.47	0.17	0.12	0.03

0.16	1.26	0.93	0.41	0.17	0.12	0.03

0.19	0.97	0.70	0.36	0.14	0.09	0.02

0.23	0.91	0.67	0.27	0.11	0.08	0.02

0.26	0.80	0.64	0.26	0.11	0.07	0.02

0.29	0.77	0.60	0.24	0.10	0.07	0.02

0.32	0.67	0.49	0.22	0.08	0.06	0.01

0.35	0.61	0.46	0.21	0.08	0.05	0.01

0.39	0.60	0.43	0.18	0.07	0.05	0.01

0.42	0.55	0.40	0.18	0.07	0.04	0.01

0.45	0.44	0.33	0.13	0.05	0.04	0.01

0.48	0.29	0.22	0.12	0.05	0.03	0.01

0.52	0.29	0.21	0.08	0.04	0.02	0.01

0.55	0.25	0.18	0.08	0.03	0.02	0.00

0.58	0.19	0.14	0.06	0.03	0.02	0.00

0.61	0.19	0.14	0.06	0.02	0.02	0.00

0.65	0.14	0.11	0.04	0.02	0.01	0.00

0.68	0.09	0.07	0.04	0.02	0.01	0.00

0.71	0.08	0.06	0.03	0.01	0.01	0.00

0.74	0.08	0.06	0.03	0.01	0.01	0.00

0.77	0.07	0.06	0.02	0.01	0.01	0.00

0.81	0.07	0.05	0.02	0.01	0.01	0.00

0.84	0.07	0.05	0.02	0.01	0.01	0.00

0.87	0.05	0.04	0.02	0.01	0.01	0.00

0.90	0.03	0.02	0.01	0.01	0.00	0.00

0.94	0.02	0.01	0.00	0.00	0.00	0.00

0.97	0.01	0.01	0.00	0.00	0.00	0.00

0.10	1.67	1.26	0.48	0.18	0.12	0.03

Average of yearly averages:	0.01

Inputs generated by pe4.pl - 8-August-2003

	Data used for this run:

	Output File: NCTobac

	Metfile:	w13722.dvf

PRZM scenario:	NCtobaccoC.txt

EXAMS environment file:	pond298.exv

Chemical Name:	Chloropicrin

Description	Variable Name	Value	Units	Comments

Molecular weight	mwt	164.4	g/mol

	Henry's Law Const.	henry	0.00205	atm-m^3/mol

Vapor Pressure	vapr	23.8	torr

	Solubility	sol	1621	mg/L

	Kd	Kd

mg/L

	Koc	Koc	36.05	mg/L

	Photolysis half-life	kdp	1.3	days	Half-life

Aerobic Aquatic Metabolism	kbacw

	31.42

	days

	Halfife

Anaerobic Aquatic Metabolism	kbacs	0.05	days	Halfife

Aerobic Soil Metabolism	asm	15.71	days	Halfife

Hydrolysis:	pH 7	0	days	Half-life

Method:	CAM	8	integer	See PRZM manual

	Incorporation Depth:	DEPI	25	cm

	Application Rate:	TAPP	392	kg/ha

	Application Efficiency:	APPEFF	1	fraction

	Spray Drift	DRFT	0	fraction of application rate applied to pond

Application Date	Date	15-4	dd/mm or dd/mmm or dd-mm or dd-mmm

Record 17:	FILTRA

IPSCND	1

	UPTKF

	Record 18:	PLVKRT

PLDKRT

FEXTRC	0

Flag for Index Res. Run	IR	Pond

Flag for runoff calc.	RUNOFF	none	none, monthly or total(average of
entire run)

B.3.2 North Carolina Sweet Potato

stored as NCsweet.out

	Chemical: Chloropicrin

	PRZM environment: NCSweetPotatoC.txt,modified Friday, 8 August 2003 at
09:25:48

EXAMS environment: pond298.exv, modified Thuday, 29 August 2002 at
16:33:30

Metfile: w13722.dvf, modified Wedday, 3 July 2002 at 09:05:50

Water segment concentrations (ppb)

	Year	Peak	96 hr	21 Day	60 Day	90 Day	Yearly

1961	1.21	0.96	0.37	0.14	0.09	0.02

1962	0.13	0.10	0.06	0.05	0.03	0.01

1963	0.97	0.73	0.36	0.14	0.10	0.02

1964	0.12	0.09	0.03	0.02	0.02	0.00

1965	0.32	0.23	0.12	0.06	0.05	0.01

1966	0.99	0.76	0.36	0.17	0.12	0.03

1967	0.51	0.36	0.15	0.11	0.09	0.02

1968	0.29	0.21	0.08	0.04	0.03	0.01

1969	0.21	0.16	0.09	0.04	0.04	0.01

1970	0.53	0.37	0.15	0.05	0.05	0.01

1971	0.33	0.26	0.13	0.06	0.05	0.01

1972	0.84	0.61	0.30	0.13	0.10	0.03

1973	1.77	1.34	0.51	0.21	0.15	0.04

1974	0.97	0.71	0.34	0.15	0.10	0.03

1975	0.29	0.23	0.11	0.06	0.05	0.01

1976	0.37	0.31	0.14	0.06	0.04	0.01

1977	0.27	0.20	0.09	0.04	0.03	0.01

1978	3.49	2.60	1.12	0.42	0.28	0.07

1979	0.31	0.23	0.16	0.08	0.05	0.01

1980	0.60	0.48	0.19	0.08	0.06	0.01

1981	0.33	0.25	0.12	0.06	0.04	0.01

1982	0.76	0.57	0.23	0.15	0.10	0.02

1983	0.20	0.15	0.08	0.03	0.02	0.01

1984	0.49	0.38	0.18	0.11	0.08	0.02

1985	1.46	1.08	0.44	0.18	0.14	0.04

1986	0.21	0.16	0.06	0.03	0.02	0.01

1987	0.04	0.03	0.01	0.01	0.00	0.00

1988	0.29	0.22	0.09	0.05	0.04	0.01

1989	1.40	1.08	0.46	0.18	0.12	0.03

1990	1.20	0.89	0.41	0.16	0.11	0.03

Sorted results

	Prob.	Peak	96 hr	21 Day	60 Day	90 Day	Yearly

0.03	3.49	2.60	1.12	0.42	0.28	0.07

0.06	1.77	1.34	0.51	0.21	0.15	0.04

0.10	1.46	1.08	0.46	0.18	0.14	0.04

0.13	1.40	1.08	0.44	0.18	0.12	0.03

0.16	1.21	0.96	0.41	0.17	0.12	0.03

0.19	1.20	0.89	0.37	0.16	0.11	0.03

0.23	0.99	0.76	0.36	0.15	0.10	0.03

0.26	0.97	0.73	0.36	0.15	0.10	0.03

0.29	0.97	0.71	0.34	0.14	0.10	0.02

0.32	0.84	0.61	0.30	0.14	0.10	0.02

0.35	0.76	0.57	0.23	0.13	0.09	0.02

0.39	0.60	0.48	0.19	0.11	0.09	0.02

0.42	0.53	0.38	0.18	0.11	0.08	0.02

0.45	0.51	0.37	0.16	0.08	0.06	0.01

0.48	0.49	0.36	0.15	0.08	0.05	0.01

0.52	0.37	0.31	0.15	0.06	0.05	0.01

0.55	0.33	0.26	0.14	0.06	0.05	0.01

0.58	0.33	0.25	0.13	0.06	0.05	0.01

0.61	0.32	0.23	0.12	0.06	0.05	0.01

0.65	0.31	0.23	0.12	0.06	0.04	0.01

0.68	0.29	0.23	0.11	0.05	0.04	0.01

0.71	0.29	0.22	0.09	0.05	0.04	0.01

0.74	0.29	0.21	0.09	0.05	0.04	0.01

0.77	0.27	0.20	0.09	0.04	0.03	0.01

0.81	0.21	0.16	0.08	0.04	0.03	0.01

0.84	0.21	0.16	0.08	0.04	0.03	0.01

0.87	0.20	0.15	0.06	0.03	0.02	0.01

0.90	0.13	0.10	0.06	0.03	0.02	0.01

0.94	0.12	0.09	0.03	0.02	0.02	0.00

0.97	0.04	0.03	0.01	0.01	0.00	0.00

0.10	1.45	1.08	0.46	0.18	0.14	0.03

Average of yearly averages:	0.02

Inputs generated by pe4.pl - 8-August-2003

	Data used for this run:

	Output File: NCsweet

	Metfile:	w13722.dvf

PRZM scenario:	NCSweetPotatoC.txt

EXAMS environment file: pond298.exv

Chemical Name:	Chloropicrin

Description	Variable Name	Value	Units	Comments

Molecular weight	mwt	164.4	g/mol

	Henry's Law Const.	henry	0.00205	atm-m^3/mol

Vapor Pressure	vapr	23.8	torr

	Solubility	sol	1621	mg/L

	Kd	Kd

mg/L

	Koc	Koc	36.05	mg/L

	Photolysis half-life	kdp	1.3	days	Half-life

Aerobic Aquatic Metabolism	kbacw

	31.42

	days

	Halfife

Anaerobic Aquatic Metabolism	kbacs	0.05	days	Halfife

Aerobic Soil Metabolism	asm	15.71	days	Halfife

Hydrolysis:	pH 7	0	days	Half-life

Method:	CAM	8	integer	See PRZM manual

	Incorporation Depth:	DEPI	25	cm

	Application Rate:	TAPP	392	kg/ha

	Application Efficiency:	APPEFF	1	fraction

	Spray Drift	DRFT	0	fraction of application rate applied to pond

Application Date	Date	15-4	dd/mm or dd/mmm or dd-mm or dd-mmm

Record 17:	FILTRA

IPSCND	1

	UPTKF

	Record 18:	PLVKRT

PLDKRT

FEXTRC	0

Flag for Index Res. Run	IR	Pond

Flag for runoff calc.	RUNOFF	none	none, monthly or total(average of
entire run)

B.4.   Calculation of 1-in-10 year EEC using Weibull Probability Plots.

Output from the PRZM/EXAMS simulation is typically a series of estimated
environmental concentrations (EEC) corresponding to multiple years of
meteorological data.  Each value is an estimate of the peak
concentrations corresponding to a specific averaging time (e.g., 96
hours, 21 days, etc.).  The 24-hour averaging time is sometimes referred
to as the “Peak” concentration because the shortest time-step for a
PRZM/EXAMS simulations is one day.  Therefore, the column of EEC values
reported in an output file for “Peak” refers to the maximum 24-hour
EEC for each of the meteorological years.

For ecological risk assessment, it is important to match the averaging
time to the duration of the toxicity study.  However, of the multiple
years of data, which EEC should be selected in the calculation of the
RQ?  The most conservative case would be to choose the maximum EEC for
each averaging time.  An alternative would be to calculate an upper end
value that is less than the maximum.  One statistic adopted by OPP for
use in ecological risk assessment is the 1-in-10 year return value.
This is the EEC that, on average, will be exceeded only once every 10
years.  It is important to note that for any single 10-year period, the
1-in-10 year value may be exceeded more than once, or not at all.  The
key concept is that it represents the average probability of exceedance.

The 1-in-10 year statistic can be calculated using probability plotting
methods.  There are a number of different techniques, but a common
practice in hydrology for plotting flow-duration and flood-frequency
curves is to use the plotting position associated with the Weibull
distribution (Helsel and Hirsch 1993).  The general formula for
probability plotting is given by:

where p is the probability level, n is the number of data points, and a
is a coefficient that varies between 0 and 0.5.  For the Weibull
distribution, a is 0 so the plotting position is

For the PRZM/EXAMS simulations presented above, there are 30 years of
meteorological data, so n = 30.  To generate a Weibull probability plot
to estimate the exceedance probabilities, the data should be sorted in
descending order.  That is, there is a lower probability of exceeding
the maximum EEC than the second highest EEC.  The plotting position
associated with the maximum value is then calculated as follows:

The minimum and maximum probability values associated with the entire
data set will approach [0, 1] as the sample size increases.  Sometimes
probability plots are used to estimate the values beyond the observed
range.  To calculate the 1-in-10 year statistic, we need the EEC
associated with a probability value of 0.100.  This value does not
correspond directly with any of the modeled values, but it is between
third highest value (p = 0.097) and fourth highest value (0.129).  An
interpolation procedure is needed to estimate the EEC associated with p
= 0.100.  A linear interpolation is commonly performed, although two
methods are available.  One method involves fitting a line to the entire
set of data plotted on a Weibull probability plot.  The second method
involves a linear interpolation only between the two values that
encompass the desired p-value.  PRZM/EXAMS output is based on the
Weibull plotting positions with a straight line interpolation between
just the two data values that encompass the desired p-value of 0.100.

	Appendix C:  Ecological Effects Data  TC \l2 "Appendix C:  Ecological
Effects Data

Overview

	The toxicity testing required does not test all species of birds, fish,
mammals, invertebrates, and plants.  Only two surrogate species for
birds (bobwhite quail and mallard) are used to represent all bird
species (over 1000 in the US, including subspecies),  three species of
freshwater fish (rainbow trout, bluegill sunfish and fathead minnow) are
used to represent all freshwater fish species (over 900 in the US), and
one estuarine/marine fish species (sheepshead minnow) is used to
represent all estuarine/marine fish (over 300 in the US).  The surrogate
species for terrestrial invertebrates is the honey bee, for freshwater
invertebrates the surrogate species is usually the waterflea (Daphnia
magna) and for estuarine/marine invertebrates the surrogate species are
mysid shrimp and eastern oyster.  These four species are used to
represent all invertebrate species (over 10,000 in the US).  For plants,
there are ten surrogate species used for all terrestrial plants and five
surrogate species used for all aquatic plants.  There are over 20,000
plant species in the US which includes flowering plants, conifers,
ferns, mosses, liverworts, hornworts and lichens with over 27,000
species of algae worldwide.

	The surrogate species testing scheme used in this assessment assumes
that a chemical’s mechanism of action and toxicity found for avian
species is similar to that in all reptiles (over 300 species in the US).
 The same assumption applies to amphibians (over 200 species in the US)
and fish; the tadpole stage of amphibians is assumed to have the same
sensitivity as a fish.  Therefore, the results from toxicity tests on
surrogate species are considered applicable to other member species
within their class and are extrapolated to reptiles and amphibians.  The
US species numbers noted in this section were taken from the Natureserve
website (   HYPERLINK http://www.natureserve.org www.natureserve.org
NatureServe: An online encyclopedia of life [web application].2000) and
the worldwide species number from Ecological Planning and Toxicology,
Inc.1996.

	In the following sections, the shaded values in the tables are the ones
used in the current risk assessment.

a.  Toxicity to Terrestrial Animals  TC \l3 "a.  Toxicity to Terrestrial
Animals

	  i.  Birds, Acute and Subacute  TC \l4 "i.  Birds, Acute and Subacute

An acute oral toxicity study using the technical grade of the active
ingredient (TGAI) is required to establish the toxicity of chloropicrin
to birds.  The avian oral LD50 is an acute, single-dose laboratory study
designed to estimate the quantity of toxicant required to cause 50%
mortality in a test population of birds.  The preferred test species is
either the mallard, a waterfowl, or bobwhite quail, an upland gamebird.
The TGAI is administered by oral intubation to adult birds, and the
results are expressed as LD50 milligrams (mg) active ingredient (a.i.)
per kilogram (kg) of body weight.  Toxicity category descriptions are
the following:

 	If the LD50 is less than 10 mg a.i./kg, then the test substance is
very highly toxic.

If the LD50 is 10-to-50 mg a.i./kg, then the test substance is highly
toxic.

If the LD50 is 51-to-500 mg a.i./kg, then the test substance is
moderately toxic.

If the LD50 is 501-to-2,000 mg a.i./kg, then the test substance is
slightly toxic.

If the LD50 is greater than 2,000 mg a.i./kg, then the test substance is
practically nontoxic.

Acute oral testing on chloropicrin is needed for risk assessment.

Two dietary studies using the TGAI are usually required to establish the
toxicity of pesticides to birds.  These avian dietary LC50 tests, using
the mallard and bobwhite quail, are acute, eight-day dietary laboratory
studies designed to estimate the quantities of toxicant in the feed
required to cause 50% mortality in the two respective test populations
of birds.  The TGAI is administered by mixture to juvenile birds' diets
for five days followed by three days of "clean" diet, and the results
are expressed as LC50 parts per million (ppm) active ingredient (a.i.)
in the diet.  Toxicity category descriptions are the following:

If the LC50 is less than 50 ppm a.i., then the test substance is very
highly toxic.

If the LC50 is 50-to-500 ppm a.i., then the test substance is highly
toxic.

If the LC50 is 501-to-1,000 ppm a.i., then the test substance is
moderately toxic.

If the LC50 is 1001-to-5,000 ppm a.i., then the test substance is
slightly toxic.

If the LC50 is greater than 5,000 ppm a.i., then the test substance is
practically nontoxic.

 However, dietary exposure is not considered to be the primary or even a
substantial route of avian exposure to chloropicrin, and thus avian
dietary toxicity data are not currently needed for risk assessment.
Inhalation is expected to be the primary route of exposure and thus
acute inhalation toxicity data on chloropicrin are needed for risk
assessment.

	ii.  Birds, Chronic  TC \l4 "ii.  Birds, Chronic

Chronic/sub-chronic inhalation testing with chloropicrin is needed to
assess risk to birds in part because of the potential for repeated or
continuous exposure resulting from multiple fields being treated on
differing days within a given geographic area.

	iii.  Mammalian Toxicity Data (from HED)  TC \l4 "iii.  Mammalian
Toxicity Data (from HED)

 Chloropicrin Toxicity Profile (from HED 1/31/05 review)

Guideline No./Study Type	MRID No. (year)/Classification/Exposure
Conditions	Results

870.1100

Acute Oral - Rat

	05014376 (1976)

Acceptable/Guideline.

	LD50 = 37.5 mg/kg

Toxicity Category I

870.1200

Acute Dermal - Rat

	05014376 (1976)

Acceptable/Guideline

	LD50 = 100 mg/kg

Toxicity Category I

870.1300

Acute Inhalation - Mouse

	45117901 (1999)

Acceptable/Non-Guideline

Head only study, 4 Albino Swiss-Webster male mice/grp exposed to 0.99,
3.20, 4.20, 7.25, 10.00, 14.50 ppm (analytical concen.)or 0.00664,
0.0215, 0.0282, 0.0486, 0.0671, 0.0973 mg/L (calculated analytical
concen.)of gaseous CP for 30 mins.	No deaths seen at any dose level.
Clinical obs. normal before and after exposure. Body wt. gains may been
decreased at HDT only (8% of initial body wt. in control and 2% at the
HDT).

-The exposure level at 50% RD (RD50) was 2.34 ppm with 95% CI of 1.84 to
2.98 ppm or RD50 of 0.016 mg/L and 95% CI of 0.012 mg/L to 0.020 mg/L.

-0% depression in the respiration rate was plotted by the % depression
in the respiration rate reported in the study versus log exposure level
and extrapolating the graph to 0% depression. The RD0 respiratory
depression occurs around 0.0017 to 0.0019 mg/L.

870.1300

Acute Inhalation - Rat	45117902 (1999)

Acceptable/Non-Guideline

Whole body inhalation study, 5 Sprague Dawley rats/sex/grp were exposed
to 0, 10.6, 18.0, or 28.5 ppm (analytical) or 0, 0.071, 0.121, 0.158
mg/L (calculated) of aerosolized CP for 4-hrs and held for 2 days after
exposure. Particle sizes had a MMAD from 4.85 µm to 6.1µm with a GDS
of 1.4 to 1.6. 	LC50 [typo corrected] was 17 ppm (M) and 19 ppm (F).

Death only occurred at 2 top dose levels up to 2 days post-exposure.

Clinical signs: obs noted at all dose levels, labored breathing,
gasping, decreased activity, nasal discharge, salivation, moist rales.
Top 2 levels produced gasping for last 2 hrs of exposure.

Gross pathology: Liver, adrenal wts, and histological findings increased
at HDT. Histological findings of respiratory tract were seen at all dose
levels and damage to the lungs, such as congestion, bronchiole mucosal
edema, necrosis, and cellular infiltrates.

-No NOAEL demonstrated.

LOAEL = 10.6 ppm or 0.071 mg/L (LDT).

870.2400C

Primary Eye Irritation - Rabbit

	N/A

	reserved

870.2500

Primary Skin Irritation - Rabbit

	05014376 (1976)

 Acceptable/Guideline

	Corrosive

Toxicity Category I

870.2600

Dermal Sensitization 	N/A

	Reserved

870.3100

Subchronic Feeding - Rat

Not required by the Agency

870.3100

Subchronic Feeding - Mice

Not required by the Agency

870.3100

Subchronic Feeding - Mice

Not required by the Agency

870.3150

Subchronic Feeding - Dog

Not required by the Agency

870.3200

21-Day Dermal - Rat

Reserved

870.3465

13-Week Inhalation - Mouse

	43063201 (1993)

Acceptable/Guideline

0, 0.3, 1.0, or3.0 ppm in a whole-body chamber, 6 h/day, 5 days/week for
13 weeks	NOAEL = 0.3 ppm (0.002 mg/L/day)

LOAEL = 1.0 ppm (0.007 mg/L/day) based on decreased body weight and food
consumption, increased absolute and relative lung weights in both sexes,
and histopathological lesions of the nasal cavity and lungs of females.

870.3465

13-Week Inhalation - Rat	43063201 (1993)

Acceptable/Guideline

0, 0.3, 1.0, or3.0 ppm in a whole-body chamber, 6 h/day, 5 days/week for
13 weeks	NOAEL = 0.3 ppm (0.002 mg/L/day)

LOAEL = 1.0 ppm (0.007 mg/L/day), based on increased lung weights of
both sexes, and histopathological changes in the nose of females and
lungs of males and females.

870.3700

Inhalation Developmental Toxicity - Rat

	42740602 (1993)

Acceptable/Guideline

0, 0.4, 1.2, or 3.5 ppm in a whole-body inhalation chamber, 6 h/day on
GDs 6-15.  	Maternal NOAEL = 0.4 ppm (0.003 mg/L/day)

Maternal LOAEL = 1.2 ppm (0.008 mg/L/day) based on mortality, decreased
body weight and food consumption, and signs consistent with CP toxicity.

Developmental NOAEL > 3.5 ppm (0.024 mg/L)

Developmental LOAEL= 3.5 ppm (0.024 mg/L), based on decreased pup body
weights.

870.3700

Inhalation Developmental Toxicity - Rabbit

	42740601 (1993)

Acceptable/Guideline

0, 0.4, 1.2, or 2.0 ppm in a whole-body inhalation chamber, 6 h/day, on
GDs 7-29.

	Maternal NOAEL is 0.4 ppm (0.003 mg/L)

Maternal LOAEL is 1.2 ppm (0.008 mg/L), based on mortality, body weight
loss, and decreased food consumption.

Developmental NOAEL= 0.4 ppm (0.003 mg/L)

Developmental LOAEL= 1.2 ppm (0.008 mg/L), based on abortions and
decreased fetal weights.

870.3800

Inhalation 2-Generation Reproductive Toxicity -

(Main study)

Rat	43391901 (1994)

Acceptable/guideline

0, 0.5, 1.0, or 1.5 ppm in whole body inhalation chamber

Note: Offspring not directly exposed until PND 28	Parental systemic
NOAEL > 1.5 ppm (0.0101 mg/L)

Parental systemic LOAEL not identified

Offspring NOAEL > 1.5 ppm (0.0101 mg/L)

Offspring LOAEL not identified

Reproductive NOAEL > 1.5 ppm (0.0101 mg/L)

Reproductive LOAEL not identified

870.3800

Range-finding, Inhalation 2-Generation Reproductive Toxicity - Rat
46427801 (conducted 1992, study report 1996)

0, 0.4, 1.0, or 2.0 ppm whole body for 6hrs/day, 7 days/week during
premating (14 days) and gestation day 0-20.	No treatment-related
mortality, clinical signs, or necropsy findings in any parental males or
females, and no treatment-related effects on reproductive parameters.
Mean body weight and weight gain decreased in high-dose group (1-3% M&
5-6% F) beginning at week 1.  Maternal body weight was decreased 5-8%
and decreased 17% during gestation.  Food consumption decreased 8-14% in
males and 14% in females during premating and 7% during gestation.
Litter size decreased 33% and uterine implantation sites decreased 30%
in the high-dose group.

870.4100

Chronic Feeding Toxicity-Rat	43744301 (1995)

Acceptable/guideline

Gavage at 0, 0.1, 1.0, or 10 mg/kg/day for 104 weeks.	Only clinical
toxicity observed was salivation after dosing in high-dose male and
female rats. Dose-related increase in incidence of subcutaneous masses
of skin of females related to the increased incidence of mammary
fibroadenomas. Hyper-keratosis and hyperplasia of the nonglandular
stomach in both sexes. Females had dose-related increase in incidence of
fibroadenoma of the mammary gland at high-dose. Increased rate of C-cell
hyperplasia of the thyroid in high-dose females.

NOAEL = 0.1 mg/kg/day [F]

NOAEL = 1.0 mg/kg/day [M]

LOAEL = 1.0 mg/kg/day [F], based on periportal hepatocyte vacuolation
and thyroid C-cell hyperplasia and stomach lesions at the high-dose.

LOAEL = 10 mg/kg/day [M], basedon on stomach lesions.

870.4100

Chronic Feeding Toxicity - Dog	43196301(1994)

Acceptable/guideline

0, 0.1, 1.0, or 5.0 mg/kg/day for one year (capsule).	NOAEL [M] = 0.1
mg/kg/day

NOAEL [F] = 1.0 mg/kg/day

LOAEL [M] = 1.0 mg/kg/day, based on gastrointestinal irritation
(vomiting and diarrhea), and blood chemistry alterations,

LOAEL [F] = 5.0 mg/kg/day, based on gastrointestinal irritation
(vomiting and diarrhea), microcytic hypochromatic anemia, and blood
chemistry alterations.

870.4200

Carcinogenicity Inhalation - Mouse (78 weeks) 	43632201 (1997)

Acceptable/guideline

0, 0.1, 0.5, or 1.0 ppm for 78 weeks	NOAEL = 0.1 ppm (0.0007 mg/L)

LOAEL = 0.5 ppm (0.0034 mg/L), based on systemic toxicity and
irritation, based on decreased body weights and gains, increased lung
weights, and histological changes in the nasal cavity, upper respiratory
tract and lungs.

No significant treatment-related increase in tumors.

870.4200

Carcinogenicity/gavage- Mouse/Rat [bioassay]	05014915 (1978)

supplemental

Rats: [M]: 0, 25 or 26 mg/kg/day

[F]: 0, 20, or 22 mg/kg/day

Mice [M]: 0, 66 mg/kg/day

[F]: 0, 33 mg/kg/day	High-incidence of early death in CP dose rats. No
neoplasm observed at higher incidences in dosed rats from controls.
Rapid decrease in survival after first year in both sexes of mice.

Proliferative lesions of squamous epithelium of the forestomach of mice
included two carcinomas and a papilloma. Statistical analysis did not
demonstrate related to CP.  Bioassay of CP did not permit evaluation of
carcinogenicity due to short survival time of mice and rats.

870.4300

Chronic Inhalation Toxicity/Carcinogenicity-Rat. (2 year)	43755301
(1995)

Acceptable/guideline

0, 0.15, 0.5, or 1.0 ppm in a whole body inhalation chamber for 6
hrs/day, 5days/week for up to 108 weeks.	NOAEL =0.1 ppm (0.0007 mg/L)

LOAEL = 0.5 ppm (0.0034 mg/L), based on increased mortality rate and
decreased mean survival time in males, and transiently decreased body
weight gains in both sexes.

Port of entry NOAEL = 0.5 ppm

Port of entry LOAEL = 1.0 ppm (males), based on severe rhinitis of the
anterior nasal cavity.

870.5100

Bacterial Reverse Mutation Test (Ames Assay)	41960801 (1990)

Acceptable/guideline	S9-activated CP is Mutagenic in Salmonella
typhimurium strains TA98,and  TA100.

870.5300

Mutagenic-Lymphoma Mutation-Mouse	41960803 (1990)

Acceptable/guideline	CP ranging from 0.038 to 0.75 nL/mL-S9 and 0.89 to
16 nL/mL +S9 did not induce a mutagenic response in two independently
performed mouse lymphoma forward mutation assays.

870.5375

In Vitro Chromosomal Aberration in Chinese Hamster Ovary	41960802 (1990)

Acceptable/guideline

	Nonactivated doses of CP from 0.75 to 1 nL/mL induced a reproducible
and significant clastogenic response in Chinese hamster ovary (CHO)
cells harvested 12 hours post-treatment.

Nonactivated CP was clastogenic over a narrow range of cytotoxic
concentrations. CP in the absence of S9 activation is a clastogen in
this mammalian test system.

870.5395

Unscheduled DNA Synthesis-Rat	41960804 (1990)

Acceptable/guideline	CP was not genotoxic in primary rat hepatocytes
over a concentration range (0.3 to 6 nL/mL) that included moderately
cytotoxic levels. CP showed no evidence of UDS.

870.6200

Inhalation Acute  Neurotoxicity - Rats

Not required by the Agency

870.6200

Feeding Subchronic  Neurotoxicity - Rats

Not required by the Agency

870.7485

Metabolism - Rat

Not available.

870.7600

Dermal Penetration - Rat

Not required by the Agency

b.  Toxicity to Freshwater Aquatic Animals  TC \l3 "b.  Toxicity to
Freshwater Aquatic Animals

	i.  Freshwater Fish, Acute  TC \l4 "i.  Freshwater Fish, Acute

Two freshwater fish toxicity studies using the TGAI are required to
establish the toxicity of chloropicrin to fish.   The preferred test
species are rainbow trout (a coldwater fish) and bluegill sunfish (a
warmwater fish).  Results of these tests are tabulated below. The
toxicity category descriptions for freshwater and estuarine/marine fish
and aquatic invertebrates, are defined below in parts per million (ppm).

If the LC50 is less than 0.1 ppm a.i., then the test substance is very
highly toxic.

If the LC50 is 0.1-to-1.0 ppm a.i., then the test substance is highly
toxic.

If the LC50 is greater than 1 and up through 10 ppm a.i., then the test
substance is moderately toxic.

If the LC50 is greater than 10 and up through 100 ppm a.i., then the
test substance is slightly toxic.

If the LC50 is greater than 100 ppm a.i., then the test substance is
practically nontoxic.

Table 3:  Freshwater Fish Acute Toxicity - Chloropicrin Technical

Species/

Flow-through or Static	% ai	LC50

 (ppb) 	Toxicity Category	MRID/Accession (ACC) No. Author/Year	Study
Classification

Bluegill Sunfish

(Lepomis macrochirus)/Static	99.0	<105	at least highly toxic	FTLR
439/McCann/1972	Suppl.

Rainbow Trout

(Oncorhynchus sp.)/Static	99.0	< 16.98	Very highly toxic	FTLR
425/McCann/1971

	Suppl.

The requirement for two freshwater fish acute toxicity studies has not
been satisfied.  Flow-through studies with measured concentrations are
needed to reduce uncertainty in the risk assessment.

	ii.  Freshwater Fish, Chronic  TC \l4 "ii.  Freshwater Fish, Chronic

A freshwater fish early life-stage test  is required for chloropicrin
since it is expected to be transported to water from the intended use
site, and one or more of the following conditions are met: (1) the
pesticide is intended for use such that its presence in water is likely
to be continuous or recurrent, (2) any aquatic acute LC50 or EC50 is
less than 1 ppm, and/or (3) the EEC in water is equal to or greater than
0.01 of any acute LC50 or EC50 value.   The preferred test species is
rainbow trout.

The fish early life-stage is a laboratory test designed to estimate the
quantity of toxicant required to adversely effect the reproduction of a
test population of fish.  The test should be performed using
flow-through conditions.   The test material is administered into water
containing the test species, providing exposure throughout a critical
life-stage, and the results, generally, are expressed as a No Observed
Adverse Effect Concentration (NOAEC) in parts per million or parts per
billion of active ingredient.  The No Observed Adverse Effect
Concentration  represents an exposure concentration, at or below which
biologically significant effects will not occur to species of similar
sensitivities.

	(iii)	Freshwater Invertebrates, Acute  TC \l4 "(iii)	Freshwater
Invertebrates, Acute

A freshwater aquatic invertebrate toxicity test using the TGAI is
required to establish the toxicity of chloropicrin to aquatic
invertebrates. The preferred test organism is Daphnia magna, but early
instar amphipods, stoneflies, mayflies, or midges may also be used.
Results of this test are tabulated below.

Table 5:  Freshwater Invertebrate Acute Toxicity - Chloropicrin

Species/

Flow-through or Static	% ai	LC50/EC50 (ppb) 	Toxicity Category
MRID/Accession (ACC) No. Author/Year	Study Classification

Daphnid

(Daphnia pulex)/static	> 96.5	< 71	very highly toxic	130704/Cody and
Shema/1983	Supplemental

1    Core (study satisfies guideline).  Supplemental (study is
scientifically sound, but does not satisfy guideline).

The requirement for an acute freshwater invertebrate acute toxicity
study has not been satisfied.  A flow-through study with measured
concentrations is needed to reduce uncertainty in the risk assessment.

	iv.  Freshwater Invertebrate, Chronic  TC \l4 "iv.  Freshwater
Invertebrate, Chronic

A freshwater aquatic invertebrate life-cycle test is required for
chloropicrin because this degradate is expected to be transported to
water from the intended use site, and one or more of the following
conditions are met: (1) the pesticide is intended for use such that its
presence in water is likely to be continuous or recurrent, (2) any
aquatic acute LC50 or EC50 is less than 1ppm, and/or (3) the EEC in
water is equal to or greater than 0.01 of any acute LC50 or EC50 value.
A flow-through study with measured concentrations is needed for risk
assessment.

c.  Toxicity to Estuarine and Marine Animals  TC \l3 "c.  Toxicity to
Estuarine and Marine Animals

	i.  Estuarine and Marine Fish, Acute  TC \l3 "	i.  Estuarine and Marine
Fish, Acute

	Acute toxicity testing with estuarine/marine fish is required for
chloropicrin since the active ingredient and or degradates are expected
to reach the marine/estuarine environment due to its expected use in
coastal counties.  The preferred test species is the sheepshead minnow.

	ii.  Estuarine and Marine Fish, Chronic  TC \l3 "	ii.  Estuarine and
Marine Fish, Chronic

	An estuarine/marine fish early life-stage toxicity test using
chloropicrin is reserved, pending submission and review of freshwater
fish chronic testing.

	iii.  Estuarine and Marine Invertebrates, Acute  TC \l3 "	iii.
Estuarine and Marine Invertebrates, Acute

	Acute toxicity testing with estuarine/marine invertebrates is required
for chloropicrin because it is expected to reach the marine/estuarine
environment due to its expected use in coastal counties.  The preferred
test species are mysid shrimp and eastern oyster.

	iv.  Estuarine and Marine Invertebrate, Chronic  TC \l3 "	iv.
Estuarine and Marine Invertebrate, Chronic

	An estuarine/marine invertebrate life-cycle toxicity test (Guideline
72-4b) using chloropicrin is reserved, pending submission and review of
freshwater invertebrate chronic testing.

	d.  Toxicity to Plants  TC \l3 "d.  Toxicity to Plants

	i.  Terrestrial Plants  TC \l4 "i.  Terrestrial Plants

	Terrestrial plant Tier I seedling emergence and vegetative vigor
testing of a  Typical End-Use product (TEP) is currently recommended for
all pesticides having outdoor uses (EFED Policy, Keehner. July 1999).
For seedling emergence and vegetative vigor testing, the following plant
species and groups should be tested: (1) six species of at least four
dicotyledonous families, one species of which is soybean (Glycine max)
and the second is a root crop, and (2) four species of at least two
monocotyledonous families, one of which is corn (Zea mays).  Tier I
tests measure the response of plants, relative to a control, at a test
level that is equal to the highest use rate expressed as pounds active
ingredeint per acre (lbs ai/A).  Tier II studies are required if the
Tier I studies indicate any of the test species, when exposed to the
test material, displayed a ≥25% inhibition or over-enhancement of
various growth parameters as compared to the control.  This guideline
has not been satisfied.

	ii.  Aquatic Plants  TC \l4 "ii.  Aquatic Plants

	Aquatic plant testing is recommended for all pesticides having outdoor
uses (EFED Policy, Keehner. July 1999).  The tests are performed on
species from a cross-section of the  aquatic plant population.  The
preferred test species are duckweed (Lemna gibba), marine diatom
(Skeletonema costatum), blue-green algae (Anabaena flos-aquae),
freshwater green alga (Selenastrum capricornutum), and a freshwater
diatom.  Tier I aquatic plant testing is a maximum dose test designed to
quickly evaluate the toxic effects to the test species in terms of
growth and reproduction and to determine the need for additional aquatic
plant testing.  Tier II aquatic plant testing is a multiple dose test of
the plants species that showed a phytotoxic effect to the pesticide
being tested at the Tier I level.  Tier II testing is designed to
determine the detrimental effect levels of the chemical on the aquatic
plants which showed a greater than 50% detrimental effect in Tier I
testing.

e.  Toxicity to Non-target Insects

An acute contact study with the honey bee (141-1) is required, since the
proposed uses are outdoors.

	Appendix D.  The  Risk Quotient Method and Levels of Concern  TC \l2
"Appendix D.  The  Risk Quotient Method and Levels of Concern

	Risk characterization integrates the results of the exposure and
ecotoxicity data to evaluate the likelihood of adverse ecological
effects.  The means of this integration is called the quotient method.
Risk quotients (RQs) are calculated by dividing exposure estimates by
acute and chronic ecotoxicity values.

	RQ = EXPOSURE/TOXICITY

	RQs are then compared to OPP's levels of concern (LOCs).  These LOCs
are used by OPP to analyze potential risk to nontarget organisms and the
need to consider regulatory action.  The criteria indicate that a
pesticide used as directed has the potential to cause adverse effects on
nontarget organisms.  LOCs currently address the following risk
presumption categories: (1) acute risks - regulatory action may be
warranted in addition to restricted use classification, (2) acute
restricted use - the potential for acute risk is high, but may be
mitigated through restricted use classification, (3) acute endangered
species - endangered species may be adversely affected, and (4) chronic
risk - the potential for chronic risk is high regulatory action may be
warranted.   Currently, EFED does not perform assessments for chronic
risk to plants, acute or chronic risks to  insects, or chronic risk from
granular/bait formulations to birds or mammals.

	The ecotoxicity test values (measurement endpoints) used in the acute
and chronic risk quotients are derived from required studies.  Examples
of ecotoxicity values derived from short-term laboratory studies that
assess acute effects are: (1) LC50 (fish and birds), (2) LD50 (birds and
mammals), (3) EC50 (aquatic plants and aquatic invertebrates) and (4)
EC25 (terrestrial plants).  Examples of toxicity test effect levels
derived from the results of long-term laboratory studies that assess
chronic effects are: (1) LOAEL or LOAEC (birds, fish, and aquatic
invertebrates) and (2) NOAEL or NOAEC (birds, fish and aquatic
invertebrates).  For birds, mammals, fish and aquatic invertebrates the
NOAEL or NOAEC generally is used as the ecotoxicity test value in
assessing chronic effects, although other values may be used when
justified.  Risk presumptions and the corresponding RQs and LOCs, are
tabulated below.

Table 1.  Risk presumptions for terrestrial animals  based on risk
quotients (RQ) and levels of concern (LOC).

Risk Presumption	RQ	LOC

Birds

Acute Risk 	EEC1/LC50 or LD50/ft2 or LD50/day3	0.5

Acute Restricted Use	EEC/LC50 or LD50/ft2 or LD50/day (or LD50 < 50
mg/kg)	0.2

Acute Endangered Species	EEC/LC50 or LD50/ft2 or LD50/day 	0.1

Chronic Risk	EEC/NOAEC	1

Wild Mammals

Acute Risk 	EEC/LC50 or LD50/ft2 or LD50/day		0.5

Acute Restricted Use	EEC/LC50 or LD50/ft2 or LD50/day (or LD50 < 50
mg/kg)	0.2

Acute Endangered Species	EEC/LC50 or LD50/ft2 or LD50/day		0.1

Chronic Risk 	EEC/NOAEC	1

 1  abbreviation for Estimated Environmental Concentration (ppm) on
avian/mammalian food items

 2  mg/ft2

 3  mg of toxicant consumed/day

  LD50 * wt. of bird

  LD50 * wt. of bird

Table 2.  Risk presumptions for aquatic animals based on risk quotients
(RQ) and levels of concern (LOC).

Risk Presumption	RQ 	LOC

Acute Risk	EEC1/LC50 or EC50	0.5

Acute Restricted Use	EEC/LC50 or EC50	0.1

Acute Endangered Species	EEC/LC50 or EC50	0.05

Chronic Risk	EEC/NOAEC	1

 1  EEC = (ppm or ppb) in water

Table 3.  Risk presumptions for plants based on risk quotients (RQ) and
levels of concern (LOC).

Risk Presumption	RQ	LOC

Terrestrial and Semi-Aquatic Plants

Acute Risk	EEC1/EC25	1

Acute Endangered Species	EEC/EC05 or NOAEC	1

		Aquatic Plants

Acute Risk	EEC2/EC50	1

Acute Endangered Species	EEC/EC05 or NOAEC 	1

1  EEC = lbs ai/A

2  EEC = (ppb/ppm) in water

	Appendix E.    Data Requirement Tables  TC \l1 "Appendix E.    Data
Requirement Tables

	Table A1(A). Ecological Effects Data Requirements for: Chloropicrin

Guideline #

Data Requirement	Are Additional Data Needed for Risk Assessment?

MRID #’s	Study Classification

  71-1(a)	Avian Acute Oral	Y	------------	------------

------	Avian Acute Inhalation	Y	------------	-----------

71-2(a)	Avian Dietary–quail	N	------------	------------

71-2(b)	Avian Dietary–mallard	N	------------	-------------

---------	Avian Subchronic/Chronic Inhalation 	Y	-------------
-------------

72-1(a)	Fish Acute Toxicity–bluegill	Y	FTLR 439	S

72-1(b)	Fish Acute Toxicity–rainbow trout	Y	FTLR 425	S

72-2(a)	Aquatic Invertebrate Acute Toxicity–freshwater	Y	130704	S

72-3(a)	Marine/Estuarine Acute Toxicity–Fish	Y	-------------
-------------

72-3(b)	Marine/Estuarine Acute Toxicity–Mollusk (shell deposition)	Y
------------

	-------------

72-3(c)	Marine/Estuarine Acute Toxicity–Shrimp	Y	------------
-------------

72-4(a)	Fish Early Life Stage–freshwater	Y	-------------	-------------

72-4(a)	Fish Early Life Stage– marine/estuarine	Reserved	------------
-------------

72-4(b)	Aquatic Invertebrate Life Cycle–freshwater 	Y	-----------
------------

123-1(a)	Seedling Germination/Seedling Emergence–Tier II 	Y
-------------	------------

123-1(b)	Vegetative Vigor–Tier II 	Y	-------------	------------

123-2	Aquatic Plant Growth – Tier II	Y

-----------

141-1	Honeybee Acute Contact 	Y	-------------	------------

A=Acceptable; S=Supplemental; U=Unnaceptable; W=Waived; N/A=Not
Applicable; NA=Not Available; Inv.=Invalid; R=Potentially Repairable

Table 1A (B). Environmental Fate Data Requirements for: Chloropicrin

Guideline #

Data Requirement	Is Data Requirement Satisfied?

MRID #’s	Study Classification

161-1	Hydrolysis	Y	43022401	A

161-2	Photodegradation in Water	Y	42900201	S

161-3	Photodegradation on Soil	N/A	NA	W

161-4	Photodegradation in Air	Y	05007865	A

162-1	Aerobic Soil Metabolism	Y	43613901	S

162-2	Anaerobic Soil Metabolism	N/A	----------	----------

162-3	Anaerobic Aquatic Metabolism	Y	43759301	S

162-4	Aerobic Aquatic Metabolism	N/A	----------	----------

163-1	Mobility-Column Leaching	Y	44191301	S

163-2	Laboratory Volatility	Y	43798601	A

163-3	Field Volatility	Reserved	----------	----------

164-1	Terrestrial Field Dissipation	N	43085101	S

165-4	Accumulation in Fish/

Bioconcentration	N/A	NA	W

A=Acceptable; S=Supplemental; U=Unnaceptable; W=Waived; N/A=Not
Applicable; NA=Not Available

p={i-a} OVER {n+1-2a}

p={i} OVER {n+1}

p SUB 1={1} OVER {30+1}=0.03226