Barry TA; Segawa R; Wofford P; Ganapathy C.  1997.  Off-site air monitoring following methyl bromide chamber and warehouse fumigations and evaluation of the Industrial Source Complex-Short Term 3 Air Dispersion Model. Chapter 14 in Fumigants: Environmental Fate, Exposure and Analysis, ACS Symposium Series 652.  Editors JN Seiber et al. American Chemical Society: Washington D.C., pp. 178 - 88.

Burns, L.A. 2002.  Exposure Analysis Modeling System (EXAMS): User Manual and system documentation. National Exposure Research Laboratory.  U.S. Environmental Protection Agency, Research Trianglr Park, NC 27711.    HYPERLINK http://www.epa.gov/ceampubl/swater/exams/index.htm http://www.epa.gov/ceampubl/swater/exams/index.htm

Carsel, RF; Imhoff, JC; Hummel, PR; Cheplick, JM; and Donigian, AS Jr. 1998. PRZM-3, A Model for Predicting Pesticide and Nitrogen Fate in the Crop Root and Unsaturated Soil Zones: Users Manual for Release 3.0. National Exposure Research Laboratory, Office of Research and Development, U.S. Environmental Protection Agency, Athens, GA.

  HYPERLINK http://www.epa.gov/ceampubl/gwater/przm3/index.htm http://www.epa.gov/ceampubl/gwater/przm3/index.htm

Carter, W.P.L., D. Luo, and I.L. Malkina. 1997. Investigation of the Atmospheric Reactions of Chloropicrin. Atmospheric Environment. 31:1425-1439.

CARB (California Air Resources Board).2005. Report for Air Monitoring Around a Bed Fumigation for Chloropicrin in Santa Cruz County, 2003. California Environmental Protection Agency Air Resources Board, Sacramento, Ca.   HYPERLINK http://www.cdpr.ca.gov/docs/empm/pubs/tac/studies/chlrpicrin.htm http://www.cdpr.ca.gov/docs/empm/pubs/tac/studies/chlrpicrin.htm

CARB (California Air Resources Board). 2004. Ambient Air Monitoring for Chloropicrin and Breakdown Products of Metam Sodium in Monterey and Santa Cruz Counties , Fall 2001.  California Environmental Protection Agency Air Resources Board, Sacramento, Ca.   HYPERLINK www http://www.cdpr.ca.gov/docs/empm/pubs/tac/studies/chlrpicrin.htm

CARB (California Air Resources Board). 2003a. Ambient Air Monitoring for Chloropicrin and Breakdown Products of Metam Sodium in Kern County , Summer 2001.  California Environmental Protection Agency Air Resources Board, Sacramento, Ca.   HYPERLINK http://www.cdpr.ca.gov/docs/empm/pubs/tac/studies/chlrpicrin.htm http://www.cdpr.ca.gov/docs/empm/pubs/tac/studies/chlrpicrin.htm

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 http://www.cdc.gov/mmwr/preview/mmwrhtml/mm5332a4.htm http://www.cdc.gov/mmwr/preview/mmwrhtml/mm5332a4.htm

CDPR (California Department of Pesticide Regulation. 2003. Semiannual report summarizing the reevaluation status of pesticide products during 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  HYPERLINK 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 Research Laboratories Division of Bio-Rad Laboratories, Inc. 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 chloropicrin: A farmer’s nightmare.  Bull. Environ. Contam. Toxicol. 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.

UNIDO. 2003. Ozone-friendly Industrial Development UNIDO in the Montreal Protocol - technology transfer to other countries. Impact and lessons learned - Fumigants. United Nations Industrial Development Organization, Vienna, Austria. 21 pp.

U.S. EPA (United States Environmental Protection Agency).1992. Pesticide in ground water data base. A compilation of monitoring studies: 1971-1991. A National summary. p. NS-163 (1992)

U.S. EPA. (United States Environmental Protection Agency). 1995. User’s Guide for the Industrial Source complex Dispersion Models. Volume 1. User Instructions. USEPA Office of Air Quality Planning and Standards; Emissions, Monitoring and Analysis Division, Research Triangle Park, North Carolina.

USEPA.  1998a.  Guidelines for Ecological Risk Assessment. Published on May 14, 1998, Federal Register 63(93):26846-26924. Risk Assessment Forum, U.S. Environmental Protection Agency, Washington, D.C. EPA/630/R-95/002F. 191 pgs. April.

USEPA (U.S. Environmental Protection Agency). 2002. Inventory of U.S. Greenhouse Gas Emissions and Sinks: 1990-2000. U.S. Environmental Protection Agency, Office of Atmospheric Programs, EPA 430-R-02_003.

U.S. EPA (United States Environmental Protection Agency). 2004. Health Effects Division’s Draft Standard Operating Procedures (SOPs) for Estimating Bystander Risk from Inhalation Exposure to Soil Fumigant.

USEPA (U.S. Environmental Protection Agency). 2005a. Overview of the Use and Usage of Soil Fumigants. Biological and Economic Analysis Division. U.S. Environmental Protection Agency, Office of Pesticide Programs. www.epa.gov/oppsrrd1/reregistration/soil_fumigants/soil_fumigant_use.pdf

USEPA (U.S. Environmental Protection Agency). 2005b. Environmental Fate and Ecological Risk Assessment for the Re-registration of Methyl Bromide. U.S. Environmental Protection Agency Office of Pesticide Programs, Washington, D.C.

USEPA (U.S. Environmental Protection Agency). 2005c. Human Health Risk Assessment: Chloropicrin. U.S. Environmental Protection Agency, Office of Pesticide Programs, Draft report.

U.S. Forest Service. 1995. Prepared by Information Venture, Inc. under U.S. Forest Service Contract. http://www.infoventures.com/e-hlth/

Wilhelm, S.N., K. Shepler, L.J. Lawrence, and H. Lee. 1996. Environmental fate of Chloropicrin. P 79-83. In J.N Seiber et al. (ed.) Fumigants: Environmental fate, exposure, and analysis. ACS Symp. Ser. 652. American Chemical Society, Washington, DC.

Woodrow, J.E., D.G. Crosby, and J.N. Seiber. 1983. Vapor-phase photochemistry of pesticides. Res. Rev. 85:111-125.

World Health Organization (WHO). 1998. Phosgene Health and Safety Guide. IPCS International Programme on Chemical Safety Health and Safety Guide No. 106. World Health Organization, Geneva, Switzerland. 16 pp.

World Meteorological Association.(WMO). 2002.WMO/UNEP Scientific Assessment of Ozone Depletion Report Number 47.

Yvon, S.A.. and J.H. Butler. 1996. An Improved Estimate of the Oceanic Lifetime of Atmospheric CH3Br. Geophysical Res. Lett. 23:53-56.

VI. Appendices  TC "VI. Appendices" \f C \l "1"

	Appendix A.  Environmental Fate and Transport Data  TC "Appendix A.  Environmental Fate and Transport Data" \f C \l "2"

161-1 Hydrolysis (MRID# 43022401)

eous 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 ± 1°C 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.

d 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.

methyl 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.

etected 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.

ate 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 "Appendix B. Aquatic Exposure PRZM/EXAMS Modeling" \f C \l "2"

	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 "Appendix C:  Ecological Effects Data" \f C \l "2"

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

	  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

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

 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

	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

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.

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lly significant effects will not occur to species of similar sensitivities.

	(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

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

	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

	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

	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

	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

	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

	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 "Appendix D.  The  Risk Quotient Method and Levels of Concern" \f C \l "2"

	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 "Appendix E.    Data Requirement Tables" \f C \l "2"

	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/

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[Federal Register Volume 86, Number 65 (Wednesday, April 7, 2021)]
[Notices]
[Page 18060]
[FR Doc No: 2021-07138]

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

ENVIRONMENTAL PROTECTION AGENCY

[FRL-10021-52-Region 3]

Notice of Administrative Settlement Agreement Pursuant to the
Comprehensive Environmental Response, Compensation, and Liability Act

AGENCY: Environmental Protection Agency (EPA).

ACTION: Notice; request for public comment.

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

SUMMARY: In accordance with the Comprehensive Environmental Response,
Compensation, and Liability Act (``CERCLA''), notice is hereby given
that a proposed administrative settlement agreement for recovery of
response costs (``Proposed Agreement'') associated with the
Transportation Drive PCB Superfund Site in Hazle Township, Luzerne
County, Pennsylvania (``Site'') was executed by the Environmental
Protection Agency (``EPA'') and is now subject to public comment, after
which EPA may modify or withdraw its consent if comments received
disclose facts or considerations that indicate that the Proposed
Agreement is inappropriate, improper, or inadequate. The Proposed
Agreement would resolve potential EPA claims against Consolidated
Lands, LLC (``Settling Party''). The Proposed Agreement would require
Settling Party to reimburse EPA $250,000.00 for response costs incurred
by EPA for the Site. For thirty (30) days following the date of
publication of this notice, EPA will receive electronic comments
relating to the Proposed Agreement. EPA's response to any comments
received will be available for public inspection by request. Please see
the ADDRESSES section of this notice for special instructions in effect
due to impacts related to the COVID-19 pandemic.

DATES: Comments must be submitted on or before May 7, 2021.

ADDRESSES: As a result of impacts related to the COVID-19 pandemic,
requests for documents and submission of comments must be via
electronic mail, except as provided below. The Proposed Agreement and
additional background information relating to the Proposed Agreement
are available for public inspection upon request by contacting Maria
Goodine, Compliance Officer, at<EMAIL_ADDRESS>Comments must be
submitted via electronic mail to this same email address and should
reference the ``Transportation Drive PCB Superfund Site, Proposed
Settlement Agreement'' and ``EPA CERCLA Docket No. CERC-03-2021-
0009CR.'' Persons without access to electronic mail may call Ms.
Goodine at<PHONE_NUMBER> to make alternative arrangements.

FOR FURTHER INFORMATION CONTACT: Maria Goodine (3SD41), Compliance
Officer, U.S. Environmental Protection Agency Region III, Phone: (215)
814-2488; email<EMAIL_ADDRESS>
    Dated: April 1, 2021.
Linda Dietz,
Acting Director, Superfund and Emergency Management Division, U.S.
Environmental Protection Agency, Region III.
[FR Doc. 2021-07138 Filed 4-6-21; 8:45 am]
BILLING CODE 6560-50-P