### 2 

# Problem Formulation for the Environmental Fate, Ecological Risk, Endangered Species, and Drinking Water Exposure Assessments in Support of the Registration Review of Hydramethylnon

N H N H

C F 3 

### C H C H C C H C H 

### C F 3 

### N N 

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## CAS: 67485

- 29

- 4 PC Code: 118401

Prepared by: 

### Edward Odenkirchen , Ph.D., Sr. Science Advisor He Zhong , Ph.D., Biologist U.S. Environmental Protection Agency Office of Pesticide Program s Environmental Fate and Effects Division Environmental Risk Branch I 1200 Pennsylvania Ave., NW Mail Code 7507P Washington, DC 20460 Reviewed by: 

### Anita Ullagaddi, Biologist Christopher Koper, Chemist

November 15 , 2012

### 3 Table of Contents

Executive Summary

................................ ................................ ................................ ........................ 4 1. Purpose

................................ ................................ ................................ ................................ ........ 4 2. Problem Formulation

................................ ................................ ................................ .................. 5 2.1. Nature of Regulatory Action

................................ ................................ ................................ 5 2.2. Previous Assessments

................................ ................................ ................................ .......... 6 2.2.1. Ecological Risk Assessments

................................ ................................ ........................ 6 2.2.2. Drinking Water Exposure Assessments

................................ ................................ ........ 6 3. Stressor Source and Distribution

................................ ................................ ................................ 7 3.1. Mechanism of Action

................................ ................................ ................................ .......... 7 3.2. Overview of Pesticide Use and Usage

................................ ................................ ................ 7 3.3. Env ironmental Fate and Transport

................................ ................................ ...................... 7 3.4. Clean Water Act

................................ ................................ ................................ ................ 10 4. Receptors

................................ ................................ ................................ ................................ .. 11 4.1. Effects to Aquatic Organisms

................................ ................................ ........................... 11 4.2. Effects to Terrestrial Organisms

................................ ................................ ....................... 14 4.3. Incident Databases Review

................................ ................................ ............................... 16 4.4. Ecosystems Potentially at Risk

................................ ................................ ......................... 16 5. Assessment Endpoints

................................ ................................ ................................ ............. 17 6. Conceptual Model

................................ ................................ ................................ .................... 17 6.1. Risk Hypothesis

................................ ................................ ................................ ................. 17 6.2. Conceptual Diagram

................................ ................................ ................................ .......... 17 7

. Analysis Plan

................................ ................................ ................................ ............................ 20 7.1. Stressors of Concern

................................ ................................ ................................ .......... 20 7.2. Measures of Exposure

................................ ................................ ................................ ........ 20 7.3. Measures of Effect

................................ ................................ ................................ ............. 22 7.4. Integration of Exposure and Effects

................................ ................................ .................. 23 7.5. Endangered Species Assessments

................................ ................................ ...................... 23 7.6. Endocrine Disruptor Screening

................................ ................................ .......................... 24 7.7. Drinking Water Assessment

................................ ................................ .............................. 25 7.8. Preliminary Identification of Data Gaps

................................ ................................ ............ 25 7.8.1. Environmental Fate Data

................................ ................................ ............................ 25 7.8.2. Ecological Effect Data

................................ ................................ ................................ 27 8. References

................................ ................................ ................................ ................................ 31 APPENDIX A. Submitted Environmental Fate and Effects Studies

................................ ......... 43 2 APPENDIX B. SI P v.1.0 and STIR v. 1.0 Descriptions, Assumptions, Inputs and Outputs

...... 43 APPENDIX C. Physical and Chemical Properties of Hydramethylnon Major Degradates

...... 43 7 APPENDIX D. Toxicity Data of ECOSAR estimation (EPI V4.10)

................................ ....... 43 8

### 4 Executive Summary

Hydramethylnon , t etrahydro

- 5,5

- dimethyl

- 2(1H)

- pyrimidinone [3

- [4

- (trifluoromethyl)phenyl]

- 1

- [2

- [4trifluorom ethyl)phenyl]ethenyl]

- 2

- propenylidene] hydrazone

, (CAS 67485

- 29

- 4; PC Code 118401)

, is a slow acting stomach toxicant registered for the control of ants , fire ants and cockroaches in grasses/non

- crop lands and non

- food use area in domestic dwellings and

c ommercial establishments

. The Agency has concluded that t he stressor of concern is the parent hydramethylnon

. Two known major degradates 1,5

- bis(alpha, alpha, alpha

- trifluoro

- p

- tolyl)

- 1,4

- pentadien

- 3

- one 

### ( CL98,724

, 28% ) and 4H

- pyrimido [2

- 1

- c]as

- triazio

- 4

- one1,6,7,8

- tetrahydro

- 7,7

- dimethyl

- 3

- [p

- (trifluoromethyl)

- styryl] ( CL247,176 , 25.2% and 30.5% ) will not be assessed further because of the low toxi city based on the ECO SAR analysis

. However, several unknown degradates from photolysis and anaerobic degr adation studies will be assumed as t he parent hydramethylnon unless the unknown s are proper ly identified.

T he drinking water ( DW) from surface water source will be assessed as h ydramethylnon may move horizontally through soil runoff , e.g. an aerial gran ular application following by a rain fall
event. H ydramethylnon appears to have a low potential for groundwater contamination d ue to the lack of movement of hydramethylnon in the soil profile under most conditions. Therefore, DW assessment from the groun d water source will not be conducted

. Data gaps of the environmental fate and potential ecological effects are identified and included in a data call

- in (DCI) section. The following is a brief summary , 1). Environmental Fate Data: A quatic photo de gradat ion (835.2240) , a naerobic aquatic metabolism (835.4400) studies , and aerobic aquatic metabolism study (835.4300). 2). E cologic al E ffect Data : Avian acute oral toxicity for passerine species (850.2100), saltwater invertebrate life cycle (850.1350), fresh w ater an saltwater fish early life stage (850

- 1400), plan toxicity (850.4100, and 850.4150) and growth (850.5400 and 850.4400). The value of the above data to the risk assessment and how uncertainty will be addressed in lieu of data are discussed in detail in section 7.8.2.

1. Purpose

The purpose of this problem formulation is to provide an understanding of what is known about the environmental fate and ecological effects of hydramethylnon considering its currently registered uses. Hydramethylnon (CAS 6 7485

- 29

- 4; PC Code 118401) is a slow acting stomach toxicant registered for the control of ants in grasses and non

- crop lands such as lawns, turfs, and non

bearing nursery stocks. It is also registered for the control of ants and cockroaches in non

- food u se areas in domestic dwellings and commercial establishments and for control of imported fire ants in areas of the southern United States where infestations occur. The registered granular or baits formulation may be applied via broadcast or spot treatment

. 

### Currently, 37 active labels are registered (USEPA 2012a) and among them, several formulations (Reg# 241

- 260, 241

- 261, 241

- 322 and 2724

- 496) are labeled for aerial broadcast application at 0.0176 lb a.i. /acre in airport/landing fields, animal housing pr emises, commercial/industrial lawns, golf course turf,

### 5 nonagricultural uncultivated lands, ornamental lawns and turf, pastures, rangeland and recreational areas etc. ( USEPA 2012 b ). In addition, the AMDRO granular formulation is also registered at 0.0219 l b a.i. /acre (not exceed 0.0876 lb a.i. /acre per year) for control of bigheaded ants on pineapples in Hawaii (USEPA 2003)

. The impregnated formulation may be applied as a bait to control household ants and cockroaches. Hydramethylnon is also used for co ntrol of subterranean termites in a bait package that is sold to and only for use by certified pest control

o perators (PCOs). 

### The above uses establish a complete environmental exposure pathway. Therefore, a comprehensive ecological risk assessment and ch aracterization is warranted for the hydramethylnon usage. Mitigation as a result of the Re

- registration Eligibility Decision (RED) (USEPA, 1998) required that all labels need to comply with worker protection standards (WPS) for occupational and residentia l use. In addition, the Agency has developed a program (the “Endangered Species Protection Program”) to identify pesticides whose use may cause adverse impacts on endangered and threatened species, and to implement mitigation measures that will eliminate the adverse impacts. 

### This document provides a plan for analyzing data relevant to hydramethylnon and for conducting environmental fate, ecological risk, endangered species, and drinking water exposure assessments for its registered uses. Additionally, th is problem formulation identifies data gaps, uncertainties, and potential assumptions used to address those uncertainties relative to characterizing the potential ecological risk associated with the registered uses of hydramethylnon.

2. Problem Formulati on
2.1. Nature of Regulatory Action

Under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA), all pesticides distributed or sold in the United States generally must be registered by the Environmental Protection Agency (Agency). In determinin g whether a pesticide can be registered in the U.S., the Agency evaluates its safety to non

- target species based on a wide range of environmental and health effects studies. In 1996, FIFRA was amended by the Food Quality Protection Act, and the Agency was mandated to implement a new program for the periodic review of pesticides, i.e
., Registration Review ( http://www.epa.gov/oppsrrd1/registration_review/ ). The Registration Review program is in tended to ensure that, as the ability to assess risk evolves and as policies and practices change, all registered pesticides continue to meet the statutory standard of no unreasonable adverse effects to human health and the environment. Changes in science , public policy, and pesticide use practices will occur over time. Through the new Registration Review program, the Agency periodically reevaluates pesticides to make sure that as change occurs, products in the marketplace can be used safely.

As part of the implementation of the new Registration Review program pursuant to Section 3(g) of FIFRA, the Agency is beginning its evaluation of hydramethylnon to determine whether it continues to meet the FIFRA standard for registration. This problem formulation f or the environmental fate, ecological risk, endangered species, and drinking water assessment chapter in support of the registration review of hydramethylnon will be posted in the initial docket which will open the public phase of the review process.

### 6 2.2. Previous Assessments

2.2.1. Ecological Risk Assessments

Hydramethylnon was developed by American Cyanamid in 1977 and first registered in the United States in 1980

. The reregistration eligibility decision (RED) assessed nonfood use for indoor and outdoo r residential and agricultural areas for the control of ants, cockroaches, termites and other domestic insects such as crickets, silverfish, palmetto bugs and water bugs (USEPA 1998). Based on the negligible residues from the grass and rangeland use, the RED concluded that the hydramethylnon uses pose minimal risk to freshwater and terrestrial non

target organism s. However, certain confirmatory data for avian reproduction were needed (USEPA 1998).

In 2003, a Section 3 new use assessment was completed for use of hydramethylnon on pineapples in Hawaii for control of bigheaded ants (PC Code Number: 118401, DP Barcode: D249596)”. This assessment estimated that the risk quotients exceed levels of concern for acute risk, acute restricted use, and acute enda ngered species risk presumption categories for 20

- g birds and 15

- g and 35

- g mammals. Also the risk quotients exceeded the levels of concern for acute restricted use and acute endangered species risk presumption categories for freshwater fish. The followi ng studies we re identified as data gaps: estuarine/marine fish LC 50 

### (850.1075), estuarine/marine invertebrate EC 50 

### ( 850.1035), sediment toxicity testing ( 850.1735 and 850.1740), aquatic photodegradation (835.2240), aerobic aquatic metabolism (835.4300), a nd terrestrial field dissipation (835.6100) . In addition, the same assessment recommended label revisions to specify the number of applications and the minimum interval between applications (USEPA 2003).

2.2.2. Drinking Water Exposure Assessments

Pr eviously conducted drinking water exposure assessments are listed in Table 1 . Based on the negligible residues from the grass and rangeland use, the RED concluded that hydramethylnon residues in drinking water were unlikely (USEPA 1998). However, in a Se ction 3 new use
assessment conducted since RED

, Tier

- 1 FIRST modeling show ed the peak (acute) and annual average (chronic) concentrations of 76.09 ppb and 1.45 ppb , respectively. The ground water concentrations are not likely to exceed 0.035 ppb by SCI

- G ROW modeling (USEPA 2003).

Table 1. Previous Hydramethylnon Drinking Water Assessments

Date References Purpose 03 /2003 DP 249596 Section 3 New Crop Use Registration of Hydrame th ylnon on Pineapples in Hawaii for Control of Bigheaded Ants

12/ 1998 EPA 738

- R

- 98

- 023 Reregistration Eligibility Decision (RED) Hydramethylnon

### 7 3. Stressor Source and Distribution

Hydramethylnon is a slow acting stomach toxicant registered in early 1980 for the control of ants in grasses and non

- crop lands such as lawns, tur fs, and non

- bearing nursery stocks. The active ingredient of hydramethylnon is formulated for 37 end use products, primarily as baits, to control ants and cockroaches in non

- food use areas in domestic dwellings and commercial establishments, fire ants in areas of the southern United States and subterranean termites.

3.1. Mechanism of Action

Hydramethylnon is a trifluoromethyl aminohydrazone and is metabolic inhibitor blocking the biological process in the insect that makes adenosine triphosphate (ATP). Hydr amethylnon acts upon the mitochondria where it disrupts cellular respiration by inhibiting the electron transport chain (ETC) at the cytochrome b

- c1 complex.

3.2. Overview of Pesticide Use and Usage

The use sites and usage s on the registered hydramethylnon ar e summarized by the B iological and Economic Analysis Division at the Agency (USEPA 2012a,b). The active ingredient of hydramethylnon is formulated for 37 end use products ( USEPA 2012a) such as: Amdro

, Combat

, Maxforce

, Sensible, and Siege, TC

- 250, Grants Kills, Liquid Ant Bait, RF

- 2018 Magma, and Raid registered, and sold in the United States by the registrants: BASF, Bayer Environmental Sciences, Whitmire Micro

- Gen Research Laboratories, Grant Laboratories, Wellmark International, S.C. Johnson & Son Inc, Bell laboratories, Combat Insect Control Systems, and Ambrands. Hydramethylnon is formulated as a granular, pelletted/tabletted, impregnated materials and solution

- ready to use as well as bait for control of imported fire ants, harvester ants, and leafcut ting ants in rangeland and pastures. The registered granular formulation may be applied via broadcast or to individual mounds for ant and fire ant control. S everal formulations (Reg# 241

- 260, 241

- 261, 241

- 322 and 2724

- 496) are labeled for aerial broadcas t application at 0.0176 lb a.i. /acre in airport/landing fields, animal housing premises, commercial/industrial lawns, golf course turf, nonagricultural uncultivated lands, ornamental lawns and turf, pastures, rangeland and recreational areas etc. (USEPA 2 012b)

. The maximum registered field broadcast application rate is 0.0219 lb a

. i

. / acre and not exceed 0.0876 lb a.i. /acre per year (USEPA 2012b)

. The impregnated formulation may be applied as a bait to control household ants and cockroaches. In additio n, hydramethylnon is also used for control of subterranean termites in a bait package that is sold to and only for use by certified PCOs.

3.3. Environmental Fate and Transport

Technical hydramethylnon (Fig. 1) is a yellow to tan crystalline solid with a char acteristic vegetable oil odor and melting point of 189

- 191 oC. The compound is insoluble in water (7

- 9) ppb (USEPA 1998), slightly soluble in alcohols, and soluble in acetone, chlorobenzene, and 1,2

- dichloroethane. Hydramethylnon vapor pressure is 2x10 - 8 

### mm of Hg @ 25 oC with an average

n

- octanol and water partition coefficient (Kow) 27,965 (or Log Kow = 4.45) (MRID 416125

- 02).

### 8 Two technical hydramethylnon products are registered by BASF Corporation (with 98% technical formulation 241

- 270) and Bell Labo ratories Inc. (with 99.5% technical formulation 12455

- 134).

The major degradation routes of hydramethylnon are abiotic photolysis and soil binding. Hydramethylnon's photolytic half

- life in water is ≤1 hour ( MRIDs 42238201 and 42473301). A major degradate CL247,176

, ( 4H

- pyrimido [2

- 1

- c]as

- triazio

- 4

- one1,6,7,8

- tetr ahydro

- 7,7

- dimethyl

- 3

- [p

- (trifluoromethyl)

- styryl] ) , represented 25.2% and 30.5% of the recovered 14 

### C

phenyl and 14 

### C

- pyrimidine radioactivity, respectively. Another major degradate CL98,724

, ( 1,5

- bis(alpha, alpha, alpha

- trifluoro

- p

- tolyl)

- 1,4

- pentadien

- 3

- one ) , represented 28.0% of recovered phenyl labeled material. In addition, four unidentified compounds were discernible in the pyrimidine radiolabeled and the phenyl radiolabeled samples, ranging from 29.6% to 7.6% of recovered radioactivity ( MRIDs 422382 01 and 42473301)

. Hydramethylnon soil photolysis is biphasic, with half

- lives of 4 days for the first phase and in about 30 days for the second phase with two unidentified degradates making up 10% of the applied radioactivity (MRIDs 42113401 and 42 3 53 801)

. Submitted mobility study shows that hydramethylnon adsorb strongly to soils: loamy sand, sandy loam, loam, and silt loam soils with reported K d 

### values ranged from 1039

- 1782 mL/g and K des 

### values ranged from 3330 to 5630 mL/g ( MRID 41888302) . Aerobic soi l metabolism study indicates that hydramethylnon appears to dissipate very slowly by biotic processes with 385 days half

- life for (MRID 00061709). The half

- lives of 445

- 552 days were reported for anaerobic aquatic metabolism (MRID 43102701). The compou nd is stable to hydrolysis at pH 5, pH 7, and pH 9 ( MRID 42194701)

. Field dissipation data showed hydramethylnon has 3 days and 55 days half

- lives in Florida and Texas field environments respectively (MRIDs 43293101 and 43293102). Therefore, hydramethyl non on soil surfaces appears to be non

- persistent (MRID 42353801) and immobile (MRID 41888302). However, below the soil surface hydramethylnon appears to be more persistent (MRID 43102701). Due to the lack of movement of hydramethylnon in the soil profil e under most conditions, hydramethylnon appears to have a low potential for groundwater contamination, but may move horizontally on the soil surface through runoff

, e.g. a broadcast granular application following by a rain fall event

. Hydramethylnon sh owed some tendency to accumulate in fish tissues with reported bioconcentration factors of 1300X in whole fish, 780X in fillet, and 1900X in viscera. Slow depuration (48 to 63% of residues depurated after a 14

- day clearance period) was observed. The

curre nt limited outdoor use patterns of hydramethylnon combined with its low aqueous solubility, tendency to rapidly photodegrade in water, and high soil sorption affinity suggest low potential for bioaccumulation in the environment. Appendix A includes a comp lete list of submitted studies. T he physical, chemical and environmental fate properties of hydramethylnon are listed in Table 2 , and of hydramethylnon major degradates are listed in Appendix C

.

### 9 Table 2. Physical, Chemical, and Environmental Fate P roperties of Hydramethylnon (PC 118401). Parameter Value Reference Comments
Parent

Chemical Hydramethylnon Hydramethylnon RED USEPA ( 1998)

Chemical Name Tetrahydro

- 5,5

- dimethyl

2(1H)

- pyrimidinone [3

- [4

- (trifluoromethyl)phenyl]

- 1

- [2

- [4trifluoromethyl) phenyl]ethen yl]

- 2

- propenylidene]hydrazone Hydramethylnon RED USEPA (1998 )

Chemical Family amidinohydrazone Hydramethylnon RED USEPA (1998 )

Empirical Formula C 25 H 24 F 6 N 4 MRID 41612502 Product Chemistry

SMILES N1CC(C)(C)CNC1=NN=C( C=Cc2ccc(C(F)(F)F)c c2)C= Cc3ccc(C(F)(F)F)cc3 EPI V4.10

CAS Number 67485

- 29

- 4 MRID 41612502 Product Chemistry

Structure MRID 41612502 Product Chemistry

Selected Physical/Chemical Parameters
Molecular mass 494.5 MRID 41612502 Product Chemistry

Solu bility (25°C) 7

- 9 ppb Hydramethylnon RED USEPA (1998)

Kow 27,965 MRID 41612502 Product Chemistry

Vapor pressure (23.1°C) < 2×10 - 8 mm Hg MRID 41612502 Product Chemistry

Henry’s law constant (25°C) 8.21×10 - 11 atm·m 3 /mol EPI Suite 4.10

Persistenc e Hydrolysis pH 5 835.2120 pH 7 pH 9 Stable MRID 42194701 Acceptable

Aqueous Photolysis (t 1⁄2 ) 835.2240 < 1hr MRID 42238201 MRID 42473301 Su pplemental

Soil Photolysis (t 1⁄2 ) 835.2410 30 (Pyrimidyl labeled) and 35 (Phenyl labeled) days MRID 42113401 MRID 42353801 Acceptable

### 10 Parameter Value Reference Comments Photodegradation in Air 835.2370 N/A (Waived)

Aerobic Soil Metabolism (t 1⁄2 ) 835.4100 391 (Pyrimidyl labeled) and 375 (Phenyl labeled) days MRID 42320801 Supplemental

Anaerobic Soil Metabolism (t 1⁄2 ) 835.4200 Stable (Not reported) MRID 00061709 Supplemental

Anaerobic Aquatic Metabolism (t 1⁄2 ) 835.4400 455 (Pyrimidyl labeled) and 552 (Phenyl labeled) days MRID 4310 2701 Supplemental

Ae robic Aquatic Metabolism (t 1⁄2) 835.4300 N/A

Bioaccumulation in Fish (Depuration half

- life) 850.1730 14 days (BCFs in blue g ill sunfish of 780 in fillet, 1300 in whole fish and 1900 in viscera) MRID 00101611 Acceptable

Mobility
Kd 8 35.1230 835.1240 Loam sand 1039 mL/g Sandy loam 1669 mL/g

Loam soil 1715 mL/g

Silt loam 1717 mL/g MRID 41888302 Acceptable

Laboratory Volatility 835.1410 N/A (Waived)

Field Volatility 835.8100 N/A (Waived)

Field Dissipation

Terrestrial Field Dissipation (t 1⁄2 ) 835.6100 3 days (Florida) & 55 days (Texas) MRID 43293101 & MRID 43293102 Supplemental & Supplemental



### 3.4. Clean Water Act

Hydramethylnon is not identified as a cause of impairment for any water bodies listed as impaired under section 303(d) of the Clean Water Act 1 

### . No total maximum daily loads (TMDL) have been developed 2 

### . The Impaired Waters and Total Maximum Daily Loads website can be consulted for more information 3



### . The Agency invites submission of water quality data for hydramet hylnon. To the extent possible, data should conform to the quality standards in the OPP Standard Operating Procedure: Inclusion of Impaired Water Body and Other Water Quality Data in OPP’s Registration Review Risk Assessment and Management Process 4 

### , in or der to ensure they can be used quantitatively or qualitatively in pesticide risk assessments.

1 http ://iaspub.epa.gov/tmdl_waters10/attains_nation_cy.cause_detail_303d?p_cause_group_id=885
2 h ttp://iaspub.epa.gov/tmdl_waters10/attains_nation.tmdl_pollutant_detail?p_pollutant_group_id=885&p_pollutant_ group_name=PESTICIDES
3 http://www.epa.gov/owow/tmdl/
4 http://www.epa.gov/oppfead1/cb/ppdc/2006/november06/session1

- sop.pdf

### 11 4. Receptors

Consistent with the process described in the Overview Document (USEPA, 2004), the risk assessment for hydramethylnon relies on a surrogate species approach. Toxicological data generated from surrogate test species, which are intended to be representative of broad taxonomic groups, are used to extrapolate the potential effects on a variety of species (receptors) included under these taxonomic groupin gs.

Acute and chronic toxicity data from studies submitted by pesticide registrants along with the available open literature will be used to evaluate the potential direct and indirect effects of hydramethylnon to aquatic and terrestrial receptors. This i ncludes toxicity on the technical grade active ingredient, degradates, and when available, formulated products (e.g., “Six

- Pack” studies). The open literature studies are identified through EPA’s ECOTOXicology (ECOTOX) database 5



### , which employs a literatu re search engine for locating chemical toxicity data for aquatic life, terrestrial plants, and wildlife. The evaluation of both sources of data may also provide insight into the direct and indirect effects of hydramethylnon on biotic communities from loss of species that are sensitive to the chemical and from changes in structure and functional characteristics of the affected communities. D ata from an ECOTOX run for hydramethylnon will be evaluated for possible quantitative and/or qualitative inclusion in the risk assessment in support of Registration Review.

Data requirements to support registration of a pesticide are typically for toxicity of the technical grade active ingredient and in certain cases toxicity of degradation products and formulations. St udies submitted by the registrant are listed in Appendix A . The ECOTOX database will be searched when the risk assessment for hydramethylnon is prepared. At that time, endpoints more sensitive than available guideline studies will be reviewed from the open literature studies.

A summary of data representing non

- target organisms exposed to hydramethylnon in aquatic and terrestrial habitats is provided in Sections 4.1 and 4.2. A summary of ecological incidents associated with hydramethylnon and a description of ecosystems potentially at risk are provided in Section 4.3.

4.1. Effects to Aquatic Organisms

Acute toxicity data indicate that technical grade hydramethylnon is highly toxic to fish (freshwater and marine/estuarine) and freshwater invertebrates. No dat a are currently available (pending review of public literature) for hydramethylnon toxicity to marine/estuarine invertebrates, algae, or multicellular plants. Data are not available that evaluate chronic toxicity to any aquatic organisms. Table 6 summari zes the effects from the available studies which will be considered in the risk assessment. Appendix A includes a complete list of submitted studies.

5 http://cfpub.epa.gov/ecotox/

### 12 Table 6. Summary of Toxicity of Hydramethylnon (TGAI) to Aquatic Organisms

Species Exposure Scenario % AI Toxicity MRID Toxicity Category Classification

Rainbow trout (Oncorhynchu smykiss) 96 hour 850.1075 92 LC 50 = 0.157 mg

a

. i

. /L 35279 Hi ghly toxic acceptable

Bluegill sunfish (Lepomis macrochirus) 96 hour 850.1075 92 LC 50 = 1.67 mg

a

. i

. /L 35279 Mode rate toxic acceptable

Channel catfish ( Ictalurus punctatus ) 96 hour 850.1075 92 LC 50 = 0.090 mg

a

. i

. /L 52858 Very h ighly toxic acceptable

Waterflea (Daphnia magna) 48 hour 850.1010 92 EC 50 = 1.14 mg

a

. i

. /L 35877 Moderate toxic acceptable

Mysid Shrim p (Americamysis Bahi) 48 hour 850.1035 97.8 LC 50 = 0.0544 mg a.i./L 46684802 Very h ighly toxic acceptable

Sheepshead Minnow, ( Cyprinodon variegatus ) 96 hour 850.1075 97.8 LC 50 = >0.976 mg a.i./L 46684803 H ighly toxic acceptable

Midge larvae (Chironomus dilutus) 850.1735 97.8 Pore water LC 50 = >0.079 mg a.i./L NOAEC 0.079 mg a.i./L

Sediment LC 50 = >929 mg a.i./kg

- dw NOAEC 929 mg a.i./kg

- dw

Overlying Water LC 50 = >0.015 mg a.i./L NOAEC 0.015 mg a.i./L 46684805 Very h ighly toxic

Practically

no n

- toxic

Very h ighly toxic acceptable

Marine amphipod, ( Leptocheirus plumulosus) 850.1740 97.8 LC 50 = 2.2 mg a.i./L NOAEC 0.504 mg a.i./L 46684804 Moderately toxic acceptable

### 13 No empirical data for the primary degradates identified in environme ntal fate studies are available

. The OPP/Health Effect s Division used the potential toxicity concern prediction tool
DEREK to conclude that neither of the two degradates (CL98,724 and CL247,176) is likely to be toxic as the parent hydramethylnon. In addi tion, ECO SAR analysis by EFED estimated much less toxic potency of the two degradates than that of the parent compound (Appendix D)

. Therefore, degradates CL98,724 and CL247,176 will not be warranted for further assessment

.

Aquatic Animal

Acute Effects

F reshwater Fish

Of the three species tested, rainbow trout, bluegill sunfish , and channel catfish, the lat t er species is the most sensitive and that endpoint, pending review of public literature, would serve as the effects basis for acute freshwater fish ri sk assessment. Data acceptable for risk assessment are not available for formulations or degradation products.

Freshwater Invertebrates

Only one species is available, pending public literature review. The daphnid endpoint would serve as the basis for ac ute freshwater invertebrate risk assessment.

Marine

- Estuarine Fish

Only one tested species, sheepshead minnow has been tested and this endpoint would serve as the estuarine/marine fish acute risk assessment effects endpoint , pending public literature revie w

.
Marine

- Estuarine Invertebrates

One species of estuarine/marine invertebrates has yielded a valid acute toxicity test result (mysid shrimp) and would be used in the acute risk assessment , pending public literature review

.

Chronic Effects

No freshwater o r estuarine/marine fish nor estuarine marine invertebrate chronic data are available, pending public literature review.

A supplemental study with Daph n ia magna is available. The study was found to exhibit a statistically significant effect in the solven t control versus water control . Therefore, the study is incapable of providing a reliable estimate of a no effect concentration for hydramethylnon and cannot be used quantitatively in risk assessments. While the study is useful to demonstrate effects it cannot be reliable used quantitatively.

### 14 Sediment Dwelling Organisms

Two species of benthic invertebrates have been tested (a marine amphipod and a chironomid midge). Pending further data from the literature, both studies provide acceptable acute lethal

en dpoints and no effect endpoints for sediment risk assessment.

Aquatic Plants

Pending a public literature review, no data are available for assessing the effects of hydramethylnon to aquatic plants

.

4.2. Effects to Terrestrial Organisms

Acute toxicity data i ndicate that technical grade hydramethylnon is slightly toxic to birds and mammals.

Table 7 summarizes the effects from the available studies which will be considered in the risk
assessment. Appendix A includes a complete list of submitted studies.

Table 7. Summary of Toxicity of Hydramethylnon (TGAI) to Terrestrial Organisms Species Test Type % AI Toxicity MRID Toxicity Category Classification

Mallard duck ( Anas platyrhynchos ) 850.2100 92 LD 50 = 2510 mg

a

. i

. /kg

- bw 64575 Slightly toxic Acceptabl e (“Core”)

Bobwhite quail ( Colinus virginianus ) 850.2100 92 LD 50 = 1828 mg

a

. i

. /kg

- bw 32038 or 64576 Slightly toxic Acceptable (“Core”)

Mallard duck ( Anas platyrhynchos ) 850.2200 96 LC 50 = 4355 mg

a

. i

. /kg

- diet 32039 or 85931 Slightly toxic Acceptab le (“Core”)

Bobwhite quail ( Colinus virginianus ) 850.2200 92 LC 50 = 1780 mg

a

. i

. /kg

- diet 32040 or 64577 Slightly toxic acceptable (“Core”)

Mallard duck ( Anas platyrhynchos ) 850.2300 97.8 NOAEC: 28.5 mg a.i./kg diet LOAEC: 57.0 mg a.i./kg diet

Based on 14 days survival 45449702 Not Applicable acceptable

Bobwhite quail ( Colinus virginianus ) 850.2300 97.8 NOAEC 57 mg a.i./kg diet
LOAEC ≥ 57 mg a.i./kg diet 45449701 Not Applicable acceptable

Laboratory rat Oral dose 95 LD 50 41612503 acceptable

### 15 Species Test Type % AI Toxicity MRID Toxicity Category Classification

(acute) (males) = 817 mg a.i ./kg

- bw (females) = 1502 mg a.i./kg

- bw Moderately toxic

Slightly toxic (“Core”)

Laboratory rat 3

- g eneration reproduction study 93.3 NOAEL = 50 mg a.i./kg diet LOAEL = 100 mg a.i./kg diet

based on male infertility 35525, 35526, 1015 75 Not Applicable acceptable

Honey bee (Apis mellifera 850.3020 96.8 LD 50 68 ug a.i./bee 41607801 Practically nontoxic acceptable



### Terrestrial Animals

Acute Effects

Birds

Of the two species of birds tested in single oral dose and subacute dietary dose experiments (mallard duck and bobwhite quail) the quail provides the most sensitive acute and subacute endpoints for use in risk assessment.

Data are not available on acute oral toxicity to a passerine species. In addition, data are not available fo r formulations.

Insects

Acute toxicity to honeybee data is available from one study and will be used in the risk
assessment.

Mammals

Acute toxicity testing indicates that technical hydramethylnon produced an LD 50 

### of 817 mg/kg

bw in males and 1502 mg/kg

- bw in females

.

### 16 Chronic Effects

Two species of birds (mallard duck and bobwhite quail) have been studies in a long

- term reproduction test. Of the two species, the mallard duck was the most sensitive (survivors of hatchlings) and this endpoint wil l be used in the risk assessment.

A 3

- generation reproduction study is available for rats exposed to technical hydramethylnon and the male infertility NOAEC and will serve as the reproduction endpoint in the risk assessment.

Terrestrial Plants

Pending li terature review, no data are available for effects on terrestrial plants.

4.3. Incident Databases Review

A preliminary review on August 22, 2012, of the Ecological Incident Information System (EIIS, version 2.1.1), which is maintained by the Agency’s Office o f Pesticide Programs, and the Avian Monitoring Information System (AIMS), which is maintained by the American Bird Conservancy, indicates there are no reported ecological incidents associated with the use of hydramethylnon.

However, incidents have been r eported to the Agency in aggregated incident reports. Pesticide registrants report certain types of incidents to the Agency as aggregate counts of incidents occurring per product per quarter. Ecological incidents reported in aggregate reports include tho se categorized as ‘minor fish and wildlife’ (W

- B), ‘minor plant’ (P

- B), and ‘other non

- target’ (ONT) incidents. ONT incidents include reports of adverse effects to insects and other terrestrial invertebrates. For hydramethylnon, registrants have reported 4 minor fish and wildlife incidents, no minor plant incidents, and no other non

- target incidents. Unless additional information on these aggregated incidents becomes available, they will be assumed to be representative of registered uses of hydramethylno n in the risk assessment.

. 4.4. Ecosystems Potentially at Risk

The ecosystems at risk are often extensive in scope; therefore, it may not be possible to identify specific ecosystems during the development of a nation

- wide ecological risk assessment. Te rrestrial ecosystems potentially at risk could include the treated site and immediately adjacent areas that may receive spray drift or runoff. Aquatic ecosystems potentially at risk from hydramethylnon due to granular broadcast application , runoff, or er osion include water bodies adjacent to or downstream from the treated area and could include impounded bodies such as ponds, lakes and reservoirs, or flowing waterways such as streams or rivers. For uses in coastal areas, aquatic habitat also includes mar ine ecosystems, including estuaries.

### 17 5. Assessment Endpoints

Assessment endpoints represent the actual environmental value that is to be protected, defined by an ecological entity (species, community , or other entity) and its attribute or characteristi cs (USEPA, 1998). For hydramethylnon, the ecological entities may include the following: birds, mammals, terrestrial

- phase amphibians, reptiles, freshwater fish and invertebrates, aquatic

- phase amphibians, estuarine/marine fish and invertebrates, terrest rial plants, terrestrial invertebrates, and aquatic plants. The attributes for each of these entities include growth, reproduction, and survival.

6. Conceptual Model

For a pesticide to pose an ecological risk, it must reach ecological receptors in biol ogically significant concentrations. An exposure pathway is the means by which a pesticide moves in the environment from a source to an ecological receptor. For an ecological pathway to be complete, it must have a source, a release mechanism, an environm ental transport medium, a point of exposure for ecological receptors, and a feasible route of exposure. The conceptual model for hydramethylnon provides a written description and visual representation of the predicted relationships between hydramethylnon, potential routes of exposure, and the predicted effects for the assessment endpoint. A conceptual model consists of two major components: risk hypothesis and a conceptual diagram (USEPA, 1998).

6.1. Risk Hypothesis

A risk hypothesis describes the predi cted relationship among the stressor, exposure, and assessment endpoint response along with the rationale for their selection. For hydramethylnon, the following ecological risk hypothesis is being employed for this national

- level ecological risk

assessmen t:

Hydramethylnon, when used in accordance with current labels, can result in offsite movement of the compound via runoff, leading to exposure of non

- target plants and animals. Application of hydramethylnon to outdoor areas may serve as a major source of hydramethylnon exposure to wildlife. When used in accordance with the labels, hydramethylnon use may cause adverse effects upon the survival, growth, and reproduction of non

- target terrestrial and aquatic organisms. These non

- target organisms include fe derally

- listed threatened and endangered species.

6.2. Conceptual Diagram

The formulations employed and the environmental fate properties of hydramethylnon indicate that broadcast application and runoff, represent potential transport mechanisms to aqua tic and terrestrial habitats where non

- target organisms may be either directly or indirectly exposed. These transport mechanisms (i.e., sources) are depicted in the conceptual diagrams below ( Figures 1, and 2 ) along with the receptors of concern and the p otential attribute changes in the receptors due to hydramethylnon exposure. Solid arrows depict the most likely routes of

### 18 exposure and effects; dashed lines depict potential routes of exposure that are not considered likely for hydramethylnon. Figure 1 r epresents the expected aquatic exposure pathways; Figure 2 focuses on exposure pathways for terrestrial plants, terrestrial invertebrates, and dietary routes of exposure for terrestrial vertebrates. Drinking water and inhalation risks for terrestrial wild life were not considered in the conceptual diagram based on the “no concern” conclusions drawn from screening model runs for theses pathways described elsewhere in this document. At the present time, the Agency does not have a method to quantify the derma l routes of exposure to terrestrial wildlife, and data are limited to quantify the contribution of such exposures to the toxic burden an organism experiences.

Figure 1. Conceptual model for exposure and effects of h ydra methylnon to aquatic organisms. Dotted lines indicate exposure pathways that have a low likelihood of contributing to ecological risk. * Route of exposure includes only ingestion of fish and aquatic invertebrates



### Stressor

Source

Receptors

Attribute Change Hydramethylnon Applied to Use Site

Spray drift

Aquatic animals Invertebrates Vertebrates Piscivorous mammals

and birds *

Individual organisms Reduced survival Reduced growth Reduced reproduction Food chain Reduction in algae and

vascular plants Reduction in prey Modification of PCEs

related to prey availability Habitat integrity Reduction in primary pro ductivity Reduced cover Community change Modification of PCEs related to

habitat Surface water/

Sediment Runoff

Aquatic Animals Invertebrates Vertebrates 

### Exposure Media

Upt ake/gills or integument

Ingestion Ingestion Atmospheric transport Soil Leaching to Groundwater

Uptake/gills or integument

Aquatic Plants Non

- vascular Vascular Uptake/cell, roots, leaves Riparian plants terrestrial exposure pathways see Figure 2 Off

- Gassing

Wet/dry Deposition

### 19 Figure 2. Conceptual model for exposure and effects of h ydramethylnon to terrestrial organisms. Dotted lines indicate exposure pathways that have a low likelihood of contributing to ecological risk. Irrigation water Stressor

Source

Attribute Change Hydramethylnon Applied to Use Site

Direct application Spray drift

Terrestrial vertebrates* Terrestrial

Inverts*

Individual organisms Reduced survival Reduced growth Reduced reproduction Food chain Reduction in prey and food Modification of PCEs related to prey availability Habitat integrity Reduction in primary productivity Reduced cover Community change Modification of PCEs related to habitat Terrestrial

plants grasses/forbs, Runoff

Terrestrial vertebrates* Exposure Media & Receptors Soil

Ingestion Ingestion Dermal uptake /Ingestion Atmospheric transport

Root uptake/contact Wet/dry deposition

Ingestion Leaching to Groundwater

Off

- gassing

### 20 7. Analysis Plan

In order to address the risk hypothesis, the potential for adverse effects on the environment is estimated. The use, en vironmental fate, and ecological effects of hydramethylnon are characterized and integrated to assess the risks.

This analysis plan will be revisited and may be revised depending upon a full review of the data available in the open literature and the in formation submitted by the public in response to the opening of the Registration Review docket.

7.1. Stressors of Concern

The stressor of concern is the parent hydramethylnon

. F our unidentified compounds were discernible in the pyrimidine radiolabeled and the phenyl radiolabeled samples, ranging from 29.6% to 7.6% of recovered radioactivity found from aqueous photolysis studies ( MRID s 42 238201 and 4 2473301 ) and two unidentified degradates making up 10% of the applied radioactivity from soil photolysis s tudies (MRIDs 42113401 and 42353801) will be treated as the parent unless the unknown s are identified and the toxicities are assessed. T wo major degradates CL98,724 (28%) and CL247,176 (31%) are not warranted for further assessment based on DEREK and ECO S AR estimation (Appendix D) . In addition , the Agency will review open literature to identify degradate(s) of potential toxicological concern. Data sources that will be used in the future assessment include: 1) registrant submissions in support of registra tion review; 2) publicly available literature on ecological effects; 3) monitoring data for freshwater streams, lakes, reservoirs, and estuarine areas; and 4) incident reports of adverse effects on aquatic and terrestrial organisms associated with the use of hydramethylnon.

7.2. Measures of Exposure

Hydramethylnon exposures in aquatic and terrestrial environments will be evaluated by available standard models. The risk conclusions in perspective scenarios will need to be based on maximum labeled appli cation rate, number of applications, and minimum application intervals and application methods that have the greatest potential for off

- site transport for the currently registered use.

Aquatic Exposure

The expected environmental concentrations (EECs) are modeled based on parent hydramethylnon only . The EECs of surface water source will be used to calculate the risk quotient (RQ) for assessing the acute and chronic risks to aquatic organisms. A Tier

- II PRZM/EXAM models coupled with the input shell PE 5.pl (August, 2007) will be used to generate EECs for acute and chronic exposure, e.g., peak for acute, 21 days average for chronic invertebrate and 60 days average for chronic fish exposures. More specific model information in Office of Pesticide Progra ms, USEPA is available online (http://www.epa.gov/oppefed1/models/water/index.htm).

### 21 Terrestrial Exposure

There is potential exposure to non

- target organisms through consumption of contaminated food items (e.g. treated insects or vegetation), direct appli cation, and runoff

. EEC values used for terrestrial vertebrate exposure will be derived from the Kenaga nomograph ( Hoerger and Kenaga, 1972) as modified by Fletcher et al. (1994) using the T

- REX model (version 1. 5.1 ). The upper lim it values from the nomograph represent the 95 th 

### percentile of residue values from actual field measurements. The Fletcher et al. (1994) modifications to the Kenaga nomograph are based on measured field residues from 249 published research papers, includin g information on 118 species of plants, 121 pesticides, and 17 chemical classes. For input into T

- REX, the default foliar dissipation half

- life of 35 days will be used due to insufficient foliar dissipation rate data on hydramethylnon. Hydramethylnon

- onl y EECs will cover risk from the degradation products given the labeled maximum application rate is for a single annual application if degradation products are not more toxic than hydramethylnon.

If terrestrial plant toxicity data become available, TerrPla nt (version 1.2.2, 12/26/2006) will be used to calculate EECs for characterizing exposure to terrestrial and semi

- aquatic plants. This model estimates pesticide concentrations in runoff and in spray drift. EECs are based upon application rate, solubility , incorporation depth, and application method and form.

SIP

The Screening Imbibition Program (SIP v.1.0, Released June 15, 2010) was used to calculate an upper bound estimate of bird and mammal exposure to hydramethylnon in drinking water. The estima te is calculated using the solubility limit of hydramethylnon in water (0.009 mg/L at 25°C). Risk is assessed using the most sensitive acute and chronic avian toxicity endpoints and the most sensitive acute and chronic mammalian toxicity endpoints (data s ummarized elsewhere in this document). Appendix B provides a description of the model, assumptions in deriving an upper bound exposure estimate, and model results. Detailed information about SIP v.1.0, as well as the tool, can be found on the EPA’s websi te at http://www.epa.gov/pesticides/science/models_pg.htm#terrestrial

. Drinking water exposure alone was not determined to be a potential acute concern for mammals or birds

.

STIR

STIR v.1.0, S creening T ool for I nhalation R isk, is used to provide an upper bound estimate of exposure of birds and mammals to pesticides through inhalation of spray drift or vapor. The upper bound exposure estimate requires a number of input pa rameters including the vapor pressure and molecular weight for the vapor

- phase pesticide; additionally it requires the application rate and method of application (i.e., ground or aerial) for spray drift. The toxicity aspect of the tool requires an avian a cute oral LD 50 

### value (the model provides an estimate of avian inhalation toxicity in the absence of such data), the chemical specific avian allometric scaling factor to adjust toxicity based on body weight for the chemical (if available), the weight

### 22 of the tested bird, a rat acute oral LD 50 

### value, a rat acute inhalation LC 50 

### value, the duration of the rat inhalation study, and the weight of the tested rat. This tool was designed for use in the Problem Formulation phase of the ecological risk assessment pro cess to quantitatively evaluate the need for further analysis of inhalation as a potential pathway of concern for birds and mammals.

STIR was used to evaluate the potential for significant avian risk from inhalation of hydramethylnon using an assumed va por pressure of 2 X 10 - 8 

### mm H g (this value is conservative as reported vapor is less than the value). Acute oral toxicity for birds and rats was derived from values posted elsewhere in this document and an acute inhalation value for rats was from MRID 428 71101 as 2.9 mg/L over 4 hours of exposure. The S TIR results did not indicate that the inhalation pathway should be of concern even under conse rvative assumptions of exposure f or hydrame th ylnon for the highest broadcast application rate of 0.0176 lb a.i./ acre. Appendix B provides a description of the model, assumptions in deriving an upper bound exposure estimate, and model results.

7.3. Measures of Effect

Ecological effects data are used as measures of direct and indirect effects to biological recept ors. As discussed previously, data are obtained from registrant

- submitted studies or from literature studies identified by ECOTOX. The ECOTOX database provides more ecological effects data in an attempt to bridge existing data gaps. ECOTOX is a source f or locating single chemical toxicity data and potential chemical mixture toxicity data for aquatic life, terrestrial plants, and wildlife. ECOTOX was created and is maintained by the USEPA, Office of Research and Development, and the National Health and E nvironmental Effects Research Laboratory's Mid

Continent Ecology Division.

Also as discussed previously, information on the potential effects of hydramethylnon on non

target animals will be collected from the Ecological Incident Information System (EIIS), aggregate incident reports, and the Avian Incident Monitoring System (AIMS).

Where available, sub

- lethal effects observed in both registrant

- submitted and open literature studies will be evaluated qualitatively. Such effects may include behavioral cha nges (e.g. lethargy and changes in coloration). Quantitative assessments of risks are limited to those endpoints that can be directly linked to the Agency’s assessment endpoints of impaired survival, growth, and reproduction.

The as sessment of risk for direct effects to non

- target organisms makes the assumption that toxicity of hydramethylnon to birds is similar to terrestrial

- phase amphibians and reptiles. The same assumption is made for fish and aquatic

- phase amphibians.

The acu te measures of effect used for animals in this assessment are the LD 50 

### , LC 50, 

### and EC 50


### . LD stands for "Lethal Dose", and LD 50 

### is the amount of a material, given all at once, that is estimated to cause the death of 50% of the test organisms. LC stands for “Lethal Concentration” and LC 50 

### is the concentration of a chemical that is estimated to kill 50% of the test organisms. EC stands for “Effective Concentration” and the EC 50 

### is the concentration of a chemical that is estimated to produce a specific effect in 50% of the test organisms. Endpoints for chronic

### 23 measures of exposure for listed and non

- listed animals are the NOAEL/NOAEC and NOEC. NOAEL stands for “No Observed

- Adverse

- Effect

- Level” and refers to the highest tested dose of a substance that has be en reported to have no harmful (adverse) effects on test organisms. The NOAEC (i.e., “No

- Observed

- Adverse

- Effect

- Concentration”) is the highest test concentration at which none of the observed effects were statistically different from the control. The NO EC is the No

- Observed

- Effects

- Concentration. Only acute exposures are assessed for plants. Non listed plants are assessed using the EC 25 

### (terrestrial plants) or EC 50 

### (aquatic plants) and listed plants (terrestrial and aquatic) are assessed using either t he NOAEC or EC 05


### . 7.4. Integration of Exposure and Effects

Risk characterization is the integration of exposure and ecological effect characterizations to determine the potential ecological risk from the use of hydramethylnon and the likelihood of direct and indirect effects to non

- target organisms in aquatic and terrestrial habitats. The exposure and effects data are integrated in order to evaluate potential adverse ecological effects

on non

- target species.

Typically the risk quotient (RQ) method is us ed to compare exposure and measured toxicity values. EECs are divided by acute and chronic toxicity values. The resulting RQs are then compared to the Agency’s Levels of Concern (LOC) (USEPA, 2004). These criteria are typically used to indicate when a c hemical’s use, as directed on the labels, has the potential to cause adverse direct or indirect effects to non

- target organisms. In addition, incident data from EIIS, aggregate incident reports, and AIMS will be considered as part of the risk

c haracteriza tion.

7.5. Endangered Species Assessments

Consistent with the Agency’s responsibility under the Endangered Species Act (ESA), the Agency will evaluate risks to Federally

- listed threatened and endangered (listed) species from registered uses of hydramet hylnon. This assessment will be conducted i n accordance with the Overview Document (USEPA, 2004), provisions of the ESA, and the Services’ Endangered Species Consultation Handbook (USFWS and NMFS, 1998).

The assessment of effects associated with the regi stration of hydramethylnon is based on an action area. The action area is used to identify all listed (threatened and endangered) species and designated critical habitat that could be affected by the Federal action. The Federal action is the authorizatio n or registration of pesticide use or uses as described on the label(s) of pesticide products containing a particular active ingredient. The action area is defined by the Endangered Species Act as, “all areas to be affected directly or indirectly by the F ederal action and not merely the immediate area involved in the action” (50 CFR §402.2). Based on an analysis of the Federal action, the action area is defined by the actual and potential use of the pesticide.

In the case of nationwide ecological ris k assessment conducted for hydramethylnon under Registration Review, the action area will encompass the entire U.S. and its territories. The purpose of defining the action area as the entire U.S. and its territories is to ensure that the initial area of c onsideration encompasses all areas where hydramethylnon may be used now and in the future that are subject to the ESA, including the potential for off

- site transport via spray drift

### 24 (unlikely given formulations used) and downstream dilution. Additionally, the concept of a nationwide action area takes into account the potential for direct and indirect effects and any potential modification to critical habitat based on ecological effect measures associated with reduction in survival, growth, and reproduction , as well as the full suite of sublethal effects available in the effects literature. It is important to note that the nationwide action area does not imply that direct and/or indirect effects and critical habitat modification are expected to or are likel y to occur over the full extent of the action area, but rather to identify all listed species and critical habitat that may potentially be affected by the action. The Agency will use more rigorous analysis including consideration of available land cover d ata, toxicity data, and exposure information to determine areas where individual listed species and designated critical habitat may be affected or modified via endpoints associated with reduced survival, growth, or reproduction.

7.6. Endocrine Disruptor Screening

As required by FIFRA and the Federal Food, Drug and Cosmetic Act (FFDCA), EPA reviews numerous studies to assess potential adverse outcomes from exposure to chemicals. Collectively, these studies include acute, subchronic and chronic toxicity, including assessments of carcinogenicity, neurotoxicity, developmental, reproductive, and general or systemic toxicity. These studies include endpoints which may be susceptible to endocrine influence, including effects on endocrine target organ histopatho logy, organ weights, estrus cyclicity, sexual maturation, fertility, pregnancy rates, reproductive loss, and sex ratios in offspring. For ecological hazard assessments, EPA evaluates acute tests and chronic studies that assess growth, developmental and re productive effects in different taxonomic groups. As part of registration review, EPA reviewed these data and selected the most sensitive endpoints for relevant risk assessment scenarios from the existing hazard database. However, as required by FFDCA

se ction 408(p), hydramethylnon is subject to the endocrine screening part of the Endocrine Disruptor Screening Program (EDSP).

EPA has developed the EDSP to determine whether certain substances (including pesticide active and other ingredients) may have an effect in humans or wildlife similar to an effect produced by a “naturally occurring estrogen, or other such endocrine effects as the Administrator may designate.” The EDSP employs a two

- tiered approach to making the statutorily required determinations. Tier 1 consists of a battery of 11 screening assays to identify the potential of a chemical substance to interact with the estrogen, androgen, or thyroid (E, A, or T) hormonal systems. Chemicals that go through Tier 1 screening and are found to have the potential to interact with E, A, or T hormonal systems will proceed to the next stage of the EDSP where EPA will determine which, if any, of the Tier 2 tests are necessary based on the available data. Tier 2 testing is designed to identify any adverse endo crine

- related effects caused by the substance, and establish a dose

- response relationship between the dose and the E, A, or T effect.

Under FFDCA section 408(p), the Agency must screen all pesticide chemicals. Between October 2009 and February 2010, EPA issued test orders and data call

- ins for the first group of 67 chemicals, which contains 58 pesticide active ingredients and 9 inert ingredients. EPA published the second list of chemicals for Tier 1 Screening on November 17, 2010

. Hydramethylnon is not among the group of pesticide active ingredients on the first or second

### 25 lists to be screened under the EDSP. According ly, as part of registration review, EPA will issue future EDSP orders and data call

- ins, requiring the submission of EDSP screening assays for hydramethylnon

. For further information on the status of the EDSP, the policies and procedures, the list of chem icals, future lists, the test guidelines and the Tier 1 screening battery, please visit our website: http://www.epa.gov/endo/

. 7.7. Drinking Water Assessment

A Drinking Water Assessment (DWA) from the surface water source will be conducted based on the updated application rates and the latest input parameter guidelines since the previous DWA (USEPA 2003 ) . Concentrations of the residue in surface waters will be estimated using a Tier II PRZM/EXAMS model ( http://www.epa.gov/oppefed1/models/water/index.htm ). DWA from the ground water source will not be conducted

. The reason is that h ydramethylnon appears to have a low potential for groundwater contamin ation d ue to the lack of movement of hydramethylnon in the soil profile under most conditions.

7. 8 . Preliminary Identification of Data Gaps

Available studies submitted to fulfill environmental fate and ecological effects guideline requirements, as well as outstanding data gaps for hydramethylnon, are defined in Sections 7. 8 .1 and 7. 8 .2 , respectively. Studies are i dentified that offer data for each guideline requirement, as well as study classifications and whether or not further data are needed in order to support risk
assessment.

7. 8 .1. Environmental Fate Data

Table 10 lists submitted fate studies with MRID, data classification and existing data gaps for parent hydramethylnon. In summary of the hydramethylnon environmental fate data, it appears that the photolysis is potentially a major degradation pathway. However, one of the uncertaint ies is the several unknown degradates formed through the photolysis pathway. In aquatic photolysis, f our unidentified compounds were discernible in the pyrimidine r adiolabeled and the phenyl radiolabeled samples, ranging from 29.6% to 7.6% of recovered radioactivity ( MRIDs 42238201 and 42473301)

. Hydramethylnon soil photolysis is biphasic, with half

- lives of 4 days for the first phase and in about 30 days for the se cond phase with two unidentified degradates making up 10% of the applied radioactivity (MRIDs 42113401 and 42 3 53 801 ). In addition, two major degradates (15% and 12.7%) were not identified in anaerobic aquatic metabolism study (MRID 43102701). Proper iden tification of th e above unknowns is very critical to help to characterize the hydramethylnon environmental fate. In absence of these data, a conservative approach will be used to assume the unknown degradates are the parent hydramethylnon

. Finally, the a erobic aquatic metabolism (835.4300) study is not submitted and without the data, a conservative stable half

- life will be assum ed

.

### 26 Table 10. Environmental Fate Data Gaps for Hydramethylnon

Guideline Description MRID Classification Data Gap Comments
835. 2120 Hydrolysis 42194701 Acceptable No 1 Four degredates were not identified. In absence of the data, the unknowns will be treated as the parent.

2 Waived

3 Data are required under on 40CFR Part 158 . In absence of the data, a conservative stable assumpt ion will be used.

4 Two major degradates (15% and 12.7%) were not identified. In absence of the data, the unknowns will be treated as the parent.

5 Study conducted in Florida

6 Study conducted in Texas

7 Detection of the residue in soil 835.2240 Photod egradation in Water 42238201 42473301 Supplemental Yes 1

835.2410 Soil Photolysis 42353801 Acceptable No

835.2370 Photodegradation in Air None N/A No 2

835.4100 Aerobic Soil Metabolism 42320801 Supplemental No

835.4200 Anaerobic Soil Metabolism 000 61709 Supplemental No

835.4300 Aerobic Aquatic Metabolism None N/A Yes 3

835.4400 Anaerobic Aquatic Metabolism 43102701 Supplemental Yes 4

835.1230 835.1240 Leaching Adsorption/Desorption 41888302 Acceptable No

835.1410 Laboratory Volatility None N /A No 2

835.8100 Field Volatility None N/A No 2

835.6100 Terrestrial Field Dissipation 43293101 5 Supplemental No

43293102 6 Supplemental No Hydramethylnon ECM 43345201 7 N/A No

850.1730 Accumulation in Fish 00101611 Acceptable No



### Aerobic Aquatic Metabolism

Guideline 835.4300, aerobic aquatic metabolism data are not available for hydramethylnon; these are required under the 40 CFR Part 158 data requirements for outdoor terrestrial uses of conventional pesticides

Aquatic photolysis and An aerobic Aquatic Metabolism

Both aquatic photolysis ( 835.2240) and soil photolysis ( 835. 440 0 ) studies are classified as supplemental because of several major degradates (>10%) were not identified and the data requirement were not satisfied for environmenta l fate characterization.

### 27 7. 8 .2. Ecological Effect Data

Several data gaps for hydramethylnon ecological effects remain across all taxonomic groups ( Tables 12, 13, and 14 ).

TABLE 12. Ecological Effect Data Gaps for Terrestrial Animals Exposed to Hydr amethylno n
Guideline Description MRID Classification Data Gap? Comments

850.2100 Avian acute oral toxicity (upland game or waterfowl species) 32038 or 63576

and 64575 Acceptable (“Core”) No 1 Avian acute oral toxicity data are not available for passerines, which are now required under the most recent 40 CFR Part 158. Avian acute oral toxicity (passerine species) N/A Not applicable Yes 1

850.2200 Avian dietary toxicity (upland game species) 32040 or 64577 Acceptable No

Avian dietary toxicity

(wate rfowl species) 32039 or 85931 Acceptable No

850.2300 Avian reproduction (upland game species) 45449701 Supplemental No

Avian reproduction (waterfowl species) 45449702 Acceptable (“Core”) No

850.3020 Honeybee acute contact toxicity 41607801 Accep table No

### 28 TABLE 13. Ecological Effect Data Gaps for Aquatic Animals Exposed to Hydramethylnon

Guideline Description MRID Classification Data Gap? Comments

850.1075 Acute freshwater fish toxicity 52858 Acceptable No 1 These data are required under 40 CFR part 158 for terrestrial outdoor uses.

2 These data are required under 40 CFR part 158 based on potential exposure and acute marine/estuarine fish and invertebrate RQs. EFED has previously requested these studies and they were made a condition of regi stration for the product Instinct (EPA Reg. Number 62719

- 583). Acute freshwater fish toxicity 35279 Acceptable No

Acute estuarine/ marine fish toxicity 52857 Acceptable No

Acute estuarine/ marine fish toxicity with flow

- through 46684803 Suppl emental No

850.1010 Acute toxicity to freshwater invertebrates 35877 Acceptable No

850.1025 Acute estuarine/ marine mollusk toxicity 46684801 Invalid Yes 2

850.1035 Acute estuarine/ marine invertebrate toxicity 46684802 Acceptable No

850.1300 F reshwater invertebrate life cycle 101610 Supplemental Yes 2

850.1350 Saltwater invertebrate life cycle Not applicable Not applicable Yes 2

850.1400 Freshwater fish early life stage Not applicable Not applicable Yes 1

Saltwater fish early life stage Not applicable Not applicable Yes 2

850.1735 Whole sediment acute fresh water invertebrates 46684804 Acceptable No

850.1740 Whole sediment acute marine water invertebrates 46684805 Acceptable No

### 29 TABLE 14. Ecological Effect Data Gaps for Plan ts Exposed to Hydramethylnon

Guideline Description Classification Data Gap? Comments

850.4100 Terrestrial plant toxicity (Tier I&II seedling emergence) Not submitted Yes 1 1 These data are required under 40 CFR part 158 and are not available.
2 A Tier I study is triggered. A Tier II study may be conducted in lieu of a Tier I if it is suspected that an adverse effect will be detected at the limit dose. If a Tier I study is conducted and any adverse effects are observed this would necessitate conduct a nd submission of a Tier II study as well. 850.4150 Terrestrial plant toxicity (Tier I&II vegetative vigor) Not submitted Yes 1 , 2

850.5400 Aquatic plant growth (freshwater green alga) Not submitted Yes 1 , 2

Aquatic plant growth (freshwater diatom) Not submitted Yes 1

, 2

Aquatic plant growth

(saltwater diatom) Not submitted Yes 1

, 2

Aquatic plant growth (Cyanobacteria) Not submitted Yes 1

, 2

850.4400 Aquatic plant growth (vascular plants) Not submitted Yes 1

, 2



### Avian Acute Oral and Dietary Toxici ty

Acute avian oral toxicity data are not available for a passerine species. Avian acute oral toxicity data on passerines are now required under the current 40 CFR Part 158. Avian acute oral toxicity data will be used to determine the lethal dose of hydra methylnon to birds on a body weight basis. Passerine species may be more or less sensitive to hydramethylnon because they have higher metabolic rates than the tested species (mallard duck, Beltsville small white turkey poults, and white leghorn cockerel c hicks) due to their smaller sizes and because they may utilize different metabolic pathways. EFED will assume risk to birds on an acute oral basis in the absence of these data

### 30 Estuarine/Marine Mollusc Acute Toxicity

D ata are invalid for an acute mollusc endpoint. These data are important for in that they provide close taxonomic surrogacy for a variety of Federally listed mollusks. There are no toxicity surrogates for hydramethylnon and this acute is required under 40 CFR Part 158 for pesticides expected to enter estuarine/marine systems. Hydramethylnon is expected to reach these systems.

Freshwater Fish and Marine/Estuarine Fish Chronic Toxicity (Early

- Life Stage)

A study is not available on chronic toxicity to freshwater fish or marine/estuarine fish (early

- life stage). Under the 40 CFR Part 158 data requirements for conventional pesticides, this data is conditionally required (OCSPP Guideline 850.1400) for outdoor terrestrial uses.

Because chronic data are lacking for both fish types it is not po ssible to assign an acute to chronic ratio from one acute/chronic paired data set to the other fish type. Consequently, at the minimum either a freshwater fish or an estuarine/marine fish (of a species presently tested in acute testing protocols) should b e performed and the resulting ACR applied to other fish. Optimally, both a freshwater and estuarine species (of species presently tested in acute testing protocols) should b e test ed using early life stage testing protocols.

Freshwater and Marine/Estuarin e Invertebrate Chronic Toxicity (Life Cycle)

Acceptable s tudies are not available on chronic toxicity to freshwater and marine/estuarine invertebrates. Data are required for both invertebrates under the 40 CFR Part 158 data requirements for outdoor terr estrial uses of conventional pesticides. Potential exposure to hydramethylnon is expected for both freshwater and estuarine/marine environments, and EFED has previously requested the marine/estuarine study in earlier risk assessments.

Terrestrial Plant Toxicity

Guideline terrestrial plant data are not available for hydramethylnon ; these are required because of hydramethylnon’s outdoor uses

. Aquatic Plant Toxicity

Aquatic plant toxicity studies are required for pesticides with outdoor terrestrial us es (four non

vascular plant studies and one vascular plant study. No data are available on unicellular or vascular species. Exposure to hydramethylnon is possible and the different species are likely to show a range of sensitivity to hydramethylnon. A Ti er I plant study may be conducted in lieu of a Tier II study with the understanding that any adverse effects observed by the Tier I study would necessitate conduct and submission of a Tier II study as well.

### 31 8. References

USEPA. 1998. Reregistration Eligibility Decision (RED) Hydramethylnon. 143 pp

USEPA. 2003. Section 3 New Crop Use Registration of Hydramethylnon on Pineapples in Hawaii for Control of Bigheaded Ants (PC Code Number: 118401, DP Barcode: D249596) 45 pp.

USEPA. 2004. Overview of the Ecological Risk Assessment Process in the Office of Pesticide Programs. U.S. Environmental Protection Agency, Office of Prevention, Pesticides and Toxic Substances, Office of Pesticide Programs, Washington DC. January 23, 2004.

USEPA. 2012a. 118 401 Hydramethylnon Full LUIS Label Tracking, BEAD 7/18/2012

USEPA. 2012 b . 118401 Hydramethylnon EFE D label data report, BEAD 7/18/2012

### 32 APPENDIX A. Submitted Environmental Fate and Effects Studies

SUBMITTED ENVIRONMENTAL FATE STUDIES

161

- 1 Hydrolysis

MRID Citation

31307 Reichert, B.L.; Stout, S.J.; Pasarela, J. (1980) Amdro Fire Ant In

- secticide CL 217,300: The Hydrolysis of Carbon

- 14 Labeled CL 217,300: Project No. 0420. (Unpublished study received Apr 24, 1980 under 241

- EX

- 93; sub mitted by American Cyanamid Co., Princeton, N.J.; CDL:242308

- G)

62328 Kapoor, I.P. (1979) Letter sent to T. Wang dated Feb 27, 1979: The hydrolysis of carbon

- 14 labeled CL 217,300 in an aqueous system. (Unpublished study received Mar 21, 1979 under 241

- E X

- 93; submitted by American Cyanamid Co., Princeton, N.J.; CDL: 237848

- N)

98491 ACC 247235 Barringer, D.F.; Stanley

- Millner, P. (1982) Amdro^(TM)I Fire Ant Insecticide (CL 217,300): The Hydrolysis of Carbon

- 14 CL 217,300. (II) Studies at Concentrations in the ppb Range without Cosolvent: Report No. C

- 2005. (Unpublished study received Apr 9, 1982 under 241

- 260; submitted by American Cyanamid Co., Princeton, N.J.; CDL:247235

- A)

42194701 Beckman, K.; Cranor, W. (1992) Hydrolysis of Hydramethylnon as a Fun ction of pH at 25 C: Lab Project Number: 38960. Unpubli

- shed study prepared by ABC Labs., Inc. 67 p.



### 161

- 2 Photodegradation

- water

MRID Citation

42238201 Cranor, W.; Beckman, K. (1992) Determination of the Aqueous Photolysis Rate of Hydramethylno n (Interim Report): Lab Project Number: 38961. Unpublished study prepared by ABC Labs, Inc. 51 p.

42473301 Cranor, W. (1992) Determination of the Aqueous Photolysis Rate of Hydramethylnon: ?Final Report|: Lab Project Number: 38961. Unpublished study
prep ared by ABC Labs, Inc. 79 p.

70924 Lee, A.; Mallipudi, M.; Stanley, P.A.; et al. (1980) Amdro^(TM)I Fire Ant Insecticide (CL 217,300): Photolysis in Distilled Wa

- ter: Project No. 0420. Final rept. (Unpublished study received Mar 16, 1981 under 241

- 260; submitted by American Cyanamid Co., Princeton, N.J.; CDL:244585

- A)



### 161

- 3 Photodegradation

- soil

MRID Citation

61703 Kapoor, I.P. (1979) Letter sent to T. Wang dated Sep 13, 1979: The Photolisis of

### 33 Carbon

- 14 Labelled CL217,300. (Unpublished study r eceived Jul 1, 1980 under 241

- 260; submitted by American Cyan

- amid Co., Princeton, N.J.; CDL:099777

- B)

ACC 098985 CL 217,300: The Photolysis of CL 217,300 Bait Formulation on Several Carriers. A. Markantonates. Acc. #095985,

71014 Barringer, D.F., Jr.; Stanley, P.A. (1981) Amdro^(TM)I Fire Ant In

- secticide (CL 217,300): Photolysis on Soil Thin

- layer Plates (Benzylic Carbon

- 14 Labeled): PDM 18

- 1:1

- 23. Final rept. (Un

- published study received Mar 18, 1981 under 241

- 260; submitted by American Cyanamid Co ., Princeton, N.J.; CDL:244605

- A)

101609 Barringer, D. (1981) Amdro Fire Ant Insecticide (CL 217,300): Photolysis on Soil Thin

- layer Plates (Pyrimidine Carbon

- 14 Labeled): Report No. PD

- M 18

- 22:1

- 18. (Unpublished study re

- ceived May 14, 1982 under 241

- 2 60; submitted by American Cyanamid Co., Princeton, NJ; CDL:247502

- B)

42113401 Melcer, M. (1991) Hydramethylnon (...): Photodegradation on Soil: Interim Report: Lab Project Number: E

- 91

- 9. Unpublished study prepared by American Cyanamid Co. 47 p.

423538 01 Melcer, M. (1992) Hydramethylnon (AC 217,300): Photodegradation on Soil: Lab Project Number: E

- 91

- 9. Unpublished study prepared by American Cyanamid Comp. 192 p



### 162

- 1 Aerobic soil metabolism

MRID Citation

42320801 Gorman, M. (1992) Aerobic Soi l Metabolism of Hydramethylnon: Lab Project Number: 38977. Unpublished study prepared by ABC Laboratories, Inc. 86 p.

35282 Reichert, B.L.; Gatterdam, P.E.; Miller, K.; et al. (1980) Amdro Fire Ant Insecticide (CL 217,300): Metabolism in Soil under Aer

- obic Conditions: Project No. 0420. Final rept. (Unpublished study received Jul 1, 1980 under 241

- 260; submitted by American Cyanamid Co., Princeton, N.J.; CDL:099488

-

125752 Reichert, B.; Gatterdam, P.; Miller, K.; et al. (1980) Amdro Fire Ant Insecticide (CL 217,300): Metabolism in Soil under Aerobic Conditions: PD

- M Volume 17

- 5. Final rept. (Unpublished study received Feb 18, 1983 under 241

- 260; submitted by American Cyanamid Co., Princeton, NJ; CDL:071409

- J)

ACC 098985 Preliminary Aerobic Soil Metabol ism of CL 217,300. I .P. Kapoor, Acc. #098985, Section D2, Exhibit 6.
Al'rlDRO Fire Ant I n s e c t i c i d e (CL 217,300): . Metabolism of Surface Applied Compound under Field Conditions, P. Gatterdam, Report No. C

- 1743. American Cyanamid Company, Produ ct Development, Princeton, N. J., Accession No. 241

- 260, 241

- 261.

### 34 162

- 1 Anaerobic Soil Metabolism

MRID Citation

35878 Reichert, B.L.; Knoll, B. (1979) CL 217,300: Anaerobic Soil Metabolism: Project No. 0420. (Unpublished study received Jul 1, 1980 und er 241

- 260; submitted by American Cyanamid Co., Princeton, N.J.; CDL:099488

- E)

61709 Reichert, B.L.; Knoll, B.A. (1979) CL 217,300: Anaerobic Soil Me

- tabolism: PD

- M 16

- 26. Progress rept. from 1/29/79 to 5/31/79. (Unpublished study received Jul 1, 1980 u nder 241

- 260; submitted by American Cyanamid Co., Princeton, N.J.; CDL:099778

- E)

61710 Gatterdam, P.; Miller, K. (1980) Amdro Fire Ant Insecticide (CL 217,300): Metabolism of Surface Applied Compound under Field Conditions: Report No. C

1743. (Unpublis hed study received Jul 1, 1980 under 241

- 260; submitted by American Cyanamid Co., Princeton, N.J., CDL:099778

- F)



### 162

- 3 Anaerobic aquatic metab.

MRID Citation

43102701 Cady, C. (1994) Anaerobic Aquatic Metabolism of Hydramethylnon: Final Report: L ab Project Number: ENV/94/002: 38978. Unpublished study prepared by ABC Lab., Inc. 68 p.



### 163

- 1 Leach/adsorp/desorption

MRID Citation

32045 Reichert, B.L.; Knoll, B.A. (1979) CL 217,300: Determination of Mobility in Soil: Project No. 0420. (Unpubl ished study received Jun 11, 1980 under 241

- 260; submitted by American Cyanamid Co., Princeton, N.J.; CDL:099457

- C)

62329 Kapoor, I.P. (1979) Letter sent to T. Wang dated Feb 28, 1979: Mobility of CL 217,300. (Unpublished study received Mar 21, 1979 unde r 241

- EX

- 93; submitted by American Cyanamid Co., Princeton, N.J.; CDL:237848

- O)

41888302 Mangels, G. (1990) Hydramethylnon (AC217,300): Adsorption/Desorpti

- on: Lab Project Number: E

- 90

- 21. Unpublished study prepared by American Cyanamid Co. 35 p.



### 164

- 1 Terrestrial field dissipation

MRID Citation

35283 Gatterdam, P.E.; Miller, K. (1980) Amdro Fire Ant Insecticide (CL 217,300): Metabolism of Surface Applied Compound under Field Conditions: Report No. C

1743. (Unpublished study received Jul 1, 198 0 under 241

- 260; submitted by

### 35 American Cyanamid Co., Princeton, N.J.; CDL:099488

- F)

61803 Manuel, A.J.; Wang, T.; Muzyk, K.R.; et al. (1980) Amdro(TM)I Fire Ant Insecticide (CL 217,300): Residues of CL 217,300 in Soil (Grass; GND; FL, 1979) (C

- 1646): Rep ort No. C

- 1706. (Compilation; unpublished study received Jul 1, 1980 under 241

- 260; submitted by American Cyanamid Co., Princeton, N.J.; CDL: 099775

- H)

43293101 Wrong PC on DER York, C. (1994) CL 217,300 (hydramethylnon/G): Rate of Dissipation of CL 217, 300 Residues in Soil after Treatment with AMDRO Fire Ant Insecticide (FL; 1992): Lab Project Number: RES/94/051. Unpublished study prepared by American Cyanamid Co., Huntingdon Analytical Services. 120 p.

43293102 Wrong PC on DER York, C. (1994) CL 217,3 00 (hydramethylnon/G): Rate of Dissipation of CL 217,300 Residues in Soil after Treatment with AMDRO Fire Ant Insecticide (TX; 1992): Lab Project Number: RES/94/065. Unpublished study prepared by American Cyanamid Co., Huntingdon Analytical Services. 119 p

. 43636701 Fletcher, J. (1995) CL 217,300: Freezer Stability of Residues of CL 217,300 in Soil: Lab Project Number: RES 94

- 070: AM92PT03: A011.071. Unpublished study prepared by American Cyanamid Co. and Huntingdon Analytical Services. 40 p.



### 165

- 0 Accumulation Studies

-- General

MRID Citation

31304 or 61705 Caballa, S.H.; Knoll, B. (1979) CL 217,300: Biodegradability, Environmental Fate and Ecological Magnification of Carbon

- 14 Labeled CL 217,300 in a Model Ecosystem: Project No. 0420. (Unpublis hed study received Apr 24, 1980 under 241

- EX

- 93; submitted by American Cyanamid Co., Princeton, N.J.; CDL:242308

- C)

61705 Caballa, S.H.; Knoll, B. (1979) CL 217,300: Biodegradability, Envi

- ronmental Fate and Ecological Magnification of Carbon

- 14 La

- bel ed CL 217,300 in a Model Ecosystem: PD

- M 16

- 11. Final rept. (Unpublished study received Jul 1, 1980 under 241

- 260; submitted by American Cyanamid Co., Princeton, N.J.; CDL:099777

- H)

62331 Kapoor, I.P. (1979) Letter sent to T. Wang dated Feb 23, 1979: Com parative biodegradability, environmental fate and ecological magnification of carbon

- 14 Mirex and carbon

- 14 CL 217,300 in a model ecosystem. (Unpublished study received Mar 21, 1979 under 241

- EX

- 93; submitted by American Cyanamid Co., Princeton, N.J.; CDL: 237848

- Q)

164252 American Cyanamid Co. (1979) Residues of AC 217, 300: [in or on Grass and Fate in the Environment]. Unpublished compilation. 349 p.



### 165

- 1 Confined rotational crop

MRID Citation

92163029 Lee, A. (1990) American Cyanamid Company Phase 3 Summary of MRID 00061706. AMDRO Fire Ant Insecticide (CL 217300): Uptake and Residues of Radioactivity in Follow

- Crops Grown in Soil Containing Aged Residues of Carbon

-

### 36 14 Labeled CL 217,300: Report No. PD

- M Volume 17

- 3. Prepared by AMERICAN CYANAMI D CO. 35 p.

61706 Gatterdam, P. E. 1979. AMDRO fire ant insectidide (CL 217300): Uptake and Residues of Radioactivity in Fallow

- Crops Grown in Soil Containing Aged Residues of carbon

- l4 Labeled CL 217,300. performed and submitted by American Cyanamid Com pany Princeton, NJ.

ACC 098985 Gatterdam, , P.E. CL 217,300: Residues of CL 217,300 i n Range Grass Grown i nSoil Treated w i t h Carbon

- 14 labeled compound a t Gainesville, Florida. Acc 8098985, Section 02, Exhibit 9.



### 165

- 4 Bioaccumulation in fis h

MRID Citation

92163030 Lee, A. (1990) American Cyanamid Company Phase 3 Summary of MRID 00101611. AMDRO Fire Ant Insecticide (CL 217,300): Identification and Characterization of CL 217,300 and Its Metabolite in Bluegill Sunfish Exposed to 1.8 ppb of CL 217,300 in Water. Prepared by AMERICAN CYANAMID CO. 21 p.

31305 Kuc, W.J. (1980) 14C

- AC217,300: Channel Catfish, Ictalurus punctatus (Rafinesque): Bioconcentration Study: UCES Project No. 11507

- 51. (Unpublished study received Apr 24, 1980 under 241

- EX

- 9 3; prepared by Union Carbide Corp., submitted by American Cyanamid Co., Princeton, N.J.; CDL:242308

- D)

31306 Kuc, W.J. (1980) 14C

- AC 217,300: Bluegill Sunfish, Lepomis macro

- chirus Rafinesque: Bioconcentration Study: UCES Project No. 11507

- 54. (Unpublis hed study received Apr 24, 1980 under 241

- EX

- 93; prepared by Union Carbide Corp., submitted by Ameri

- can Cyanamid Co., Princeton, N.J.; CDL:242308

- E)

35280 Reichert, B.L.; Knoll, B.; Koc, W.J.; et al. (1980) Amdro Fire Ant Insecticide (CL 217,300): Iden tification and Characterization of CL 217, 300 and Its Metabolites in Bluegill Sunfish: Project No. 0420. Final rept. (Unpublished study including UCES Proj

- ect No. 11507

- 54, received Jul 1, 1980 under 241

- 260; prepared in cooperation with Union Carbide C orp., submitted by American Cyanamid Co., Princeton, N.J.; CDL:099488

- A)

61707 Vilkas, A.G.; Kuc, W.J. (1980) American Cyanamid Company ^14IC

- AC217,300: Channel Catfish,~Ictalurus punctatus~(Rafinesque) Bioconcentration Study: UCES Project No. 11507

- 51. (Unpublished study received Jul 1, 1980 under 241

- 260; prepared by Union Car

- bide Corp., submitted by American Cyanamid Co., Princeton, N.J.; CDL:099777

- J)

61708 Reichert, B.; Knoll, B. (1980) Amdro Fire Ant Insecticide (CL 217,300): Identification and Characterization of CL 217,300 and Its Metabolites in Bluegill Sunfish: PD

- M 17

- 14. Final rept. (Unpublished study received Jul 1, 1980 under 241

- 260; submitted by American Cyanamid Co., Princeton, N.J.; CDL:099778

- C)

101611 Barringer, D.; Stanley

- Milln er, P. (1982) Amdro Fire Ant Insecti

- cide (CL 217,300): Identification and Characterization of CL 217,300 and Its Metabolite in Bluegill Sunfish Exposed to 1.8 ppb of CL 217,300 in Water: Report No. PD

- M 19

- 6:1

- 185. (Unpub

- lished study received May 14, 1 982 under 241

- 260; submitted by

### 37 American Cyanamid Co., Princeton, NJ; CDL:247502

- D)



### Non Guideline Selections
MRID Citation

34022 Tondreau, R.E.; Manuel, A.J. (1980) CL 217,300: Validation of GC Method M

- 1045 for the Determination of CL 217,300 Residue s in Soil: Report No. C

- 1646. Includes method dated Jan 3, 1980. (Unpublished study received Jun 11, 1980 under 241

- 260; submit

- ted by American Cyanamid Co., Princeton, N.J.; CDL:099454

- C)

34023 Manuel, A.J.; Wang, T.; Williams, D.; et al. (1980) Amdro Fire Ant Insecticide (CL 217,300): Residues of CL 217,300 in Soil (Grass; GND; FL, 1979) (C

- 1646): Report No. C

- 1706. (Unpublished study received Jun 11, 1980 under 241

- 260; prepared in cooperation with U.S. Dept. of Agriculture, Science and Education Admi nis

- tration, submitted by American Cyanamid Co., Princeton, N.J.; CDL:099454

- D)

34028 American Cyanamid Company (19??) Stability Information. (Unpub

- lished study received Jun 11, 1980 under 241

- 260; CDL:099450

- C)

34029 Lopata, R.J. (1980) CL 217,300: High Pressure Liquid Chromatograph

- ic Assay of Tetra

- hydro

- 5,5

- dimethyl

- 2(?~H~?)

- pyrimidinone, ?3

- ?4

- (Trifluoromethyl)

- phenyl|

- 1

- |2

- ?4

- trifluoromethyl)phenyl| ethenyl3

- 2

- propenylidene|

- hydrazone. Methods M

935 dated Nov 22, 1978 and M

- 1068.1 dated Apr 21 , 1980. (Unpublished study received Jun 11, 1980 under 241

- 260; submitted by American Cyanamid Co., Princeton, N.J.; CDL:099450

- D)

34030 Markantonatos, A. (1979) CL 217,300: HPLC Determination of CL 217,300 Content in Oil Formulations and Defatted Pregel Corn Bait Formulations. Method M

- 1040.1 dated Nov 20, 1979. (Unpub

- lished study received Jun 11, 1980 under 241

- 260; submitted by American Cyanamid Co., Princeton, N.J.; CDL:099450

- E)

61802 Tondreau, R.E. (1980) Recommended Method of Analysis: CL 217,3 00: GC Method for the Determination of CL 217,300 Residues in Soil. Method M

- 1045 dated Jan 3, 1980. (Unpublished study received Jul 1, 1980 under 241

- 260; submitted by American Cyanamid Co., Princeton, N.J.; CDL:099775

- G)

63869 Metz, W.A.; Conley, J.M. (1980) Hydrazine: High

- Pressure Liquid Chromatographic Method of Analysis for Residual Hydrazine in CL 217,300. Method M

- 1087 dated Jun 24, 1980. (Unpublished study received Jul 1, 1980 under 241

- 260; submitted by American Cyana

- mid Co., Princeton, N.J.; CDL:099768

- B)

71016 Atlas, R.M. (1980) Effects of the Insecticide AC 217,300 on Soil Microorganisms. (Unpublished study received Mar 18, 1981 under 241

- 260; prepared by Univ. of Louisville, Dept. of Biology, sub

- mitted by American Cyanamid Co., Princeto n, N.J.; CDL:244603

- A)

71024 Lopata, R.J. (1978) CL 217,300: High Pressure Liquid Chromatograph

- ic Assay of Tetrahydro

- 5,5

- dimethyl

- 2(1~H~)

- pyrimidinone, ?3

- ?4

- (trifluoromethyl)

- phenyl|

- 1

- ?2

- ?4

- (trifluoromethyl)phenyl| ethenyl|

- 2

- propenylidene|

- hydrazo ne. Method M

- 935 dated Nov 22, 1978. (Unpublished study received Mar 16, 1981 under 241

- EX

- 97; submitted by American Cyanamid Co., Princeton, N.J.; CDL: 244587

- B)

71025 DeLuccia, S. (1981) Proposed Analytical Method for Determination of AC 217,300

### 38 Formul ations. Undated method. (Unpublished study received Mar 16, 1981 under 241

- EX

- 97; submitted by American Cyanamid Co., Princeton, N.J.; CDL:244587

- C)

79263 Gatterdam, P.E. (1981) Amdro^(TM)I Fire Ant Insecticide (CL 217,300): Recovery of Carbon

- 14 CL 217, 300 from Water Stored in Glass Vessels: Report No. C

- 1875. (Unpublished study re

- ceived Jul 24, 1981 under 241

- 260; submitted by American Cyanam

- id Co., Princeton, N.J.; CDL:245593

- A)

125750 Vander Meer, R.; Williams, D.; Lofgren, C. (1982) Degradation of the toxicant AC 217,300 in Amdro Imported Fire Ant Bait under field conditions. J. Agric. Food Chem. 30(6):1045

- 1048. (Also In unpublished submission received Feb 18, 1983 under 241

- 260; submitted by American Cyanamid Co., Princeton, NJ; CDL:071409

- H)

125751 Gatterdam, P.; Miller, K. (1980) Amdro Fire Ant Insecticide (CL 217,300): Metabolism of Surface Applied Compound under Field Conditions: Report No. C

1743. (Unpublished study received Feb 18, 1983 under 241

- 260; submitted by American Cyanamid Co., Princeton, NJ; CDL:071409

- I)

43345201 Fletcher, J. (1994) AMDRO (CL 217,300): Validation of HPLC Method M 2266 for the Determination of CL 217,300 Residues in Soil: Addendum to Terrestrial Field Dissipation Studies with CL 217,300: Lab Project Number: R ES/93/142. Unpublished study prepared by American Cyanamid Co. 32 p.

ACC 098985 Caballa, S.H. CL 21'7,

- 300: ~determination of Par t i t ion Coefficient i n n

Octanol

Water Solvent System. Acc #098985, section D2,

43345202 Fletcher, J. (1994) CL 217,3 00: Independent Laboratory Validation of HPLC Method M 2266 for the Determination of CL 217,300 Residues in Soil by Huntingdon Analytical Services, Inc.: Addendum to Terrestrial Field Dissipation Studies with CL 217,300: Lab Project Number: RES/94/071: A01 1/066. Unpublished study prepared by American Cyanamid Co. and Huntingdon Analytical Services, Inc. 57 p.

32046 Caballa, S.H. (1979) CL 217,300: The Effect of Soil Microorganisms on Carbon

- 14 Labeled CL 217,300: Project No. 0420. Includes un

- dated metho d. (Unpublished study received Jun 11, 1980 under 241

- 260; submitted by American Cyanamid Co., Princeton, N.J.; CDL:099457

- D)

41888301 Mangels, G. (1990) Hydramethylnon (AC217,300): Soil Thin

- Layer Chromatography: Lab Project Number: E

- 89

- 31. Unpublished study prepared by American Cyanamid Co. 15 p.



### SUBMITTED EFFECTS STUDIES

71

- 1 Avian Single Dose Oral Toxicity

MRID Citation

32038 or 64576 Beavers, J.B.; Fink, R.; Brown, R. (1979) Final Report: Acute Oral LD50

-- Bobwhite Quail: Project No. 130

- 126. (Unpublished study received Jun 11, 1980 under 241

-

### 39 260; prepared by Wildlife Inter

- national, Ltd. in cooperation with Washington College, submit

- ted by American Cyanamid Co., Princeton, N.J.; CDL:099456

- C)

64575 Fink, R.; Beavers, J.B.; Grimes, J. ; et al. (1979) Final Report: Acute Oral LD50

-- Mallard Duck: Project No. 130

- 127. (Unpub

- lished study received Jul 1, 1980 under 241

- 260; prepared by Wildlife International Ltd. and Washington College, submitted by American Cyanamid Co., Princeton, N.J.; CDL:099779

- E)

92163003 Gagne, J. (1990) American Cyanamid Company Phase 3 Summary of MRID 00064575. AC 217,300

- Acute Oral LD50

- Bobwhite Quail: Project No. 130

- 126; June 14, 1979. Prepared by WILDLIFE INTERNATIONAL, LTD. 11 p.

92163004 Gagne, J. (19 90) American Cyanamid Company Phase 3 Summary of MRID 00064576. AC 217,300

- Acute Oral LD50

- Mallard Duck: Project No. 130

- 127; June 14, 1979. Prepared by WILDLIFE INTERNATIONAL, LTD. 12 p.

71

- 2 Avian Dietary Toxicity



### MRID Citation

32039 or 8593 1 Beavers, J.B.; Fink, R.; Grimes, J.; et al. (1979) Final Report: Eight

- Day Dietary LC50

-- Mallard Duck: Project No. 130

- 125. (Un

- published study received Jun 11, 1980 under 241

- 260; prepared by Wildlife International, Ltd. in cooperation with Washington Col

- lege, submitted by American Cyanamid Co., Princeton, N.J.; CDL: 099456

- D)

32040 or 64577 Beavers, J.B.; Fink, R.; Grimes, J.; et al. (1979) Final Report: Eight

- Day Dietary LC50

-- Bobwhite Quail: Project No. 130

- 124. (Unpublished study received Jun 11

, 1980 under 241

- 260; prepared by Wildlife International, Ltd. in cooperation with Washington College, submitted by American Cyanamid Co., Princeton, N.J.; CDL:099456

- E)

92163005 Gagne, J. (1990) American Cyanamid Company Phase 3 Summary of MRID 00064577 . AC 217,300

- Acute Oral LC50

- Bobwhite Quail: Project No. 130

- 124; July 13, 1979. Prepared by WILDLIFE INTERNATIONAL, LTD. 11 p.

92163006 Gagne, J. (1990) American Cyanamid Company Phase 3 Summary of MRID 00085931. AC 217,300

- Acute Oral LC50

- Malla rd Duck: Project No. 130

- 125; July 12, 1979. Prepared by WILDLIFE INTERNATIONAL, LTD. 12 p.

71

- 4 Avian Reproduction



### MRID Citation

45449701 Frey, L.; Martin, K.; Beavers, J. et al. (2001) Avian Reproduction Test with Hydramethylnon (AC 217300) in N orthern Bobwhite (Colinus virginianus): Lab Project Number: ETX

- 00

- 186: 130

- 191. Unpublished study prepared by Wildlife International, Ltd. 286 p. {OPPTS 850.2300}

45449702 Frey, L.; Martin, K.; Beavers, J. et al. (2001) Avian Reproduction Test with Hydr amethylnon (AC 217300) in Mallard (Anas platyrhynchos): Lab Project Number: ETX

- 00

- 187: 130

- 192. Unpublished study prepared by Wildlife

### 40 International, Ltd. 284 p. {OPPTS 850.2300}

72

- 1 Acute Toxicity to Freshwater Fish



### MRID Citation

164246 Union C arbide Corp. (1979) The Acute Toxicity of AC 217,300 to the Channel Catfish: Ictalurus punctatus (Rafinesque): UCES Project No. 11506

- 20

- 20. Unpublished study. 9 p.

164247 Union Carbide Corp. (1979) Acute Toxicity of AC 217,300 to Bluegill Sunfish, Lepom is macrochirus Rafinesque: UCES Project # 11506

- 20

- 19. Unpublished study. 10 p.

32037 Schneider, C.E. (1979) Acute toxicity of AC 217,300 to the Rainbow Trout,~Salmo gairdneri~Richardson: UCES Project # 11506

- 20

- 18. (Unpublished study received Jun 11, 1980 under 241

- 260; prepared by Union Carbide Corp., submitted by American Cyanamid Co., Princeton, N.J.; CDL:099456

- A)

35279 Vilkas, A.G.; Seminara, J. (1980) The Acute Toxicity of AC 217,300 (Lot No. AC 3196

- 99B, 91.6% Active Ingredient) to the Bluegil l Sunfish,~Lepomis macrochirus~Rafinesque: UCCES Project No. 11506

- 20

- 31. (Unpublished study received Jul 1, 1980 under 241

- 260; prepared by Union Carbide Corp., submitted by American Cyanamid Co., Princeton, N.J.; CDL:099492

- B)

52857 Vilkas, A.G.; Schup ner, J.K. (1980) The Acute Toxicity of AC 217,300 to the Rainbow Trout,~Salmo gairdneri~Richardson: UCES Project No. 11506

- 20

- 34. (Unpublished study received Oct 8, 1980 under 241

- 260; prepared by Union Carbide Corp., submitted by American Cyanamid Co., Pr inceton, N.J.; CDL:243466

- B)

52858 Vilkas, A.G.; Schupner, J.K. (1980) The Acute Toxicity of AC 217,300 to the Channel Catfish,~Ictalurus punctatus~(Rafin

- esque): UCCES Project No. 11506

- 20

- 32. (Unpublished study re

- ceived Oct 8, 1980 under 241

- 260; p repared by Union Carbide Corp., submitted by American Cyanamid Co., Princeton, N.J.; CDL: 243466

- C)

92163007 Gagne, J. (1990) American Cyanamid Company Phase 3 Summary of MRID 00035279. AC 217,300

- Acute LC50

- Bluegill Sunfish: Project No. 11506

- 20

- 31; June 23, 1980. Prepared by UNION CARBIDE CORP. 12 p.

92163008 Gagne, J. (1990) American Cyanamid Company Phase 3 Summary of MRID 00052858. AC 217,300

- Acute LC50

- Channel Catfish: Project No. 11506

- 20

- 32; August 6, 1980. Prepared by UNION CARBIDE CORP . 13 p.

92163009 Gagne, J. (1990) American Cyanamid Company Phase 3 Summary of MRID 00052857. AC 217,300

- Acute LC50

- Rainbow Trout: Project No. 11506

- 20

- 34; August 5, 1980. Prepared by UNION CARBIDE CORP. 13 p.

72

- 2 Acute Toxicity to Freshwate r Invertebrates



### MRID Citation

### 41 164248 Morrissey, A. (1979) The Acute Toxicity of AC 217,300 to the Water Flea: Daphnia magna Straus: UCES Project No. 11506

- 20

- 21. Unpublished study prepared by Union Carbide Environmental Services, Union Carbide Corp. 10 p.

92163010 Gagne, J. (1990) American Cyanamid Company Phase 3 Summary of MRID 00099779. AC 217,300

- Acute LC30

- Daphnia: Project No. 11506

- 20

- 33; June 23, 1980. Prepared by UNION CARBIDE CORP. 12 p.

35877 Vilkas, A.G.; Browne, A.M. (1980) The Acute To xicity of AC 217,300 (Lot No. AC 3196

- 99B, 91.6% Active Ingredient) to the Water Flea, Daphnia magna Straus: UCCES Project No. 11506

- 20

- 33. (Unpublished study received Jul 1, 1980 under 241

- 260; prepared by Union Carbide Corp., submitted by American Cyanam id Co., Prince

- ton, N.J.; CDL:099492

- C)

72

- 3 Acute Toxicity to Estuarine/Marine Organisms



### MRID Citation

46678301 Hughes, C.; Holmes, C. (2005) BAS 315 I: Acute Toxicity to the Mysid Shrimp, Americamysis bahia, Determined Under Flow

- Through Test C onditions. Project Number: 49244, 132203, 2005/5000091. Unpublished study prepared by ABC Laboratories, Inc. 31 p.

46684801 Hicks, S.; Holmes, C. (2005) BAS 315 I: Effect on New Shell Growth of the Eastern Oyster (Crassostrea virginica). Project Number: 4 9245, 132200, 2005/5000173. Unpublished study prepared by Analytical Bio

- Chemistry Labs., Inc. 43 p.

46684802 Hughes, C.; Holmes, C. (2005) BAS 315 I: Acute Toxicity to the Mysid Shrimp, Americamysis bahia, Determined Under Flow

- Through Test Conditions. P roject Number: 49244, 132203, 2005/5000091. Unpublished study prepared by Analytical Bio

- Chemistry Labs., Inc. 31 p.

46684803 Warbritton, R.; Holmes, C. (2005) BAS 315 I: Acute Toxicity Test with the Sheepshead Minnow, Cyprinodon variegatus, Determined Un der Flow

- Through Test Conditions. Project Number: 49243, 132197, 2005/5000124. Unpublished study prepared by Analytical Bio

- Chemistry Labs., Inc. 33 p.

72

- 4 Fish Early Life Stage/Aquatic Invertebrate Life Cycle Study



### MRID Citation

101610 Forbis, A. ; Boudreau, P.; Thompson, C.; et al. (1982) Chronic Toxicity of 14C

- AC 217,300 to Daphnia magna under Flow

- through Test Conditions: ABC #28568. Final rept. (Unpublished study received May 14, 1982 under 241

- 260; prepared by Analytical Bio

- chemistry Labora tories, Inc., submitted by American Cyanamid Co., Princeton, NJ; CDL:247502

- C)

92163011 Gagne, J. (1990) American Cyanamid Company Phase 3 Summary of MRID 00101610. AC 217,300

- Invertebrate Life

- Cycle Test, Daphnia: Project No. 28568; April 26, 1982. Prepared by ANALYTICAL BIOCHEMISTRY LABS, INC. 14 p.

### 42 72

- 6 Aquatic org. accumulation (see Fate Studies 165

- 4)



### MRID Citation

92163030 Lee, A. (1990) American Cyanamid Company Phase 3 Summary of MRID 00101611. AMDRO Fire Ant Insecticide (CL 217,300): Identification and Characterization of CL 217,300 and Its Metabolite in Bluegill Sunfish Exposed to 1.8 ppb of CL 217,300 in Water. Prepared by AMERICAN CYANAMID CO. 21 p.

101611 Barringer, D. 1982. Identifiaction and Characterization of CL 217,300 and It's Metabolite in Bluegill Sunfish Exposed to 1.8 ppb of CL 217,300 in Water. performed by ABC Laboratory, Columbia MO and American Cyanamid, Princeton NJ. sponsored by American Cyanamid Company, Princeton NJ. Received by EPA 4/4/90. MRID 101611.

141

- 1 Honey bee acute contact



### MRID Citation

41607801 Thompson, M.; Hoxter, K.; Smith, G. (1990) AC 217,300: An Acute Contact Toxicity Study with the Honey Bee: Lab Project Number: 130

- 151B. Unpublished study prepared by Wildlife International Ltd. 26 p.

35281 Gillespie, J.M.; Atkins, L. (1977) Toxicity of Experimental Com

- pounds AC 217,300 and AC 206,859 to Honey Bees: Experiment No. 60904

- 77

- Z3E. (Unpublished study received Jul 1, 1980 under 241

- 260; prepared in cooperation with Univ. of California

-- Riv

- erside, Dept. of Entomology, submitted by American Cyanamid Co., Princeton, N.J.; CDL:099488

- C)

Acute Toxicity to Aquatic Insects

850.1735 Whole sediment: acute freshwater invertebrates



### MRID Citation

46684804 Warbritton, R.; Holmes, C. (2005) BA S 315 I: Acute Toxicity to the Midge Larvae, Chironomus dilutus, in Whole Sediment. Project Number: 132206, 49246, 2005/5000123. Unpublished study prepared by Analytical Bio

- Chemistry Labs., Inc and Agvise Inc. 66 p.

850.1740 Whole sediment: acute m arine invertebrates



### MRID Citation

46684805 Hughes, C.; Holmes, C. (2005) BAS 315 I: Acute Toxicity to the Marine Amphipod, Leptocheirus plumulosus, in Whole Sediment. Project Number: 49247, 132209, 2005/5000174. Unpublished study prepared by Analytical Bi o

- Chemistry Labs., Inc and Agvise Inc. 45 p

### 43 APPENDIX B. SIP v.1.0 and STIR v. 1.0 Descriptions, Assumptions , Inputs and Outputs

SIP v.1.0 SIP v.1.0 provides an upper bound estimate of exposure of birds and mammals to pesticides through drinking wate r alone. This model is intended for use in problem formulation to determine whether or not drinking water exposure alone is a potential pathway of concern. This does not aggregate drinking water exposure with other exposure routes (i.e., diet, inhalation, dermal).



### SIP employs the following conservative assumptions to derive upper bound exposure estimates: 1) The chemical concentration in drinking water is at the solubility limit in water (at 25 o 

### C). 2) The assessed animals obtain 100% of their daily water needs through drinking water. 3) The daily water need is equivalent to the daily water flux rate as calculated by Nagy and Peterson (1988). 4) The body weight of the assessed bird is equivalent to the smallest generic bird modeled in T

- REX (i.e., 20 g). This assumption results in the highest ratio of exposure to toxicity for the 3 assessed avian body weights of T

- REX (i.e., 20, 100, 1000 g). 5) The body weight of the assessed mammal is equivalent to the largest generic mammal modeled in T

- REX (i.e., 100 0 g). This results in the highest ratio of exposure to toxicity for the 3 assessed mammalian body weights of T

- REX (i.e., 15, 35, 1000 g).

Parameter Value Chemical name hydramethylnon Solubility (in water at 25 o C; mg/L) 0.009

Mammalian LD 50 (mg/kg

- bw) 817 Mammalian test species laboratory rat Body weight (g) of "other" mammalian species

Mammalian NOAEL (mg/kg

- bw) 50 Mammalian test species laboratory rat Body weight (g) of "other" mammalian species

Avian LD 50 (mg/kg

- bw) 1828 Avian test species mallard duck Body weight (g) of "other" avian species Mineau scaling factor 1.15

Mallard NOAEC (mg/kg

- diet) 28.5 Bobwhite quail NOAEC (mg/kg

- diet) 57 NOAEC (mg/kg

- diet) for other bird speci es Body weight (g) of other avian species NOAEC (mg/kg

- diet) for 2nd other bird species Body weight (g) of 2nd other avian species

### 44 Table 2. Mammalian Results Parameter Acute Chronic Upper bound exposure (mg/kg

- bw) 0. 0015 0.0015 Adjusted toxicity value (mg/kg

- bw) 628.4042 38.4580 Ratio of exposure to toxicity 0.0000 0.0000

Conclusion* Drinking water exposure alone is NOT a potential

concern for mammals Drinking water exposure alone is NOT a potential

concern for mam mals

Table 3. Avian Results Parameter Acute Chronic Upper bound exposure (mg/kg

- bw) 0.0073 0.0073 Adjusted toxicity value (mg/kg

- bw) 949.1440 1.4140 Ratio of exposure to acute toxicity 0.0000 0.0052

Conclusion* Drinking water exposure alon e is NOT a potential concern for birds Drinking water exposure alone is NOT a potential concern for birds

*Conclusion is for drinking water exposure alone. This does not combine all routes of exposure. Therefore, when aggregated with other routes ( i.e

., diet, inhalation, dermal), pesticide exposure through drinking water may contribute to a total exposure that has potential for effects to non

- target animals.



### STIR v1.0 Inhalation is a potentially important route of exposure to pesticides for mammalian and avian wildlife (Driver et al. 1991; USEPA 2004a). STIR is a screening tool used at the Problem Formulation phase to assess the potential for risk to bird and mammals from inhalation exposure. The exposure pathways that are assessed by this tool incl ude both droplet inhalation and vapor phase inhalation. Allometric equations that relate inhalation rate to body weight are used to derive an estimated inhalation dose of either droplets or vapor for a 0.020 kg bird and a 0.015 kg mammal (Mineau et al. 19 96; Sample and Arenal 1999; USEPA 1993).

Results from acute inhalation toxicity studies for mammals from the "six

- pack" that are routinely submitted to the Registration Division of the Office of Pesticide Programs can be directly compared with the estima ted inhalation doses from vapor and droplets. In most cases however, avian inhalation data are lacking. STIR uses the avian oral toxicity data together with both the mammalian oral and inhalation toxicity data to derive an estimate of avian inhalation to xicity. Based on the findings of the 2004 Science Advisory Panel (USEPA 2004), an adjustment factor is applied to these data to adjust the estimate of avian inhalation toxicity for differences in diffusion efficiency across the avian lung membrane compare d to the mammalian lung membrane.

STIR relies on the application rate, application method, defined droplet spectra (if applicable), molecular weight, vapor pressure and the temperature associated with the vapor pressure of a specific chemical to obtain an estimate of the droplet and vapor concentration in the air. These concentrations are compared with an estimated inhalation LD50 of a specific chemical as a ratio

### 45 that is then compared with a threshold of 0.1. If the ratio of the exposure to the toxicity exceeds 0.1, then the screening tool indicates that a reviewer is to "Proceed to Refinements", at which point the reviewer can request specific studies that will help to address uncertainty related to inhalation risk. The user's guide contains informatio n for the specific studies that may be requested. However, if the screening tool indicates "Exposure not Likely Significant", then the reviewer can assume that the inhalation pathway is not expected to be a significant source of risk.

Notes * The satu rated air concentration is the theoretical maximum pure product air concentration at 25oC and 1 atm of pressure. * The height of the direct spray column is 3.3 m for aerial applications and 1 m for ground applications. * The duration of vapor inhalation is assumed to be 1 hour and the duration of direct spray inhalation is assumed to be 1.5 minutes for aerial and 30 seconds for ground applications. * The fraction of direct spray that can be inhaled is assumed to be 90%, unless a droplet spectra is specif ied on the label. Please see the user's guide for more information. * This model accounts for the difference in both avian and mammalian field active inhalation rate compared to the resting rate by multiplying the resting inhalation rate by 3 according t o USEPA, 1993. * Both of the mammalian and avian inhalation LD50's are adjusted for body weight using allometric equations based on work by Mineau et al. 1996. The avian allometric equation uses the Mineau scaling factor to modify the equation based on c hemical specific data. If chemical

specific data are available the user can specify the avian scaling factor (see Mineau, et al.,1996). Otherwise, enter the EFED default value of 1.15. STIR will not run unless a Mineau scaling factor is entered. Howeve r, 1 can be entered if the assessor believes that body weight does not influence the toxicity of the chemical being assessed. * The inhalation of droplets and the inhalation of vapor phase pesticide are accounted for in this model as two separate routes of exposure. The corresponding dose estimations should not be combined to obtain a composite exposure value.

### 46 

## Input

Application and Chemical Information
Enter Chemical Name hydramethylnon Enter Chemical Use granular Is the Ap plication a Spray? (enter y or n) n If Spray What Type (enter ground or air) Enter Chemical Molecular Weight (g/mole) 494.5 Enter Chemical Vapor Pressure (mmHg) 2.00E

- 08 Enter Application Rate (lb a.i./acre) 0.0219

Toxicity Properti es **Bird** Enter Lowest Bird Oral LD 50 (mg/kg bw) 1828 Enter Mineau Scaling Factor 1.15 Enter Tested Bird Weight (kg) 0.178 **Mammal** Enter Lowest Rat Oral LD 50 (mg/kg bw) 817 Enter Lowest Rat Inhalation LC 50 (mg/L) 2.9 Duration of Rat Inhalation Study (hrs) 8 Enter Rat Weight (kg) 0.35


## Output Results Avian (0.020 kg ) Maximum Vapor Concentration in Air at Saturation (mg/m 3 ) 5.32E

- 04 Maximum 1

- hour Vapor Inhalation Dose (mg/kg) 6.69E

- 05 Adjusted Inhalatio n LD 50 7.24E+01 Ratio of Vapor Dose to Adjusted Inhalation LD 50 9.25E

- 07 Exposure not Likely Significant Maximum Post

- treatment Spray Inhalation Dose (mg/kg) not applicable Ratio of Droplet Inhalation Dose to Adjusted Inhalation LD 50 not applicab le not applicable



### Results Mammalian (0.015 kg ) Maximum Vapor Concentration in Air at Saturation (mg/m 3 ) 5.32E

- 04 Maximum 1

- hour Vapor Inhalation Dose (mg/kg) 8.41E

- 05 Adjusted Inhalation LD 50 3.45E+02 Ratio of Vapor Dose to Adjuste d Inhalation LD 50 2.44E

- 07 Exposure not Likely Significant Maximum Post

- treatment Spray Inhalation Dose (mg/kg) not applicable Ratio of Droplet Inhalation Dose to Adjusted Inhalation LD 50 not applicable not applicable

### 47 A PPENDIX C. Physical and Che mical Properties of Hydramethylnon Major Degradates

1,5

- bis(alpha, alpha, alpha

- trifluoro

- p

- tolyl)

- 1,4

- pentadien

- 3

- one Chemical CL98,724 MRID 42473301
Chemical Name 1,5

- bis(alpha, alpha, alpha

trifluoro

- p

- tolyl)

- 1,4

- pentadien

- 3

- one MRID 42473301

Em pirical Formula C 19 H 12 F 6 O 1 EPI V4.10
SMILES O=C(C=Cc2ccc(C(F)(F)F)c c2)C=Cc3ccc(C(F)(F)F)cc3 EPI V4.10

Structure MRID 42473301 Degradate found in Aqueous Photolysis Anaerobic Soil Meta. Field Dissipation

Molecular Mass 370.3 MRID 424 73301 Water solubility 38.9 ppb EPI V4.10
4H

- pyrimido [2,1

- c) as

- triazio

- 4

- one 1, 6, 7, 8

- tetrahydro

- 7,7

- dimethyl

- 3

- [p

- (trifloromethyl)

- styryl]
Chemical CL247,176 MRID 42473301
Chemical Name 4H

- pyrimido [2,1

- c) as

triazio

- 4

- one 1, 6, 7, 8

- tetrahyd ro

- 7,7

- dimethyl

- 3

- [p

- (trifloromethyl)

- styryl] MRID 42473301

Empirical Formula C 17 H 7 F 3 N 4 O 1 EPI V4.10
SMILES C1(=O)C(C=Cc2ccc(C(F)(F)F) cc2)=NNC2=NCC(C)(C)CN12 EPI V4.10

Structure MRID 42473301 Degradate found in Aqueous Photolysis F ield Dissipation

Molecular mass 350.35 MRID 42473301 Water solubility 11,670 ppb EPI V4.10

### 48 APPENDIX D

. Toxicity Data of ECO SAR estimation (EPI V4.10)

Hydramethylnon SMILES : N1CC(C)(C)CNC1=NN=C(C=Cc2ccc(C(F)(F)F)cc2)C=Cc3ccc(C(F)(F)F)cc3 CHEM : Hydramethylnon CAS Num: 067485

- 29

- 4 ChemID1: ChemID2: ChemID3: MOL FOR: C25 H24 F6 N4 MOL WT : 494.49 Log Kow: 8.51 (KowWin estimate) Melt Pt: Wat Sol: 0.006 mg/L (experimental database)

ECOSAR v1.00 Class(es) Found

--------------------------- --- Aliphatic Amines Hydrazines Predicted ECOSAR Class Organism Duration End Pt mg/L (ppm)

=========================== ================== ======== ====== ========== Aliphatic Amines : Fish 96

- hr LC50 0.011 * Aliphatic Amines : Daphnid 48

- hr LC50 0.004 Aliphatic Amines : Green Algae 96

- hr EC50 0.014 * Aliphatic Amines : Fish ChV 0.000314 Aliphatic Amines : Daphnid ChV 0.014 * Aliphatic Amines : Green Algae ChV 0.00102 Aliphatic Amines : Fis h (SW) 96

- hr LC50 0.012 * Aliphatic Amines : Mysid Shrimp (SW) 96

- hr LC50 0.003 Aliphatic Amines : Green Algae (SW) 96

- hr EC50 0.014 * Aliphatic Amines : Fish (SW) ChV 0.000314 Aliphatic Amines : Mysid Shrimp (SW) ChV 0.014 * Aliphatic Amines : Green Algae (SW) ChV 0.00118

Hydrazines : Fish 96

- hr LC50 0.00 3 Hydrazines : Daphnid 48

- hr LC50 2.854 * Hydrazines : Green Algae 72

- hr EC50 9.27e

- 005 Hydrazines : Fish ChV 0.000151 ! Hydrazines : Daphnid ChV 0.000604 ! Hydrazines : Green Algae ChV 2.31e

- 005 !

=========================== ================== ======== ====== ========== Neutral Organic SAR : Fish 96

- hr LC50 0.00118 (Baseline Toxicity) : Daphnid 48

- hr LC50 0.00149 : Green Algae 96

- hr EC50 0.009 * : Fish C hV 9.67e

- 005 : Daphnid ChV 0.000436 : Green Algae ChV 0.011 *

### 49 Note: * = asterisk designates: Chemical may not be soluble enough to mea sure this predicted effect.

Note: ! = exclamation designates: The toxicity value was determined from a predicted SAR using established acute

- to

- chronic ratios and ECOSAR regression techniques which are documented in the supporting Technical Reference Manual. When possible, this toxicity value should be considered in a weight of evidence approach.

Aliphatic Amines:

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

For Fish 96

- hr LC50: For aliphatic amines with log Kow greater than 7.0, a test duration of greater than 96 hrs may be required for proper expression of toxicity. Also, if the toxicity value obtained by the use of this equation exceeds the water solubility (measured or estimated), mortalities greater than 50% would not be expected in a saturated solution during an exposure period of 96 hrs.

For Daphnid 48

- hr LC50: For aliphatic amines with log Kow greater than 5.0, a test duration of greater than 48 hrs may be required for proper expression of toxicity. Also, if the toxicity value obtained by the use of this equation exceeds the water solubility (measured or estimated), significant mortalities would not be expected in a saturated solution during an exposure period of 48 hrs.

For Green Algae Acute Toxicity Values: If the log Kow of the chemical is greater than 7, or if the compound is solid and the EC50 exceeds the water solubility by 10X, no effects at saturation are predicted for these endpoints.

For Mysid Shrimp Acute Toxicity Values: If the log Kow of the chemical is greater than 6, or if th e compound is solid and the EC50 exceeds the water solubility by 10X, no effects at saturation are predicted for these endpoints.

For Fish and Daphnid Chronic Toxicity Values: If the log Kow of the chemical is greater than 8.0, or if the compound is so lid and the ChV exceeds the water solubility by 10X, no effects at saturation are predicted for these endpoints.

For Green Algae Chronic Toxicity Values: If the log Kow of the chemical is greater than 7.0, or if the compound is solid and the ChV exceed s the water solubility by 10X, no effects at saturation are predicted for these endpoints.

ECOSAR v1.00 SAR Limitations:

---------------------------- Maximum LogKow: 6.0 (Fish, Mysid LC50) Maximum LogKow: 5.0 (Daphnid LC50) Maximum LogKow: 7.0 (Green Alg ae EC50) Maximum LogKow: 8.0 (Fish, Daphnid ChV) Maximum LogKow: 7.0 (Green Algae ChV) Maximum Mol Wt: 1000

### 50 Hydrazines:

----------

For Fish and Daphnid Acute Toxicity Values: If the log Kow of the chemical is greater than 5.0, or if the compound is sol id and the LC50 exceeds the water solubility by 10X, no effects at saturation are predicted for these endpoints.

For Green Algae Acute Toxicity Values: If the log Kow of the chemical is greater than 6.4, or if the compound is solid and the EC50 exceeds the water solubility by 10X, no effects at saturation are predicted for these endpoints.

For All Chronic Toxicity Values: If the log Kow of the chemical is greater than 8.0, or if the compound is solid and the ChV exceeds the water solubility by 10X, no effects at saturation are predicted for these endpoints.

ECOSAR v1.00 SAR Limitations:

---------------------------- Maximum LogKow: 5.0 (LC50) Maximum LogKow: 6.4 (EC50) Maximum LogKow: 8.0 (ChV) Maximum Mol Wt: 1000

Baseline Toxicity SAR Limitation s:

--------------------------------- Maximum LogKow: 5.0 (Fish 96

- hr LC50; Daphnid LC50) Maximum LogKow: 6.4 (Green Algae EC50) Maximum LogKow: 8.0 (ChV) Maximum Mol Wt: 1000

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



### Degradate CL247,176 SMILES : O=C1C(C=Cc3ccc(C(F)(F)F)cc3)=NNC2=NCC(C)(C)CN12 CHEM : 4H

- pyrimido [2,1

- c) as

- triazio

- 4

- one 1, 6, 7, 8

- tetrahydro

- 7,7

- dimeth yl

- 3

- [p

- (trifloromethyl)

- styryl] CAS Num: ChemID1: ChemID2: ChemID3: MOL FOR: C17 H17 F3 N4 O1 MOL WT : 350.35 Log Kow: 3.19 (KowWin estimate) Melt Pt: Wat Sol: 11.67 mg/L (WskowWin estimate)

ECOSAR v1.00 Class(es) Found

------------------------------ Amides

### 51 Pre dicted ECOSAR Class Organism Duration End Pt mg/L (ppm)

=========================== ================== ======== ====== ========== Amides : Fish 96

- hr LC50 5.182 Amides : Daphnid 48

- hr LC50 4.400 Amides : Green Algae 96

- hr EC50 0.359 Amides : Fish ChV 0.031 Amides : Daphnid ChV 0.058 ! Amides : Green Algae ChV 0.585

=========================== ================== ======== ====== ========== Neutral Organic SAR : Fish 96

- hr LC50 26.648 * (Baseline Toxicity) : Daphnid 48

- hr LC50 17.752 * : Green Algae 96

- hr EC50 12.462 * : Fish ChV 2.464 : Daphnid ChV 2.023 : Green Algae ChV 5.603

Note: * = asterisk designates: Chemical may not be soluble enough to measure this predicted effect.

Note: ! = exclamation designates: The toxicity value was determined from a predicted SAR using established acute

- to

- chronic ratios and ECOSAR regression techniques which are documented in the supporting Technical Reference Manual . When possible, this toxicity value should be considered in a weight of evidence approach.

Amides :

------- No limitations known at this time.

ECOSAR v1.00 SAR Limitations:

---------------------------- Maximum LogKow: >8.5 (LC50) Maximum LogKow: >8.0 (EC50,ChV) Maximum Mol Wt: 1000

Baseline Toxicity SAR Limitations:

--------------------------------- Maximum LogKow: 5.0 (Fish 96

- hr LC50; Daphnid LC50) Maximum LogKow: 6.4 (Green Algae EC50) Maximum LogKow: 8.0 (ChV) Maximum Mol Wt: 1000

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

### 52 Degradate C L98,724 SMILES : O=C(C=Cc2ccc(C(F)(F)F)cc2)C=Cc3ccc(C(F)(F)F)cc3 CHEM : 1,5

- bis(alpha, alpha, alpha

- trifluoro

- p

- tolyl)

- 1,4

- pentadien

- 3

- one CAS Num: ChemID1: ChemID 2: ChemID3: MOL FOR: C19 H12 F6 O1 MOL WT : 370.30 Log Kow: 5.95 (KowWin estimate) Melt Pt: Wat Sol: 0.03888 mg/L (WskowWin estimate)

ECOSAR v1.00 Class(es) Found

------------------------------ Vinyl/Allyl Ketones Predicted ECOSAR Class Organism Duration End Pt mg/L (ppm)

=========================== ================== ======== ====== ========== Vinyl/Allyl Ketones : Fish 96

- hr LC50 0.446 * Vinyl/Allyl Ketones : Daphnid 48

- hr LC50 0.108 * Vinyl/Allyl Ketones : Green Algae 96

- hr EC50 0.286 * Vinyl/Allyl Ketones : Fish ChV 0. 019 Vinyl/Allyl Ketones : Daphnid ChV 0.030 ! Vinyl/Allyl Ketones : Green Algae ChV 0.246 *! Vinyl/Allyl Ketones : Fish (SW) 96

- hr LC50 0.045 * Vinyl/Allyl Ke tones : Mysid Shrimp (SW) 96

- hr LC50 0.012 Vinyl/Allyl Ketones : Fish (SW) ChV 0.055 * Vinyl/Allyl Ketones : Mysid Shrimp (SW) ChV 0.00015 !

=========================== ===== ============= ======== ====== ========== Neutral Organic SAR : Fish 96

- hr LC50 0.130 * (Baseline Toxicity) : Daphnid 48

- hr LC50 0.121 * : Green Algae 96

- h r EC50 0.264 * : Fish ChV 0.011 : Daphnid ChV 0.022 : Green Algae ChV 0.196 *

Note: * = asterisk designates: Chemical may not be soluble enough to measure this predicted effect.

Note: ! = exclamation designates: The toxicity value was determined from a predicted SAR using established acute

- to

- chronic ratios an d ECOSAR regression techniques which are documented in the supporting Technical Reference Manual. When possible, this toxicity value should be considered in a weight of evidence approach.

Vinyl/Allyl Ketones:

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

For All Acute and Chronic Toxicity Values: If the log Kow of the chemical is greater than the value listed below, or if the compound is solid and the

### 53 LC50, EC50 or ChV exceeds the water solubility by 10X, no effects at saturation are predicted for these endpoints.

ECOSAR v1.00 SAR Limitations:

---------------------------- Maximum LogKow: 5.0 (Fish 96

- hr LC50; Daphnid LC50; Mysid LC50) Maximum LogKow: 6.4 (Green Algae EC50) Maximum LogKow: 8.0 (ChV) Maximum Mol Wt: 1000

Baseline Toxicity SAR Limitations:

------- -------------------------- Maximum LogKow: 5.0 (Fish 96

- hr LC50; Daphnid LC50) Maximum LogKow: 6.4 (Green Algae EC50) Maximum LogKow: 8.0 (ChV) Maximum Mol Wt: 1000

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