- Page 2 of 126

- 

### The results of this screening

- level assessment on the proposed alpha

- cypermethrin uses indicate

that risk s of adverse effects to non

- target organisms are expected for aquatic animals and

mammals. Indirect effects canno t be precluded for any taxa. These results are summarized in the body of the document in Section 1.2.

Uncertainties

The environmental fate database was bridged from the cypermethrins to alpha

- cypermethrin. Data specific for alpha

- cypermethrin suggest that the persistence of alpha enriched mixture may be less persistent than that of the cypermethrins (zeta and racemic cypermethrin), therefore environmental exposures may be over estimated than if data were used that were conducted using alpha

- cypermethrin as the test material. Appendix A outlines specific data that were conducted using alp ha

- cypermethrin as the test material and where data were bridged from the

racemic or zeta

- cypermethrin.

Additionally, t here are no chronic exposure toxicity data for freshwater invertebrates, benthic organisms, or estuarine/marine fish. Therefore, acute

- to

- chronic ratios (ACRs) based on the appropriate relationships were applied to each of the taxa (e.g., an ACR based on estuarine/marine invertebrates, for which there are both acute and chronic toxicity data, was applied to freshwater invertebrates) . The ACR is considered protective for the purpose of this risk assessment; however, the application of an ACR in the absence of actual data does introduce uncertainty to the risk assessment.

Recommended Label Amendment

The proposed label contains the f ollowing language: “DO NOT apply more than the combined maximum seasonal total for cypermethrin (including alpha

- cypermethrin, zeta

- cypermethrin, and any other products containing cypermethrin) products.” T he phrase “combined maximum

seasonal total for cypermethrin ” is ambiguous and unclear. This is likely confusing for the end

user who is applying a single product with a single active ingredient

. EFED recommends revising the prop o sed label to reflect the permitted maximum annual mass of active ingr edient

, including mixtures with racemic and zeta

- cypermethrin . This should be reflected on all cypermethrin labels.- Page 3 of 126

- 

# Environmental Fate and Ecological Risk Assessment for the Registration of Alpha

- Cypermethrin

Alpha

- Cypermethrin ( R )

- cyano(3

- phenoxyphenyl)methyl (1 S ,3 S )

- rel

- 3

- (2,2

- dichloroethenyl)

- 2,2

- dimethylcyclopropanecarboxylate CAS Registry Number : 67375

- 30

- 8

PC Code : 209600

Prepared by:

Reuben D. Baris, Environmental Scientist Elizabeth A. Riley , Biologist

U. S. Environmental Protection Agency Office of Pesticide Programs

Environmental Fate and Effects Division

Environmental Risk Branch IV

1200 Pennsylvania Ave., NW

Mail Code 7507P Washington DC 20460 Reviewed by: Nathan Miller, Biologist, ERB VI

William P. Eckel , Ph.D, Senior Science Advisor, ERB VI
Mark Corbin, Branch Chief, ERB VI



### Date: September 19 , 201 2

Table of Contents- Page 4 of 126

- 

### 1. Executive Summary

................................ ................................ ................................ .............. 6

1.1. Nature of Chemical Stressor

................................ ................................ ................................ .................... 6

1.2. Potential Risks to Non

- target Organisms

................................ ................................ ............................... 7

1.3. Conclusions

- Exposure Characterization

................................ ................................ .............................. 7

1.4. Conclusions

- Effects Characterization

................................ ................................ ................................ ... 8 

### 2. Problem Formulation

................................ ................................ ................................ ........... 9

2.1. Nature of Regulatory Action

................................ ................................ ................................ .................... 9

2.2. Stressor Source and Distribution

................................ ................................ ................................ ............ 9

2.2.1. Nature of Chemical Stressor

................................ ................................ ................................ ................ 9

2.2.2. Overview of Pesticide Usage

................................ ................................ ................................ ............. 10

2.3. Receptors

................................ ................................ ................................ ................................ ................. 12

2.3.1. Aquatic and Terrestrial Effects

................................ ................................ ................................ .......... 12

2.3.2. Ecosystems Potentially at Risk

................................ ................................ ................................ .......... 13

2.4. Assessment Endpoints

................................ ................................ ................................ ............................ 13 2.5. Conceptual Model

................................ ................................ ................................ ................................ ... 14

2.5.1. Risk Hypotheses

................................ ................................ ................................ ................................ 14

2.5.2. Con ceptual Diagram

................................ ................................ ................................ .......................... 14 2.6. Analysis Plan

................................ ................................ ................................ ................................ ........... 17

2.6.1. Residues of Concern

................................ ................................ ................................ .......................... 17

2.6.2. Preliminary Identification of Data Gaps and Uncertainties

................................ ............................... 18

2.6.3. Evaluation of Multiple Active Ingredients and Mixtures

................................ ................................ .. 18

2.6.4. Measures of Exposure

................................ ................................ ................................ ....................... 18

2.6.5. Measures of Effect

................................ ................................ ................................ ............................. 19

2.6.6. Integration of Exposure and Effects

................................ ................................ ................................ .. 20 

### 3. Analysis

................................ ................................ ................................ ............................. 21

3.1. Use Characterization

................................ ................................ ................................ .............................. 21

3.2. Exposure Characterization

................................ ................................ ................................ .................... 22

3.2.1. Environmental Fate and Transport Characterization

................................ ................................ ......... 22

3.2.2. Measures of Aquatic Exposure

................................ ................................ ................................ .......... 28

3.2.3. Measures of Terrestrial Exposure

................................ ................................ ................................ ...... 33

3.3. Ecological Effects Characterization

................................ ................................ ................................ ...... 37

3.3.1. Aquatic Toxicity Assessment

................................ ................................ ................................ ............ 37

3.3.2 Terrestrial Effects Characterization

................................ ................................ ................................ ... 44 

### 4. Risk Characterization

................................ ................................ ................................ ......... 47

4.1. Risk Estimation

................................ ................................ ................................ ................................ ....... 47

4.1.1. Aquatic Organisms

................................ ................................ ................................ ............................ 48

4.1.2. Terrestrial Organisms

................................ ................................ ................................ ........................ 51

4.2. Risk Description

................................ ................................ ................................ ................................ ...... 54

4.2.1 Exposure to Aquatic Organisms

................................ ................................ ................................ ........ 54

4.2.2 Risks to Aquatic Animals

................................ ................................ ................................ .................. 55

4.2.3 Risks to Aquatic Plants

................................ ................................ ................................ ...................... 58

4.2.4. Risks to Mammals

................................ ................................ ................................ ............................. 59

4.2.5. R isk to Birds

................................ ................................ ................................ ................................ ...... 59

4.2.6. Potential Effects on Terrestrial Invertebrates

................................ ................................ .................... 59

4.2.7. Risk to Terrestrial Non

- target Plants

................................ ................................ ................................ . 60

4.3. Uncertainties and Data Gaps

................................ ................................ ................................ ................. 61

4.3.1. Fate and Transport Uncertanties

................................ ................................ ................................ ........ 61

4.3.2. Effects Uncertainties

................................ ................................ ................................ ......................... 61


### 5. F ederally Threatened and Endangered (Listed) Species Concerns

............................... 62

5.1. Action Area

................................ ................................ ................................ ................................ ............. 63

5.2. Taxonomic Groups Potentially at Risk

................................ ................................ ................................ . 63

5.2.1. Probit Dose

- Response Analysis

................................ ................................ ................................ ...... 65

5.2.2. Listed Species Occurrence Associated with Alpha

- Cypermethrin Use

................................ ...... 66- Page 5 of 126

- 

### 6. References

................................ ................................ ................................ ............................ 68

6.1. Submitted Environmental Fate and Transport Studies

................................ ................................ ..... 69

6.2. Submitted Ecotoxicity Studies

................................ ................................ ................................ .............. 72 

### Appendix A. Alpha

- Cypermethrin Bridging Strategy

................................ ................................ .......... 94 Appendix B. Sumary of Environmental Fate Data for Alpha

- cypermethrin

................................ .... 101 Appendix C. Aquatic Model Input/Output Data.

................................ ................................ ............... 104 Appendix D. Model Outputs

................................ ................................ ................................ .................. 107 Appendix E. Reported Ecological Incidents for Racemic and Zeta

- Cypermethrin in EIIS.

........... 116 Appendix F. Federally Listed Species Potentially at Risk from the Proposed Uses of Alpha Cypermethrin

................................ ................................ ................................ ................................ .......... 125- Page 6 of 126

- 

### 1. Executive Summary

1.1. Nature of Chemical Stressor

BASF is seeking registration for the new chemical insecticide alpha

- cypermethrin ( BAS 310 40

I ; (R)

- cyano(3

- phenoxyphenyl)methyl (1S,3S)

- rel

- 3

- (2,2

- dichloroethenyl)

- 2,2

- dimethylcyclopropanecarboxylate ; CAS#: 67375

- 30

- 8 ; PC code: 209600 ). Alpha

- cypermthrin is

a broad

- spectrum Type II pyrethroid insecticide that is proposed for use on a wide variety of agricultural crops. Alpha

- cype rmethrin, like other pyrethroids, is considered an axonic poison that prevents sodium channels in an organism’s neuronal membranes from closing, resulting in paralysis.

Alpha

- cyperm ethrin is an enriched enantiome ric mixture of the previously registered r acemic cypermethrin (PC code 109702). Racemic cypermethrin consists of eight stereoisomers with two optically active centers ( stereogenic centers or stereocenters) while the enriched alpha

cypermethrin consists of only 2 of the ster e oisomers

. In addition to the registerd racemic and proposed new chemical alpha

- cypermethrin, the Agency has previously registered the isomerically enriched zeta

- cypermethrin (PC code 129064)

, which consist s of 4 of the

ster e oisomers. Based on similarities in the ch emical properties and toxicological endpoint s
, environmental fate and ecotoxicity data are bridged between racemic cypermethrin and the enriched isomeric mixtures (i.e., alpha

- cypmerthin and zeta

- cypermethrin) ( Appendix A

includes additional detail on the bridging strategy)

. Though the environmental fate and ecotoxicity datasets for alpha

- cypermethrin mostly consist of studies conducted with either racemic or zeta cypermethrin, this document will discuss the environmental fate and ecological

risks associat ed with the proposed new chemical alpha

- cypermethrin and reference the other chemicals where appropriate

.

This assessment is for a national registration request for the following uses: alfalfa, brassica vegetables, citrus fruits, corn (field, pop, seed a nd sweet), cotton, cucurbits, fruiting vegetables, leafy vegetables, legume vegetables, rice (grain and st raw), root and tuber vegetables, sorg h um (and other cereals), soybeans, sugar beets, tree nuts, and wheat

. Maximum application rates range from 0.0 75 to 0.2 0 lbs a.i./A/yr. This assessment is based on proposed maximum application rates for all uses.

One end

- use formulation of alpha

- cypermethrin is proposed for registration in the United States. The proposed label include s a statement that alpha

- cype rmethrin may be mixed with other products approved for use on the proposed crops, including racemic and zeta

- cypermethrin. This risk assessment applies to the proposed end

- use formulation of alpha

- cypermethrin only and is not applicable if the formulation is used in conjunction with the other cypermethrins.

M ajor transformation products resulting from the environmental degradation of alpha

cypermethrin are 3

- (2,2

- dichloroethenyl)

- 2,2

- dimethylcyclopropane carboxylic acid (DCVA)

and 3

- phenoxybenzaldehyde, which degrades further to 3

- phenoxybenzoic acid (3

- PBA)

. Based on the assumption that cleavage of the ester bond in the parent compound results in biologically inactive degradates, these compounds are not expected to pose greater toxicity to non

- target- Page 7 of 126

- 

### org anisms; therefore only the parent compound was considered for toxicological concern for both aquatic and terrestrial ecosystems. T his assumption is supported by the results of acute toxicity studies in freshwater fish and invertebrates which indicate that the alpha

- cypermethrin degradate 3

- PBA acid is much less toxic than the parent compound.

1.2. Potential Risks to Non

- target Organisms

The results of this screening

- level assessment on the proposed alpha

- cypermethrin uses indicate

that risk s of adverse effects to non

- target organisms are expected for aquatic animals and

mammals. Indirect effects canno t be precluded for any taxa.

Table 1 .1. Potential Effects to Federally Listed Taxa Associated with Direct or Indirect Effects from the Propos ed New Uses of Alpha

- Cypermethrin.

Listed Taxon Direct Effects Indirect Effects a

Terrestrial and semi

- aquatic plants

- monocots No Yes

Terrestrial and semi

- aquatic plants

- dicots No Yes

Birds No Yes

Terrestrial

- phase amphibians and reptiles No Yes

Mammals Yes Yes Aquatic nonvascular plants No Yes

Aquatic vascular plants No Yes

Freshwater fish Yes Yes Aquatic

- phase amphibians Yes Yes

Freshwater crustaceans Yes Yes

Mollusks Yes Yes

Marine/estuarine fish Yes Yes

Marine/estuarine invertebrates Yes Yes

a until an endangered species assessment is complete, indirect effects to all species cannot be precluded



### 1.3. Conclusions

- Exposure Characterization

Alpha

- cypermethrin is slightly to moderately persistent in environmental conditions based on Goring et al. (1975) , and is considered immobile , lipophilic, and nonvolatile

. Alpha

cypermethrin is moderately persistent in soil

, with half

- lives ranging from 28 to 61 days in

aerobic soil and 53 to 63 days in anaerobic soil. There is no evidence of d egradation via hydrolysis, which was studied across environmental pHs. Laboratory data show that alpha

cypermethrin degraded by aerobic aquatic metabolism with half

- lives ranging from 9 to 10 days. A potentially major route of degradation in shallow, cle ar waters ( e.g., applications to flooded rice paddies) may be aqueous photolysis (environmental half

- life of 36 days )

. Alpha

cypermethrin has the potential to bioconcentrate in aquatic food webs.

.

Aquatic exposure estimates are based on the exposure of the parent compound alpha

cypermethrin only

. Major transformation products were reported to be less toxic than the parent (see discussion above in Section 1.1). T herefore, conservative aquatic exposure estimates were generated using environmental half

- live s for the parent only

.- Page 8 of 126

- 

### Aquatic exposure was estimated for all uses of alpha

- cypermethrin. Modeling runs were combined into common crop

- use categories (e.g., brassica vegetables)

. These uses result in the maximum exposure for each type of application method. Therefore, they provide conservative estimates of exposure for other proposed uses with lower application rates and similar application methods that were not specifically modeled. The range of all proposed uses are listed

in Table 3.1. Aquatic exposure estimates are presented in Tables 3. 8

- 3. 10

.

Te rrestrial exposure estimates are based on the residue levels of alpha

- cypermethrin on short grass, tall grass, broadleaf plants, small insects, fruits, pods, seeds, and large ins ects for all proposed uses of alpha

- cypermethrin. Terrestrial exposure estimates are presented in Tables

3.1 1

- 3.1 3

.

1.4

. Conclusions

- Effects Characterization

For spray applications of alpha

- cypermethrin, there is acute risk to all (water column

- dwelling

and sediment

- dwelling) aquatic invertebrates and fish, and chronic risk to all (water column

dwelling and sediment

- dwelling) aquatic invertebrates in the water column. Although this compound binds readily to particulate and organic carbon in the water column (average K

oc 

### = 141,700 L/Kg), possibly limiting bioavailability in this media after 24 to 48 hours, the bound residues settle onto the benthos, increasing alpha

- cypermethrin concentrations in the sediment. Alpha

- cypermethrin is e xpected to be relatively stable to breakdown from sunlight (aqueous photolysis half

- life of approximately 36 days and a dark control corrected soil photolysis half

life of over 100 days) and biodegrade slowly with a half

- life of about 2 months in aerobic a nd anaerobic soils. Therefore the sediment compartment may serve as a repository of pesticide

residues that can result in a direct acute and chronic toxic risk concern for benthic and epibenthic aquatic organisms (e.g. early life stage of many invertebrate s and fish, as well as crabs and shrimp) and a potential indirect risk to fish thr o ugh food chain alterations that can affect

freshwater and estuarine fish

.

A cute and chronic risk to avian species is not expected for spray applications of alpha

cypermeth rin. However, exposure of mammals to alpha

- cypermethrin spray applications is expected to result in acute risk to listed species, and chronic risk to listed and non

- listed species.

A qualitative analysis of the available information indicates there may be potential for risk to

listed and non

- listed terrestrial invertebrates, such as honey bees and earthworms.

Tier II studies of the effect of the alpha

- cypermethrin TGAI on vegetative vigor in terrestrial plants were submitted

. The results indicat ed that effects on terrestrial plants are possible at application rates less than the maximum per acre application rate for the p ro posed uses of alpha

cypermethrin. However, due to uncertainties associated with the study this data is not appropriate

for use in ris k assessment. This is identified as a data gap.- Page 9 of 126

- 

### 2

. Problem Formulation

The purpose of problem formulation is to provide the foundation for the environmental fate and ecological risk assessment for the registration of the new chemical alpha

- cypermethrin

, ( BAS

310 40 I ; (R)

- cyano(3

- phenoxyphenyl)methyl (1S,3S)

- rel

- 3

- (2,2

- dichloroethenyl)

- 2,2

- dimethylcyclopropanecarboxylate ; CAS#: 67375

- 30

- 8 ; PC code: 209600 ). The problem

formulation sets the objectives for the risk assessment, establishes a risk hypothesis and conceptual model depicting potential risk

, and provides a plan for analyzing the data and characterizing the risk associated with the proposed use of alpha

- cypermethrin ( USEPA, 1998 ).

2.1

. Nature of Regulatory Action

T he U.S

. Environment al Protection Agency (EPA or the Agency) is required under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) to ensure that the newly proposed use of alpha

- cypermethrin as an insecticide does not have the potential to cause unreasonable adver se effects to the environment. In addition to non

- target animals and plants, potential effects to listed species ( i.e. , species on the Federal list of endangered and threatened wildlife and plants) and their designated critical habitat are also considered under the Endangered Species Act (ESA)

in order to ensure that the registration of alpha

- cypermethrin is not likely to jeopardize the

continued existence of listed species or adversely modify their critical habitat. In order to meet the requirements of F IFRA and the ESA, this assessment follows EPA guidance on conducting ecological risk assessments ( USEPA, 1998 ) and Office of Pesticide Program’s Overview Document, which contains guidance for assessing pesticide risks to non

- target and listed organisms (US EPA, 2004)

.

The end result of the EPA pesticide registration process ( i.e. , the FIFRA regulatory action) is an approved ( or disapproved ) product label. The label is a legal document that stipulates how and where a given pesticide may be used. Product labels (also known as end

- use labels) describe the formulation type ( e.g. , liquid or granular), acceptable methods of application, approved use sites, and any restrictions on how applications may be conducted. Therefore, the use, or potential use, described by the pesticide’s labels is considered “the action” being assessed. This assessment was prepared to support evaluation of the proposed new chemical registration of alpha

cypermethrin

.

2.2

. Stressor Source and Distribution

2.2. 1. Nature of Chemical Stressor

BASF is seeking registration for the use of the new chemical insecticide alpha

- cypermethrin ( BAS 310 40 I ), R)

- cyano( 3

- phenoxyphenyl)methyl (1S,3S)

- rel

- 3

- (2,2

- dichloroethenyl)

- 2,2

- dimethylcyclopropanecarboxylate

. According to BASF

, alpha

- cypermethrin is a Type II synthetic pyrethroid. The pyrethroids ( including alpha

- cypermethrin ) share similar modes of action, and are considered axonic poisons that affect both the peripheral and central nervous system. It is now well established that severe neurological symptoms of poisoning with- Page 10 of 126

- 

### pyrethroids in mammals and insects are the result of modification of sodium (Na + 

### ) channel activity (cellular pores through which sodium ions are permitted to enter the axon to cause excitation) (Matsumura 1985). Advanced electrophysiological experiments using a voltage clamp and a patch clamp, together w ith ligand

- binding and ionic flux experiments, have unveiled unique actions of pyrethroids that keep the Na + 

### channel in the open state for an extremely long period, sometimes as long as several seconds. This modification of Na + 

### channel properties leads

to hyperactivity of the nervous system. This action leads to spontaneous depolarizations, augmented neurotransmitter secretion rate and neuromuscular block, which ultimately results in paralysis of the insect. Pyrethroids have also been shown to suppress gam ma

- aminobutyric acid ( GABA ) and glutamate receptor

- channel complexes and voltage

- activated calcium (Ca 2+ 

### ) channels, but the toxicological significance of these actions is uncertain.

Relative to physiological responses, researchers have designated two ty pes of pyrethroids, Type I (e.g., pyrethrins, S

- bioallethrin, resmethrin, permethrin) and Type II (e.g., the cypermethrins, deltamethrin, fenvalerate). Alpha

- cypermethrin is classified as Type II synthetic pyrethroid, with a cyano group at the α

- carbon po sition of the alcohol moiety, and is considered a third generation pyrethroid, that is, more light

- stable and persistent in the environment than early pyrethroids like allethrin, phenothrin (also commonly known as sumithrin) and resmethrin. Alpha

- cypermet hrin

ha s two optically active centers and is composed of 2 isomers, and like all pyrethroids, is a contact poison that can quickly penetrate the nervous system and have an effective “knockdown” action (induction of temporary paralysis) for most flying inse cts.

Alpha

- cypermethrin is formulated as an emulsifiable concentrate (BAS 310 40 I EC®) It is applied to alfalfa, brassica vegetables, citrus fruits, corn (field, pop, seed and sweet), cotton, cucurbits, fruiting vegetables, leafy vegetables, legume v egetables, rice (grain and straw), root and tuber vegetables, sorghum (and other cereals), soybeans, sugar beets, tree nuts, and wheat.

The proposed maximum annual application rates are on citrus fruits

. Citrus fruits may be treated

with a single maximum application rate of 0.025 lbs a.i./A with a 14

- day reapplication interval

for a total seasonal mass applied of 0.20 lbs /A (i.e., 8 applications)

. Other crop treatments are proposed at l ow er seasonal rates a s discussed in Section 3.1.

2.2.2

. Overview of Pesticide Usage

Usage data are not available for alpha

- cypermethrin because it is a new active ingredient proposed for use in the United States

.

Alpha

- cypermethrin is proposed as a Restricted Use Pesticide (RUP) for agricultural uses

because of its acut e toxicity to aquatic organisms. For agricultural products, application methods include aerial, air blast, ground spray, or chemigation. T he following labeling statements appear on the proposed label to avoid spray drift and contam ination of aquatic envi ronments , and were

used to refine the surface water exposure assessment (described in Section 3.2.2.1 ) where appropriate :

BUFFER ZONE REQUIREMENTS for AGRICULTURAL CROPS- Page 11 of 126

- 

### • Vegetative Buffer Strip :

o Construct and maintain a minimum 10

- foot

- wide vegetative filter strip of grass o r other permanent vegetation between the field edge and down gradient aquatic habitat (such as, but not limited to, lakes; reservoirs; rivers; permanent streams; marshes or natural ponds; estuaries; and commercial fish farm ponds).

o O nly apply products containing alpha

- cypermethrin onto fields where a maintained vegetative buffer strip of at least 10 feet exists between the field and down gradient aquatic habitat.

• Buffer Zone for Ground Application (groundboom, overhead chemigation, or airblast):

o Do not apply within 25 feet of aquatic habitats (such as but not limited to, lakes, reservoirs, rivers, streams, marshes, ponds, estuaries, and commercial fish ponds).

• Buffer Zone for ULV Aerial Application:

o Do not apply within 450 feet of aqua tic habitats (such as but not limited to, lakes, reservoirs, rivers, streams, marshes, ponds, estuaries, and commercial fish ponds).

• Buffer Zone for Non

- ULV Aerial Application:

o Do not apply within 150 feet of aquatic habitats (such as but not limited to, l akes, reservoirs, rivers, streams, marshes, ponds, estuaries, and commercial fish ponds).

SPRAY DRIFT MANAGEMENT for AGRICULTURAL CROPS

• Wind Direction and Speed:

o Only apply this product if the wind direction favors on

- target deposition.

o Do not apply when the wind velocity exceed s 15 mph.

• Temperature Inversion

o Do not make aerial or ground applications into temperature inversions.

o Inversions are characterized by stable air and increasing temperatures with height above the ground. Mist or fog may indicat e the presence of an inversion in humid areas. The applicator may detect the presence of an inversion by producing smoke and observing a smoke layer near the ground surface.

• Droplet Size:

o Use only Medium or coarser spray nozzles (for ground and non

- ULV aer ial application) according to ASAE (S572) definition for standard nozzles. In conditions of low humidity and high temperatures, applicators should use a coarser droplet size.

• Additional Requirements for Ground Applications:

o Wind speed must be measured adjacent to the application site on the upwind side, immediately prior to application.

o For ground boom applications, apply using a nozzle height of no more than 4 feet above the ground or crop canopy.

o For airblast applications, turn off outward pointing no zzles at row ends and when spraying the outer two rows. To minimize spray loss over the top in orchard applications, spray must be directed into the canopy.

• Additional Requirements for Aerial Applications:- Page 12 of 126

- 

### o The spray boom should be mounted on the aircraft a s to minimize drift caused by wingtip or rotor vortices. The minimum practical boom length should be used and must not exceed 75% of the wing span or 80% rotor diameter.

o Flight speed and nozzle orientation must be considered in determining droplet

size.

o Sp ray must be released at the lowest height consistent with pest control and flight safety. Do not release spray at a height greater than 10 feet above the crop canopy unless a greater height is required for aircraft safety.

o When applications are made with a cross

- wind, the swath will be displaced downwind. The applicator must compensate for this displacement at the downwind edge of the application area by adjusting the path of the aircraft upwind.

Alpha

- c ypermethrin is toxic to fish, aquatic invertebrates and beneficial insects. The following

Envir onmental Hazards statements appear on the proposed label:

ENVIRONMENTAL HAZARD STATEMENTS

• This pesticide is extremely toxic to fish, aquatic invertebrates, oysters and shrimp. Do not apply directly to water, o r to areas where surface water is present or to intertidal areas below the mean water mark. Do not apply when weather conditions favor drift from treated areas. Drift and runoff from treated areas may be hazardous to aquatic organisms in neighboring areas. Do not contaminate water when disposing of equipment wash

waters.

• This product is highly toxic to bees exposed to direct treatment on blooming crops or weeds. Do not apply this product or allow it to drift to blooming crops or weeds while

bees are active ly visiting the treatment area.

In addition , t he proposed label contains the following language: “DO NOT apply more than the combined maximum seasonal total for cypermethrin (including alpha

- cypermethrin, zeta

cypermethrin, and any other products containing cypermethrin) products.” It is unclear what the “combined maximum seasonal total” is for cyperm ethrin and the interpretation is vague which is confusing for the end user.

2.3

. Receptors

2.3.1

. Aquatic and Terrestrial Effects

In ecological risk assessment, a receptor is a biological entity that is exposed to a stressor ( USEPA, 1998 ). Consistent with the process described in the Overview Document (USEP A

, 2004 ), this r isk assessment uses a surrogate species approach in its evaluation of alpha

cypermethrin . Toxic ity data generated using surrogate test species, which are intended to be representative of broad taxonomic groups, are used to infer potential ef fects on a variety of species (r eceptors) included under these broader taxonomic groupings. Table 2.1 provides the general taxonomic groups and surrogate species tested to evaluat e potential ecological effects of- Page 13 of 126

- 

### alpha

- cypermethrin to broad classes of non

- target organisms

. Within each of these taxonomic groups, a measure of effect is selected from among the available test data.

Ta ble 2.1. Taxonomic Groups and Test Species Evaluated for Assessing Potential Ecological Effects of Alpha

- cypermethrin

. Taxonomic Group Typical Species

Birds 1 Mallard duck ( Anas platyrhynchos ) Bobwhite quail ( Colinus virginianus )

Mammals Norway rat ( Ratus norvegicus )

In vertebrates Honey bee ( Apis mellifera L. )

Freshwater fish 2 Bluegill sunfish ( Lepomis macrochirus ) Rainbow trout ( Oncorhynchus mykiss ) Fathead minnow ( Pimephales promelas )

Freshwater invertebrates Water flea ( Daphnia magna ) Midge ( Chironomus riparius )

Estuarine/marine fish Sheepshead minnow ( Cyprinodon variegatus )

Estuarine/marine invertebrates Mysid ( Americamysis bahia ) Eastern oyster ( Crassostrea virginica ) Terrestrial plants 3 Monocots

– Crop species, such as corn ( Zea mays )

Dicots

– Crop Species, such as soybean ( Glycine max ) Aquatic plants and algae 4 Duckweed ( Lemna gibba ) Freshwater Algae ( Pseudokirchneriella subcapita ta )

1 Birds represent surrogates for terrestrial

- phase amphibians and reptiles.

2 Freshwater fish may be surrogates for aquatic

- phase amphibians.

3 Four species of two families of monocots, of which one is corn; six species of at least four dicot families, of which one is soybeans.

4 Four species of non

- vascular algae including a freshwater green algae, a cyanobacterium, a marine diatom, and a freshwater diatom.



### 2.3. 2. Ecosystems Potentially at Risk

The ecosystems potentially 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. However, in general terms, terrestrial ecosystems potentially at risk could include the treated field and immediately adjacent areas t hat may receive drift or runoff. Areas adjacent to the treated field could include cultivated fields, fencerows and hedgerows, meadows, fallow fields or grasslands, woodlands, riparian habitats, and other uncultivated areas. Current label

directions for alpha

- cypermethrin require vegetative buffer strips and impose limitations to reduce the potential for spray drift to impact areas adjacent to the treated field. However, due to the potential persistence of alpha

- cypermethrin under certain circumstances, i t is expected to

drift and/ or runoff from application to food crops, resulting in possible exposure to aquatic

ecosystems. Aquatic ecosystems potentially at risk include water bodies adjacent to or

downstream from use site s, and might include impounded bo dies such as ponds, lakes and reservoirs, or flowing waterways such as streams or rivers including all adjacent off

- channel habitats that are permanently or intermittently connected to flowing waters. For uses in coastal areas, aquatic habitat also include s marine ecosystems, including estuaries, embayments, and

near

- shore environments such as tidal marshes

.

2.4

. Assessment Endpoints- Page 14 of 126

- 

### 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 characteristics ( USEPA, 1998 ). For alpha

- cypermethrin , ecological entities of potential concern in clude the following: birds , amphibians, reptiles, mammals, freshwater fish and invertebrates, estuarine/marine fish and invertebrates, terrestrial plants, non

- target terrestrial invertebrates , and aquatic vascular and non

- vascular plants. The attributes for each of these entities may include growth, survival, and reproduction ( Table 2. 2 in Section 2.6. 4 ).

2.5 . Conceptual Model

For a pesticide to pose an ecological risk, it must reach ecological receptors in biologically 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 ecol ogical pathway to be complete, it must have a source, a release mechanism, an environmental transport me chanism , and a feasible route of exposure.

The conceptual model is intended to provide a written description and visual representation of anticipated r elationships between alpha

- cypermethrin

, potential routes of exposure, and the predicted effects for the assessment endpoint s

. The conceptual model consists of two major components: risk hypotheses and a conceptual diagram ( USEPA, 1998 ).

2.5. 1. Risk Hyp otheses

For alpha

- cypermethrin , the fol lowing generic ecological risk hypothes i s i s being employed for

this screening

- level risk assessment:

Alpha

- cypermethrin , when used outdoors in accordance with registered labels, have the potential to lead to off

- site movement of the compound via agricultura l, , spray drift, and eroded soil leading to exposure of nontarget plants and animals

.

Based on information on the environmental fate, mode of action, direct toxicity and potential indirect effects, EFED assumes that the proposed uses of alpha

- cypermethrin

ha ve the potential to cause reduced survival, growth, and reproduction to non

- target

t errestrial and/ or aquatic animals and plants.

2.5.2

. C onceptual Diagram

The conceptual model is a graphic al representation of predicted relationships between ecological

receptor s , both listed (threatened and endangered) and non

- listed, and the stressors to which they may be exposed. A conceptual model specifies potential routes of exposure, biological receptor types, and effects endpoints of potential concern. The conceptual mode l for terrestrial organisms exposed to alpha

- cypermethrin is presented in Figure s 2.1 , while the conceptual model for aquatic organisms exposed to alpha

- cypermethrin is presented in Figure 2.2

.

Under the possible uses of alpha

- cypermethrin , the sources an d mechanisms of release of the- Page 15 of 126

- 

### compounds are from ground or aerial spray , chemigation, or ULV applications. Surface runoff from the areas of application is assumed to depend on factors such as topography, irrigation, and rainfall events. Direct depositio n may result in contamination of food items that may be consumed by terrestrial organisms. Spray drift results in contaminated adjacent areas, including bodies of water. Leaching to groundwater is not considered an important source because alpha

cypermet hrin , like many other pyrethroids, show s low mobility in a variety of soils. Alpha

cypermethrin appear s to have a low potential for volatilization, with a low vapor pressure and Henry’s Law Constants. The low vapor pressure (~10 - 9 

### torr) and relatively low Henry’s Law constant (~10 - 7 

### atm/m 3



### - mol), and its binding capacity, suggest that the potential for atmospheric transport for alpha

- cypermethrin is relatively low and that this source of the chemical is of low importance, compared to spray drift, runoff and / or direct contact after application.

T he major point of exposure for aquatic receptors is through direct contact with the water column, sediment, and pore water (gill/ integument) contaminated with spray drift (from spray application) and/or runoff and flow ( e.g. , piped storm drains) from treated areas. Indirect effects to aquatic organisms (both fish and aquatic invertebrates) can also occur through impact to various food chains. The representative aquatic receptors are certain freshwater and estuarin e/ marine fish, invertebrates, and, in certain cases, aquatic plants. For terrestrial receptors, t he major point of exposure is consumption of food contaminated with residues such as grass, foliage, and small insects. For plants, the point of exposure is direct contact or root uptake. The representative terrestrial receptors are mammals, birds and terrestrial plants. The attribute changes used to assess risk to terrestrial receptors depend on the type of test ( e.g. , reduced survival, growth, or reproduc tion for animals and seedling emergence and vegetative vigor for plants). It should be noted, that these species do not cover all the possible species in the animal and plant kingdoms; certain taxa are considered as surrogates for other taxa. For example , fish are considered surrogates for aquatic phase amphibians.

This conceptual model also shows information about the potential for biomagnification for alpha

- cypermethrin (see piscivorous birds and mammals in Fig. 2.2 ). The reported value of log

octanol / water partition coefficient of 6.4 suggests that alpha

- cypermethrin has the potential to bioaccumulate in aquatic organisms assuming that chemical metabolism is negligible. Maximum

BCFs for alpha

- cypermethrin are 161x for edible tissue, 883x for viscera , and 448x for whole fish. Depuration appeared to be moderately slow, with ~10

- 15% of the initial residues remaining after 21 days. Thus, it appears that there is potential for bioaccumulation/ bioconcentration in aquatic organisms and biomagnification in terrestrial organisms. However, potential for bioaccumulation/bioconcentration may be tempered by the sensitivity of aquatic animals to alph

cypermethrin

.

Alpha

- cyperm e thrin has a solubility of 4.0 ppb and a very high K OW 

### . These properties suggest

that the chemical could partition to the sediment and particulate s suspended in bodies of water. Alpha

- cypermethrin is likely to concentrate in the sediments, especially after repeated exposures (applications), where it will likely persist. Such sediments cou ld serve as repositories of the chemicals for extended periods of time and could potentially be toxic to sediment dwelling organisms, affecting the food chain. These issues will also be assessed in the risk assessment.- Page 16 of 126

- 

### Figure 2.1. Conceptual model for alpha

- cypermethrin effects on terrestrial organisms.



### Stressor

Source

Attribute Change Alpha

- cypermethrin applied to agricultural use sites

Direct application Spray drift

Terrestrial

vertebrates * Terrestrial

i nvert ebrate s

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 , fruit, seeds (trees, shrubs) Runoff

Terrestrial

v ertebrates 

### Exposure Media & Receptors Soil

Ingestion Ingestion Ingestion Dermal uptake/Ingestion Atmospheric transport

Root uptake/contact

Wet/dry deposition

Ingestion Leaching to
Groundwater Irrigation

water

* Drinking water and inhalation exposure pathways for terrestrial vertebrates are not expexted to be of concern.- Page 17 of 126

- 

### Figure 2.2 . Conceptual model for alpha

- cypermethrin effects on aquatic organisms.



### 2.6 . Analysis Plan

2.6.1

. Residues of Concern

M ajor transformation products resulting from the environmental degradation of alpha

cypermethrin are 3

- (2,2

- dichloroethenyl)

- 2,2

- dimethylcyclopropane carboxylic acid (DCVA)

and 3

- phenoxybenzaldehyde, which degrades further to 3

- phenoxybenzoic acid (3

- PBA)

. Based on the assumption that cleavage of the ester bond in the parent compound results in biologically inactive degradates, these compounds are not expected to pose greater toxicity to non

- target organisms; therefore only the parent compounds were consider ed for toxicological concern for both aquatic and terrestrial ecosystems. T his assumption is supported by the results of acute toxicity studies in freshwater fish and invertebrates which indicate that the alpha

- cypermethrin degradate 3

- PBA is much less to xic than the parent compound. Therefore, alpha

- cypermethrin alone is the residue of concern in this assessment. **Considered a minor route of exposure 

## Stressor

Source

Receptors

Attribute Change Alpha

- cypermethrin applied to agricultural use site s

Spray drift

Aquatic animals

Invertebrates

Vertebrates
Piscivorous mammals

and birds**

Individual organisms

Reduced survival (2) 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

productivity

Reduced cover Community change
Modification of PCEs related to

habitat Surface water/
Sediment Runoff

Aquatic Animals

Invertebrates
Vertebrates 

## Exposure

Media

Uptake/gills or integument

Ingestion Ingestion Atmospheric transport

Wet/dry deposition Soil Leaching to
Groundwater

Uptake/gills or integument

Aquatic Plants

Non

- vascular
Vascular Uptake/cell, roots, leaves Riparian plants

terrestrial

exposure pathways; see

Figure 6.1b Flow- Page 18 of 126

- 

### 2.6.2. Preliminary Identification of Data Gaps and Uncertainties

For the purposes of risk assessment

, the submitted environmental fate and ecotoxicity data for alpha

- cypermethrin are inadequate for risk assessment

. However, a s discussed previously, data are bridged for the databases of the racemic (cypermethrin) and the previously registered enriched mixtures (zeta

- cypermethrin). BASF su bmitted a bridging strategy for the use of

environmental fate and ecotoxicity data for racemic and zeta

- cypermethrin in the risk assessment for the new product, alpha

- cypermethrin ; the Agency found this strategy acceptable ( Appendix

A ) . T herefore the envir onmental fate and ecotoxicity database for alpha

- cypermethrin is bridged

across the isometric mixture s. A complete summary of the submitted environmental fate and ecotoxicity data is included in USEPA, 200 2

. Additional data submitted after 2007 are include d

in the environmental database for racemic and zeta

- cypermethrin. Data submitted using alpha

cypermethrin as the test matrial are summarized in Appendix B

.

2.6. 3

. Evaluation of Multiple Active Ingredients and Mixtures

The Agency does not routinely incl ude in its risk assessments an evaluation of mixtures of active ingredients, either those mixtures of multiple active ingredients in product formulations or those in the applicator’s tank. In the case of the product formulations of active ingredients (tha t is, a registered product containing more than one active ingredient), each active ingredient is subject to an individual risk assessment for regulatory decision regarding the active ingredient on a particular use site. If effects data are available for a formulated product containing more than one active ingredient, they may be used qualitatively or quantitatively in accordance with the Agency’s Overview Document and the Services’ Evaluation Memorandum (U.S. EPA 2004; U.S. FWS/NMFS 2004). However, the proposed end

- use product for the new chemical alpha

cypermethrin is a s a single active ingredient formulation.

2.6. 4

. Measures of Exposure

Measures of expo sure are based on aquatic and terrestrial models that estimate environmental

concentrations of alpha

- cypermethrin using labeled application rates and methods. For aquatic

exposure t he Tier II model Pesticide Root Zone Mo del (PRZM v3.12.2; May 12, 2005 ) li nked with EXposure Analysis Modeling System (EXAMS v2.98.4.6; Apr. 25, 2005) via the PRZM/EXAMS model shell (PE v5.0, Nov. 15, 2006), i.e. , PRZM/EXAMS) and the Tier I Rice Model (v1.0, May 8, 2007) w ere used to estimate screening

- level exposure concentrati ons in aquatic environments

. The measure of exposure for aquatic species in surface water bodies receiving runoff and/or spray drift is a return frequency of 1

- in

- 10 years of the estimated

environmental concentration s (EEC), based on 30

- year simulations. The maximum 1

- in

- 10 year return frequency concentration is used for estimating acute exposure s to aquatic organisms (plants and animals) ; the 1

- in

- 10 year 21

- day mean concentration is used for assessing aquatic invertebrate chronic expos ure; and the 1

- in

- 10 year 60

- day mean concentration is used for assessing chronic exposure for fish (and aquatic

- phase amphibians for which fish serve as

surrogates ). E xposure to benthic organisms from sediment concentrations in water bodies was

assessed ; pore

- water 1

- in

- 10 year EECs were calculated for maximum use patterns

.

Terrestrial exposure estimates for avian and mammalian risk assessments were derived using the- Page 19 of 126

- 

### T

- REX model ( version 1.4.1, 10/08/2008 ). The assumption of the model is that mammals and

birds may be exposed via their consumption of treated seeds on or immediately adjacent to the site of application.

The S creening I mbibition P rogram (SIP v.1.0) and Screening Tool for Inhalation Risk (STIR v.1.0) were used to calculate upper bound estimate s of wildlife exposure via drinking water and inhalation, respectively, using alpha

- cypermethrin’s solu bility or vapor pressure, avian and mammalian toxicity endpoints

.

The KABAM (K ow

- based bioaccumulation) model ve rsion 1.0 (documented at http://www.epa.gov/oppefed1/models/water/kabam/kabam_user_guide.html ) was used to estimate potential bioaccumulation of hydrophobic organic pesticid es in freshwater aquatic ecostystems and risks to mammals and birds consuming aquatic organisms which have bioaccumulated these pesticides.

2.6. 5

. Measures of Effect

Measures of effect are obtained from a suite of registrant

- submitted guideline studies that were conducted with a limited number of surrogate test species ( Table 2.1)

. No additional ecotoxicity

data on alpha

- cypermethrin were located, based on an August 2 011 query of the open literature

in the public ally available version of the ECOTOX database ( http://cfpub.epa.gov/ecotox/ ).

The acute measures of effect used in this baseline assessment are the LD 50 

### ( median Lethal Dose),

LC 50 

### ( median Lethal Concentration) or EC 50 

### ( median Effects Concentration). These are measures of acute toxicity which result in 50% of the respective effect in tested organisms. The endpoints for chronic mea sures of exposure are the no observed adverse effect concentration ( NOAEC ) and the no observed adverse effect level ( NOAEL ) . Toxicity studies were submitted for freshwater fish and invertebrates, estuarine/marine fish and invertebrates, aquatic plants, birds, mammals

, bees , and other terrestrial invertebrates . The endpoints us ed for risk

characterization are derived from studies which underwent review and were classified as “acceptable” (conducted under guideline conditions and considered to be scientifically valid) or “supplemental” (conditions deviated from guidelines but the results are considered to be scientifically valid).

Table 2. 2 lists the measures of environmental exposure and ecological effects used to assess the potential risks of alpha

- cypermethrin to non

- target organisms. The methods used to assess the

risk are consistent with those outlined in the document “Overview of the Ecological Risk Assessment Process in the Office of Pesticide Programs” (USEPA, 2004).- Page 20 of 126

- 

### Table 2.2. Measures of Exposure and Measures of Effect Used in Assessing Potential Risks

Associated wi th the Proposed Use s of Alpha

- Cypermethrin

.
Assessment Endpoint Surrogate Species and Measures of Ecological Effect 1 Measures of Exposure

Birds 2 Survival Lowest acute LD 50 (single oral dose test)

and LC 50 (subacute dietary test) Upper

- bound residues on

food items

Reproduction

and Growth Lowest NOAEC (21

- week reproduction test)

Mammals Survival Lowest acute LD 50 (single oral dose test)

Reproduction

and Growth Lowest NOAEC (2

- generation reproduction test)

Aquatic Animals ( F ish and

invertebrate s) 3 Survival Lowest tested LC 50 or EC 50 (acute toxicity test) Peak EEC s 4

Reproduction

and Growth Lowest NOAEC ( early life

- stage or full

life

- cycle test s ) 21

- day EECs for invertebrates

and 60

- day EECs for fish 4

Terrestrial plants 5 Survival and growth Lowest EC 25 (for non

- listed plants) and

corres ponding NOAEC (for listed plants)

(endpoints derived for monocots and dicots from seedling emergence and vegetative vigor studies) Estimates of runoff and spray

drift to non

- target areas

Insects 6 Survival (not quantitatively

assessed) Lowest h oneybee LD 50 (acute contact test)

Lowest Earthworm LC 50 Maximum application rate for honeybees and estimates of

soil concentrations for

earthworms

Aquatic plants (vascular

and non

- vascular) Survival and growth Lowest EC 50 (for non

- listed plants) and corresponding NOAEC or EC 05 (for listed plants) Peak EEC s 4

1 The most sensitive species tested within taxonomic groups is used for screening

- level risk assessments.

2 Birds represent surrogates for terrestrial

- phase amphibians and reptiles.

3 Freshwater fish represent surrogates for aquatic

- phase amphibians

. 4 Aquatic EECs are based on modeling described in Section 3.2.2.1

. 5 Four species of two families of monocots

- one is corn, six species of at least four dicot families, of which one is soybeans.

6 Risk to terrestrial invertebrates from alpha

- cypermethrin use is not evaluated, rather the potential hazard to honey bees and earthworms (i.e. the available data) are qualitatively assessed.



### 2.6. 6

. Integration of Exposure and Effects

E xposure and toxicity data are integrated in order to evaluate the risks of adverse ecological

effects on non

- target species. For the screening

- level risk assessment of alpha

- cypermethrin , the

deterministic risk quoti ent (RQ) method is used to compare estimated exposure concentrations

with measured toxicity values. The RQ method involves dividing point estimates of

environmental concentrations by acute and chronic toxicity values. The resulting unitless RQs

are then compared to the Agency’s L evels of C oncern (LOC ) (USEPA

, 2004) ( Table 2.3 ). These criteria are used to indicate when applications of alpha

- cypermethrin , as directed on the proposed label s , have the potential to cause adverse e ffects to listed and non

- list ed non

- target organisms.- Page 21 of 126

- 

### Table 2.3. Agency Risk Quotient (RQ) Metrics and Levels of Concern (LOC) Per Risk

Class.

RISK CLASS RISK DESCRIPTION RQ LOC

Aquatic Animals (fish and invertebrates)

Acute Potential for effects to non

- listed animals from acute

exposures Peak EEC/LC 50 1 0.5

Acute

Restricted Use Potential for effects to animals from acute exposures Risks may be mitigated through restricted use classification Peak EEC/LC 50 1 0.1

Acute Listed Species Listed species may be potentially affected by acute

exposures Peak EEC/LC 50 1 0.05

Chronic Potential for effects to non

- listed and listed animals from chronic exposures 60

- day EEC/NOAEC (fish) 1 21

- day EEC/NOAEC (invertebrates)

Aquatic Plants

Non

- Listed Potential for effects to non

- listed plants from exposures Peak EEC/LC 50 1 1

Listed Potential for effects to listed plants from exposures Peak EEC/NOAEC 1

Terrestrial Animals (mammals and birds)

Acute Potential for effects to non

- listed animals from acute

exposures EEC 2 /LC 50 (Dietary) 0.5 EEC/LD 50 (Dose)

Acute

Restricted Use Potential for effects to animals from acute exposures Risks may be mitigated through restricted use classification EEC 2 /LC 50 (Dietary) 0.2 EEC/LD 50 (Dose)

Acute Listed Species Listed species may be potentially affected by acute

exposures EEC 2 /LC 50 (Dietary) 0.1 EEC/LD 50 (Dose)

Chronic Potential for effects to non

- listed and listed animals from chronic exposures EEC 2 /NOAEC 1

Terrestrial and Semi

- Aquatic Plants

Non

- Listed Potential for effects to non

- target, non

- listed plants from

exposures EEC/ EC 25 1

Listed Plant Potential for effects to non

- target, listed plants from

exposures EEC/ NOAEC 1 EEC/ EC 05

1 LC 50 or EC 50

. 2 Based on upper bound seeding rates

.



### 3 . Analysis

3.1

. Use Characterization

Alpha

- cypermethrin is proposed for use as an emulsifiable concentrate . Proposed application methods for alpha

- cypermethrin include, aerial, air blast, ground spray, and chemigation. Proposed m aximum application rates and use patterns lis ted by use according to the proposed

labels are provided in Table 3.1

.

Table 3.1

. Proposed Maximum Use Patterns of Alpha

- Cypermethrin

. Crop/Use Maximum Maximum Application Maximum Method of- Page 2 2 of 126

- Application

Rate (lbs a.i./A) Number of Applications Interval (days) Yearly Application (lbs a.i./A/yr) Application

Alfalfa 0.025 3 7 0.075 Ground or air Brassica vegetables 0.025 6 7 0.15 Ground or air

Citrus fruits 0.025 8 14 0.20 Ground or air

Corn (field, pop, seed) 0.025 4 3 0.10 Ground, air,

banded or

infurrow
Corn (sweet) 0.025 6 3 0.15 Ground or air

Cotton 0.0 25 6 3 0.15 Ground, air,

banded or

infurrow

Cucurbits 0.025 6 7 0.15 Ground or air Fruiting vegetables 0.025 6 7 0.15 Ground or air Leafy vegetables 0.025 6 7 0.15 Ground or air Legume vegetables 0.025 6 5 0.15 Ground or air Rice (grain, straw) 0.025 4 7 0.10 Ground or air

Root and tuber vegetables (except sugar beet) 0.025 6 4 0.15 Ground or air

Sorghum (and other cereals) 0.025 5 10 0.125 Ground or air

Soybeans 0.025 6 7 0.15 Ground or air Sugar beets 0.025 6 7 0.15 Ground or air

Tree nuts 0.025 5 7 0.125 Ground or air

Wheat 0.025 5 14 0.125 Ground or air



### 3.2. Exposure Characterization

3.2.1. Environmental Fate and Transport Characterization

The general physical/chemical properties of alpha

- cypermethrin are summarized in Table 3.2

. These data represent cypermethrins (i.e., data in most cases were generated for the racemic mixture, but are bridged across the enriched isomers). Where appropriate , data generated using the enriched alpha

- cypermethrin as the test material, are identified. Data specific to alpha

cypermethrin were used to fulfill environmental fate and transport data requirements, and where there are no data specific for alpha, data w ere bridged from the database for the cypermethrins (zeta and racemic cypermethrin). Environmental fate and transport properties of alpha

cypermethrin are characterized in further detail in the following sections , and data specific to alpha

- cypermethrin ar e noted

. The Agency’s understanding of these properties is limited by the

available dataset. Data submitted using alpha

- cypermethrin as the test material is summarized in Appendix B

.

Table 3.2 General Physical and Chemical Properties of Alpha

- Cypermethrin

Parameter Value Reference

PC code 209600

--

CAS No. 67375

- 30

- 8

--- Page 23 of 126

- Parameter Value Reference

Structure

--

Chemical name (IUPAC) racemate comprising ( R )

- α

- cyano

- 3

- phenoxybenzyl (1 S ,3 S )

- 3

- (2,2

- dichlorovinyl)

- 2,2

- dimethylcyclopropanecarboxylate and ( S )

- α

- cyano

- 3

- phenoxybenzyl (1 R ,3 R )

- 3

- (2,2

- dichlorovinyl)

- 2,2

- dimethylcyclopropanecarboxylate

or racemate comprising ( R )

- α

- cyano

- 3

- phenoxybenzyl (1 S )

- cis

- 3

- (2,2

- dichlorovinyl)

- 2,2

- dimethylcyclopropanecarboxylate and ( S )

- α

- cyano

- 3

- phenoxybenzyl (1 R )

- cis

- 3

- (2,2

- dichlorovinyl)

- 2,2

- dimethylcyclopropanecarboxylate --

Chemical name (CAS) ( R )

- cyano(3

- phenoxyphenyl)methyl (1 S ,3 S )

- rel

- 3

- (2,2

- dichloroethenyl)

- 2,2

- dimethylcyclopropanecarboxylate --

Common name Alpha

- Cypermethrin (BAS 310 40 I)

--

Chemical formula C 22 H 19 CI 2 N O 3 -- Molecular weight 416.3 g/mol USEPA 2006b

Water solubility (20oC, pH 7) 4.0x10
- 3 mg/L Laskowski (2002)

Vapor pressure (25oC) 2.5x10

- 9 mm Hg Laskowski (2002)

Henry's law constant 3.4x10
- 7 atm

- m 3 /mol Laskowski (2002)

Octanol

- water partitioning coefficient Log K OW (20oC, pH 7) 6.4 Laskowski (2002)



### Alpha

- cypermethrin has a strong soil adsorption (K

oc 

### = 144,662), based on FAO Soil Mobility

Classification and a tendency to partition to sediment in aquatic systems. The reported log octanol/water partition coefficient value (6.4) suggests that the cypermethrins have the potential to bioaccumulate in aquatic organisms, assuming that chemical metabolism is negligible. The cypermethrins have a high molecular weight of 41 6.3 g/mmol. With a vapor pressure of 2.5x10 - 9


### mm Hg and a limited solubility, the calculated Henry’s Law Constant for the cypermethrins is relativiely low (3.4x10 - 7 

### atm

- m 3 

### /mol). Table 3.2 lists various important physicochemical

characteristics of the chemi cals. A summary of the submitted environmental fate and transport

data is provided in Table 3.3

.

Laboratory studies have indicated that alpha

- cypermethrin degrade s through a combination of

biotic and abiotic reactions and is slightly to moderatley persist ent in the environment , based on Goring et al. (1975) . Under acidic and neutral conditions this compound is relatively stable to hydrolysis , but is readily hydrolyzed under alkaline conditions with a half

- life of approximately 2 days at pH 9. Alpha

- cyper methrin is susceptible to aqueous photo lysis with a half

- li f e of 5 days. Cypermethrins are shown to biodegrade in aerobic and anaerobic soils with half

- lives on- Page 24 of 126

- 

### the order of about 2 months (one month for alpha cypermethrin) and in aerobic and anaerobic aquatic systems with half

- lives on the order of one to two weeks (alpha specific data is of the same range)

. Alpha

- cypermethrin is considered immobile in soils based on the FAO soil mobility

classification (K

oc 

### as high as 144, 662 L/Kg) and its potential to leach into groundwater is low ( USEPA, 2006 a ) . If released to water, alpha

- cypermethrin will rapidly partition to the sediment compartment which acts as an environmental sink for this compound. Alpha

- cypermethrin may

bioconc entrate moderately in fish ( BCF = 448X in whole fish), with moderate depuration. In terrestrial field dissipation studies alpha

- cypermethrin was not very persistent in soils and did not leach (half

- lives 1

- 2 weeks). In supplemental aquatic field dissipat ion studies (zeta

cypermethrin), the chemical appears to persist in the sediment, with reported half

- lives of 126 and 181 days in LA and CA, respectively.

Table 3.3 Environmental Fate Data Summary for Alpha

- Cypermethrin

Property Value / Degradates observed Reference

Hydrolysis half

- life: pH 5 pH 7 pH 9 stable

stable 1.8 (acid labeled) and 2.5 days (alcohol label)

cis/trans

- DCVA (max. 79% at 120 hr) and 3

- phenoxybenzaldehyde (max. 65% at 120 hr)

Alpha

- cypermethrin:

67 days (pH 7, 25oC) MRID 42620501

MRID 48425002

Aqueous photolysis half

- life 36.2 days

3

- PBA (max. 35% at 35 days)

Alpha

- cypermethrin:
5 days MRID 42395701

MRID 48425003

Soil photolysis half

- life sandy loam 55 days

cyperamide (steadily increased to a max. of 13.3%) MRID 42129001

Aerobic soil metabolism

half

- life 60.7 days (sandy loam, acid label) 59.8 days (sandy loam, alcohol label)

cis/trans

- DCVA (max. 24% at 62 days, study duration 150 days)

Alpha

- cypermethrin:

28 days (UK sandy loam soil) MRID 42156601

MRID 4845006

Anaerobic soil metabolism

half

- life 53.3 days (sandy loam, acid label) 63 days (sandy loam, alcohol label)

cis/trans

- DCVA (max. 33% 30 days after flooding), 3

- PBA (max. 26% at 60 days after flooding or end of study) MRID 42156602

Aerobic aquatic metabolism 8.9 days MRID 45920801- Page 25 of 126

- Property Value / Degradates observed Reference

half

- life 10.1 days

trans

- DCVA (max. 49% at 30 days), cis

- DCVA (max. 19% at 30 days), 3

- PBA (max. 42% at 30 days); study duration, 90 or 183 days.

Alpha

- cypermethrin:

2.8

– 11 days MRID 48425011,

48425012

Anaerobic aquatic

metabolism half

- life 13.8 days (clay loam, benzyl label) 16.5 days (clay loam, cyclopropyl label)

DCVA (max. 34% at 71 days) MRID 44876105

Adsorption coefficient

K

oc (L/Kg)

---------------------------------- Aged Column Leaching Study 328,500 (Sand) 134,900 (Sandy loam) 82,600 ( Silty loam) 20,800 (Clay loam)

Alpha

- cypermethrin: 26,492

– 144,662

------------------------------------------------------------------------- Degradate cis/trans

- DCVA found at up to 13.2% in the

leachate MRID 42129003

MRID 48425008

---------------------- MRID 42129002

Terrestrial Field Dissipation Study 13 days (CA soil) 5 days (LA soil) MRID 42459601

Bioconcentration factor (BCF) 161X edible portion

448X whole fish

883X non

- edible moderately slow depuration, with 10

- 15% of residues remaining after 21 days of depuration MRID 42868203



### 3.2.1.1. Transport and Mobility

Alpha

- c ypermethrin is considered immobile in soil. Soil organic carbon adsorption coefficients (K

oc 

### ) for cypermethrin ranged from approximately 21,000 to 3 2 8

, 500 L/Kg in four soils (sand, sandy loam, silty loam and clay). If released into water, cypermethrin rapidly partitions to the sediment column. The tendency to adsorb to soil and sediment along with the relatively low vapor pressure (2.5x10 - 9 

### mm Hg) and Henry’s law constant (3.4x10 - 7 

### atm

- m 3 

### /mol), indicates that volatilization from water and soil will not be an important transport process. It can be concluded that the cypermethrin degradates 3

- PBA and trans

- DCVA have a high potential for mobility as they were weakly sorbed to four soils tested. 3

- PBA was slightly more sorbed (K

oc 

### values ranging from 118 to 215) to the tested soils than was trans

- DCVA (K

oc 

### values ranging from 18 to 48).

3.2.1.2. Degradation

Cypermethrin labeled with 14 

### C at the cyclopropyl and benzyl moieties was relatively stable at pH 5 and 7 buffered solutions, but degraded rapidly with half

- lives of approximately 2 days in pH 9- Page 26 of 126

- 

### solutions. The major degradation products of the base catalyzed hydrolysis of cypermethri n were cis

- and trans

- DCVA (maximum 79% at 120 hours or study duration) and 3

- phenoxybenzaldehyde (maximum 65% at 120 hours). Photolysis of cypermethrin in distilled water occurs slowly, but the rate of degradation appears to be enhanced in natural water s, which contain humic and fulvic acids. A photolysis half

- life of 5 days was observed for alpha

cypermethrin in pH 7 aqueous buffered solution exposed to sunlight in California from March to April. Shorter half

- lives on the order of less than 1 to 4 day s were observed for cypermethrin dissolved in river water, seawater and distilled water with 1% humic acid exposed to sunlight (Takahashi et al. 1985). The half

- life for thin films of cypermethrin in a sandy loam soil matrix was approximately 55 days; how ever, degradation was also observed in control samples and the

dark control corrected half

- life is over 100 days. The only transformation product observed was cyperamide, at 13.3% at the end of the study (35 days). Cypermethrin degraded with a half

- life of approximately 60 days in a fine sandy loam soil maintained at 25 o 

### C and held under aerobic

conditions (28 days for alpha

- cypermethrin) . Carbon dioxide and a mixture of cis

- and trans

DCVA (maximum 24% at 62 days in a 150 day study) were the major degr adation products.

Under aquatic conditions, cypermethrin degraded more rapidly than in soil (8.9

- 10.1 days in a supplemental aerobic aquatic study and 13.8

- 16.5 days in an anaerobic aquatic study). Degradation products (see Table 3. 4 for structures) unde r aerobic aquatic conditions included

trans

- DCVA (max. 49% at 30 days), cis

- DCVA (max. 19% at 30 days) and 3

- PBA (max. 42% at 30 days, study duration 183 days). Under anaerobic conditions, the only degradation product was DCVA at 34% at 71 days (study dur ation 90 days for benzyl label and 183 days for cyclopropyl label).

Figure 3.4. Nomeclature and Structures of Potential Degradation Products of Alpha

Cypermethrin

Common Name Chemical Name Structure

DCVA 3

- (2,2

- dichloroethenyl)

- 2,2

- dimethylcyclo

propane carboxylic

acid

3

- phenoxy

benzaldehyde- Page 27 of 126

- 3

- PBA 3

- phenoxybenzoic

acid

cyperamide



### 3.2.1.3. Field Studies

Terrestrial field dissipation studies conducted in Madera, CA and Cheneyville, LA indicated that the field dissipation half

- life of formulated cypermethrin is approximately 1 to 2 weeks.

Cypermethrin in the form of Ammo 2.5 EC was applied three times at 0.2 lb ai/acre/application to a bare silt loam soil (78

- 82% sand, 14

- 20% silt, 2

- 4% clay, 0.2

- 0.6% OM, pH 6.5

- 7.2) located in Madera, California and soil samples were analyzed for cypermethrin and potential degradates

cis

- DCVA, trans

- DCVA, and 3

- PBA . Cype rmethrin was detected in 3

- 6" cores collected immediately after each application (18, 8, and 33 μg/kg), and on day 2 (20 μg/kg) and day 4 (29 μg/kg) following the third application. Cypermethrin was detected at 10 μg/kg in one 6

- 12" core collected 2 days a fter the final application, but it was not detected in any soil cores collected below this depth (detection limit of 7 μg/kg). The degradate 3

- PBA was detected in 0

- 3" cores collected immediately after the second application (8 μg/kg), immediately after th e third application (17 μg/kg), and the following days after the third application: day 2 (25 μg/kg), day 4 (32 μg/kg), day 7 (25 μg/kg), day 14 (24 μg/kg), day 21 (8 μg/kg), and day 28 (7 μg/kg). It was not detected above a detection limit of 7 μg/kg in a ny soil cores collected below 3 inches. Potential degradates cis

- and trans

- DCVA were not detected above the detection limit of 7 μg/kg in any of the soil cores. An analysis of the cypermethrin concentration as a function of time yielded a field dissipati on half

- life of 13 days.

In a second study, cypermethrin in the form of Ammo 2.5 EC was applied three times at 0.2 lb a.i./acre/application to a bare loamy sand soil (30% sand, 64% silt, 6% clay, 0.7% OM, pH 7.0) located in Cheneyville, LA . The soil cores were analyzed for cypermethrin and potential degradates cis

- DCVA, trans

- DCVA, and 3

- PBA . Based upon dissipation in the top 0

- 3" soil cores, the dissipation half

- life for cypermethrin was 5 days. Cypermethrin was not detected

above a det ection limit of 7 μg/kg in any cores collected below 3 inches. The degradate trans

-- Page 28 of 126

- 

### DCVA was detected in 0

- 3" cores collected on the following days after the third application: day 2 (16 μg/kg) and day 7 (8 μg/kg). The degradate 3

- PBA was detected in 0

- 3" cores collected immediately after the second application (10 μg/kg), immediately after the third application (20 μg/kg), and 2 days after the 3rd application (44 μg/kg). The degradate cis

- DCVA was not detected above a detection limit of 7 μg/kg in any of the soil cores. None of the analytes were detected above a detection limit of 7 μg/kg in any of the soil cores collected below 3 inches.

Given the large number of registered uses, additional data under this guideline (835.6100, Terrestrial Field Dissipa tion) are needed to describe v ariability across the U.S.

T here are two supplemental aquatic field dissipation studies conducted with zeta

- cypermethrin in

California and Louisiana. The half

- lives were 181 days and 126 days, respectively. These half

lives are not similar to those observed in the laboratory studies. Nevertheless, the reported half

lives included the sediments only.

A POTW study to determine the fate of the cypermethrins (racemic, alpha

- , and zeta

cypermethrin) in sewage treatment works i s being requested to to ascertain whether indoor and urban cypermethrin uses contribute to toxicity in receiving waters or sediments after discharge of treated sewage.

3.2.1.4. Bioconcentration

The reported value of log octanol/ water partition coefficie nt of 6.4 suggests that alpha

cypermethrin has the potential to bioaccumulate in aquatic organisms assuming that chemical metabolism is negligible. Maximum BCFs for the alpha

- cypermethrin are 161x for edible tissue, 883x for viscera, and 448x for whole fi sh (MRID 42868203 , study conducted with racemic cypermethrin ) . Depuration appeared to be moderately slow, with ~10

- 15% of the initial residues remaining after 21 days. Thus, it appears that there is potential for bioaccumulation/ bioconcentration in aquat ic organisms. However, alpha

- cypermethrin is being metabolized extensively in the fish, which suggests a reduc e ded potential for alpha

- cypermethrin to biomagnify in terrestrial organisms.

3.2.2. Measures of Aquatic Exposure- Page 29 of 126

- 

### 3.2.2.1. Surface Water Exposure

The Tier II model Pesticide Root Zone Model (PRZM v3.12.2; May 12, 2005; Carousel et al.

, undated) linked with EXposure Analysis Modeling System (EXAMS v2.98.4.6; Apr. 25, 2005; Burns, 2004) via the PRZM/EXAMS model shell (PE v5.0, Nov. 15, 2006), i.e.

, PRZM/EXAMS) and the Tier I Rice Model (v1.0, May 8, 2007) were used to estimate screening

level exposure concentrations i n aquatic environments. The PRZM model simulates pesticide movement and transformation on and across the agricultural field resulting from crop applications. The EXAMS model simulates pesticide concentrations in water due to loading via runoff, erosion, and spray drift, assuming a standard 1

- ha pond, 2

- m deep (20,000 m 3 

### ) with no

outlet that borders a 10

- ha treated field. Simulations are for multiple (usually 30) years, from which the Agency estimates peak values that are expected to recur on average once every ten years, based on time series of daily estimated concentrations. The coupled PRZM and EXAMS models and user’s manuals are available from the U.S. Environmental Protection Agency Water

Models web

- page (USEPA, 2011b).

Exposure estimates generated using the standard pond are intended as surrogates for potential concentrations in a wide variety of vulnerable water bodies, including prairie potholes, playa lakes, vernal pools, other wetlands, man

- made and natural ponds, and ephemeral and first

- order

s treams. Innumerable site

- specific factors will tend to make such water bodies more or less vulnerable than the standard pond. Static water bodies that have larger ratios of pesticide

- treated drainage area to water body volume are generally expected to ha ve higher peak concentrations than the standard pond’s EECs. Such water bodies may be smaller in size, and/or have larger drainage areas. However such water bodies may be more likely to overflow and discharge pesticide in their effluent, whereas the stan dard pond has no discharge. As watershed size increases, it becomes increasingly unlikely that the entire watershed is planted with a single crop that is all treated simultaneously with a pesticide. Headwater streams may have peak

concentrations that are higher than those predicted for the standard pond, but such concentrations will likely persist for only short periods of time or distance, as they are carried downstream and diluted with water originating elsewhere.

Estimations regarding the spray drift fraction in the PRZM/EXAMS model runs were based upon the Tier I mode of AgDRIFT® program. The primary assumption is that the wind speeds at each site are generally below 10 mph. This is consistent with the label language that indicates “Make aerial or g round applications when the wind velocity favors on target product deposition (approximately 3 to 10 mph). Do not apply when wind velocity exceeds 15 mph.” However, there may be uncertainty with respect to unconcerned applicators that would apply the che mical at wind speeds above 10 mph.

There is uncertainty with respect to the level of mitigation that a buffer zone of 150 ft plus a vegetative strip of 10 ft can provide. The estimation of spray drift was obtained from AgDRIFT®; however, there is no way to know how well the buffer zone will protect the bodies of water from runoff. In certain cases, the level of runoff is the most important factor, rather than the level of spray drift. This is an assumption made in the Tier I calculation of AgDRIFT®.- Page 30 of 126

- 

### Th e Tier I Rice Model was used to estimate screening

- level exposure to alpha

- cypermethrin that may occur in water bodies receiving release water from rice paddies that were treated with alpha

cypermethrin. This model was used to assess the proposed use on r ice seed because the PRZM/EXAMS exposure models do not specifically address the unique rice growing environment and the model is approved for use in risk assessment. The model produces a single exposure value that represents a dissolved concentration with in a rice paddy. This single value is used to approximate both acute and chronic exposures.

The Tier I Rice Model relies on an equilibrium partitioning concept to provide conservative exposure estimates resulting from application of pesticides to rice pa ddies. When a pesticide is applied to a rice paddy, the model assumes instantaneous partitioning between the water and sediment phases. The model does not account for pesticide degradation, mass transfer between the aqueous phase and the sediment, volati lization, dilution, or other potentially important attenuation processes; therefore the model provides an upper

- bound estimate of exposure for alpha

- cypermethrin which is proposed for use on rice as a foliar spray by air or ground equipment. The Tier I Ric e Model was calibrated to generate estimates that are consistent with or conservative for dissolved concentrations measured within rice paddies and in discharged paddy

water. The model was not evaluated or calibrated for concentrations measured in sedimen t and does not account for residues bound to suspended sediment. A description of and guidance for using the Tier I Rice Model may be found on the U.S. Environmental Protection Agency (EPA)

Water Models web

- page (USEPA, 2011b).

The general chemical and e nvironmental fate data for alpha

- cypermethrin listed in Table 3.2

- 3.3

were used for generating model input parameters for PRZM and EXAMS (listed in Table 3.5 ).

C hemical specific and model input values were chosen in accordance with current divisional guid ance (USEPA, 2009). Where data was submitted specific to alpha

- cypermethrin, these data

are identified below in Table 3.5.

Table 3.5. PRZM and EXAMS Surface Water Chemical Input Parameters for Alpha

cypermethrin.

Parameter (units) Value(s) Sources Comments

Chemical Name alpha

- cypermethrin Label Proposed label

K OC 141,700 MRID: 42129003 Represents the average K OC value among four values ranging from 20,800 to 328,000 ml/g; the K OC model was utilized as per recommendation of the

SAP.

Aerobic Soil Metabolism (days) 69.8 MRID: 42156601

MRID: 48425003 Represents the 90 th percentile of the upper confidence bound on the mean of

three half

- life values two for cypermethrin = 60.7 and 59.8 days, and one for alpha = 28 days; mean = 69.8 days; std. dev. = 1 8.6 days Buffer Zone (ft.) 25 ground

150 aerial Label

--

Application Efficiency (fraction) 0.99 for ground

0.95 for aerial --- EFED guidance on input parameters for PRZM/EXAMS, v2.1, dated

10/22/2009 Spray Drift (fraction) 0.039 AgDRIFT Crops that are applied by aerial- Page 31 of 126

- Parameter (units) Value(s) Sources Comments applications. Otherwise default to USEPA, 2009 input guidance

. Solubility in Water (ppm) 0.0040 Laskowski, 2002 At 20°C. Laskowski, 2002 Rev.

Environ. Contam. Toxicol. 174:49

- 170 Aerobic Aquatic Metabolism (days) 10.7 MRID 45920801 Represents the 90 th percentile of the upper confidence bound on the mean of

two half

- life values: 8.9 and 9.8 days; mean = 9.35 days; std. dev. = 0. 64 days Anaerobic Aquatic Metabolism (days) 18.1 MRID 42156602 Represents the 90 th percentile of the

upper confidence bound on the mean of

two half

- life values: 13.8 and 16.5 days; mean = 15.15 days; std. dev. = 1.35 days Hydrolysis at pH 7(days) 67 MRID 48425003 Data specific for alpha

- cypermethrin Aqueous Photolysis @ pH 7 (days) 5 MRID 48425003 Data speci fic for alpha

- cypermethrin

Molecular Weight (g/mole) 416.3 Laskowsky 2002 Laskowski, 2002 Rev. Environ.

Contam. Toxicol. 174:49

- 170 Vapor Pressure (torr or mmHg) 2.5 x 10 - 9 Laskowsky 2002 Laskowski, 2002 Rev. Environ.

Contam. Toxicol. 174:49

- 170 Henry’s Law Constant (atm

- m 3 /mol) 3.4 x 10 - 7 Laskowsky 2002 Laskowski, 2002 Rev. Environ.

Contam. Toxicol. 174:49

- 170



### The scenarios selected for modeling purposes in PRZM/EXAMS were used to represent the maximum application rates for all alpha

- cypermethrin uses , except rice

. Table 3.7 presents the model inputs for application type and method as well as the scenarios selected for each modeled

use.

Table 3.7. PRZM/EXAMS Model Input Parameters for Alpha

- cypermethrin Application

Methods

Use Scenario Metfile Application

Rate

lbs a.i./A (kg a.i./ha) Apps per

Year Interval (days) Date of

Initial

A pp. (dd

- mm) A pp. Method (CAM)

Alfalfa ILalfalfaNMC.txt 14842.dvf 0.025 3 7 01

- 06 Aerial (2)

Brassica/cucurbits vegetables 1 FLCucumbers ST

D.txt 12844.dvf 0.025 6 7 16

- 10 Aerial (2)

Citrus fruit FLCitrus STD.txt 12844.dvf 0.025 8 14 01

- 02 Ground spray (2) Corn (field, pop, seed) ILcornSTD.txt 14842.dvf 0.025 4 3 01

- 06 Aerial (2)

Corn (sweet) ILcornSTD.txt 14842.dvf 0.025 6 3 01

- 06 Aerial (2)

Cotton MScottonSTD.txt 03940.dvf 0.025 6 3 01

- 06 Aerial (2)

Legume vegetables MSsoybean STD.t

xt 03940.dvf 0.025 6 5 01

- 06 Aerial (2)

Root and tuber vegetables MNsugarbeetSTD

.txt 14914.dvf 0.025 6 4 01

- 06 Aerial (2)

Sorghum (and other cereals) KSsorghumSTD.t

xt 13996.dvf 0.025 5 10 01

- 06 Aerial (2)

Sugar beets MNsugarbeetSTD 14914.cvf 0.025 6 7 01

- 06 Aerial (2)- Page 32 of 126

- .txt Tomatoes (fruiting vegetables) FLtomatoSTD_V

2.txt 12448.dvf 0.025 6 7 16

- 10 Aerial(2)

Tree nuts GApecansSTD.txt 93805.dvf 0.025 5 7 21

- 09 Aerial (2)

Wheat NDwheatSTD.txt 14914.dvf 0.025 5 14 01

- 06 Aerial (2)

Rice Tier I Rice Model

-- 0.025 4 7 Aerial

1 Use represents brassica vegetables, cucurbits, and leafy vegetables.



### For the rice use, t he Tier I Rice Model was used to estimate screening

- level exposure to alpha

cypermethrin that may occur in water bodies receiving applications of alpha

- cypermethrin. This model uses the application rate for rice (0.028 kg a.i./ha, 4 applications for a total of 0.112 kg/ha) and the organic carbon partitioning coefficient for alpha

- cypermethrin (141,700 mL/g oc). The Tier I rice model inputs are listed below in Table 3. 8

.

Table 3. 8 . Tier I Rice Model Inputs
Compound Application Rate (kg/ha /yr ) Koc Kd

Alpha

- cypermethrin 0. 1 (0.028, 4x) 141,700 1417



### The aquatic EECs resulting from the proposed alpha

- cypermethrin uses (listed in Table 3. 9 ) were used for risk estimation in this screening

- level assessment. Example model input and output supporting these values is provided in Appendix C

.

Table 3. 9

. Modeled Aquatic Surface Water 1

- in

- 10

- year EECs for Proposed Uses of Alpha

cypermethrin

Uses Max. App. R ate (lbs a.i./A/yr) Peak (ppb) 21

- day (ppb) 60

- day (ppb)

Alfalfa 0.075 0.04 0.01 0.004

Brassica vegetables 1 0.15 0.07 0.01 0.01

Citrus fruit 0.2 0.17 0.02 0.01

Corn (field, pop, seed) 0.1 0.32 0.03 0.02

Corn (sweet) 0.15 0.45 0.04 0.03

Cotton 0.15 0.62 0.06 0.03

Legume vegetables 0.15 0.25 0.03 0.01

Root and tuber vegetables 0.15 0.08 0.02 0.01

Sorghum (and other cereals) 0.125 0.21 0.03 0.02

Sugar beets 0.15 0.08 0.01 0.01

Tomato 0.15 0.08 0.01 0.01

Tree nuts 0.125 0.20 0.02 0.01

Wheat 0.125 0.08 0.01 0.01

Rice (Tier I Rice Model) 0.1 0.54 <0.54 <0.54

1 Use represents brassica vegetables, cucurbits, and leafy vegetables.- Page 33 of 126

- 

### 3.2.2.2. Sediment Pore Water Exposure

Environmental fate data show that alpha

- cypermethrin readily dissipates from the water column but not from aquatic systems in their entirety, as it has been detected in sediment and the high propensity for the compound to bind to organic matter; therefore sediment exposure may be a

concern for sediment

- dwelling organisms. Benthic sediment pore water EECs were calculated for the proposed maximum use patterns for alpha

- cypermethrin. Pore

- water EECs are provided

in Table 3. 10

. Note that the Tier I R ice M odel does not estimate pore water concentrations.

Table 3. 10 . 1

- in

- 10 year Pore Water EECs for Proposed Uses of Alpha

- cypermethrin

Uses Max. App. R ate (lbs a.i./A/yr) Peak (ppb) 21

- day (ppb) 60

- day (ppb)

Alfalfa 0.075 0.001 0.001 0.001

Brassica vegetables 1 0.15 0.002 0.001 0.001

Citrus fruit 0.2 0.003 0.002 0.002

Corn (field, pop, seed) 0.1 0.005 0.004 0.003

Corn (sweet) 0.15 0.008 0.007 0.005

Cotton 0.15 0.01 0.007 0.005

Legume vegetables 0.15 0.004 0.003 0.002

Root and tuber vegetables 0.15 0.002 0.002 0.001

Sorghum (and other cereals) 0.125 0.005 0.004 0.003

Sugar beet 0.15 0.001 0.001 0.001

Tomato 0.15 0.002 0.002 0.001

Tree nuts 0.125 0.005 0.004 0.003

Wheat 0.125 0.001 0.001 0.001

1 Use represents brassica vegetables, cucurbits, and leafy vegetables

.



### 3.2. 3

. Measures of Terrestrial Exposure

3.2.3.1

. Terrestrial Wildlife

Exposure estimates for terrestrial animals assumed to be in the target area or in an area exposed to spray drift are derived using the T

- REX model (version 1.4.1, 10/08/2008 ). This model incorporates the Ken a ga nomograph, as modified by Fletcher et al. ( 1994 ), which is based on a large set of actual field residue data. The upper limit value s f rom the nomograph represent the

95 th 

### percentile of residue values from actual field measurements (Hoerger and Kenaga 1972 ). Consideration is given to different types of feeding strategies for mammals and birds, including herbivores, insectivores and granivores. For dose

- based exposures, three weight classes of birds (20, 100, and 1000 g) and mammals (15, 35 and 1000 g) are considered. Given that no data on interception and subsequent dissipation from foliar surfaces are a vailable for alpha

- cypermethrin, a default foliar dissipation half

- life of 35 days is used based on the work of Willis and McDowell (1987). Input parameters used in T

- REX are provided in Table 3. 1 1

. The dietary

- based EECs on a variety of food items from t he proposed new uses of alpha

- cypermethrin are provided in Table- Page 34 of 126

- 

### 3. 1 2 ; dose

- based EECs are provided in Table 3.1 3 (see Appendix B for example T

- REX
outputs ).

Table 3. 1 1

. Input parameters used in T

- REX (v1. 4

. 1 ) to determine terrestrial EECs for alpha

- cyper methrin spray application scenarios

.

Crop/Use Maximum Application

Rate (lbs a.i./A) Foliar Half

Life (days) 1 Application

Interval (days) Maximum

Number of Applications

Alfalfa 0.025 35 7 3 Brassica vegetables 2 0.025 35 7 6

Citrus fruits 0.025 35 14 8 Corn (field, pop, seed) 0.025 35 3 4 Corn (sweet) 3 0.025 35 3 6 Legume vegetables 0.025 35 5 6 Rice (grain, straw) 0.025 35 7 4

Root and tuber vegetables (except sugar beet) 0.025 35 4 6

Sorghum (and other cereals) 0.025 35 10 5

Tree nuts 0.025 35 7 5

Wheat 0.025 35 14 5

1 Default foliar half

- life in T

- REX (v1.4.1)

2 Use represents brassica vegetables, cucurbits, fruiting vegetables, leafy vegetables, soybeans, and sugar beets.

3 Use represents corn (sweet) and cotton.



### Table 3.1 2

. Dietary

- based EECs for alpha

- cypermethrin spray application scenarios.

Crop/Use Dietary

- based EECs (mg a.i./kg)

Short Grass Tall Grass Broadleaf

Plants/Small

Insects Fruits/Pods/S

e eds/Large

Insects

Alfalfa 15.77 7.23 8.87 0.99 Brassica vegetables 1 26.18 12.00 14.72 1.64

Citrus fruits 22.08 10.12 12.42 1.38 Corn (field, pop, seed) 22.00 10.08 12.38 1.38 Corn (sweet) 2 31.19 14.30 17.54 1.95 Legume vegetables 28.51 13.07 16.04 1.78 Rice (grain, straw) 19.73 9.04 11.10 1.23

Root and tuber vegetables (except sugar beet) 29.80 13.66 16.76 1.86

Sorghum (and other cereals) 20.99 9.62 11.81 1.31

Tree nuts 23.18 10.62 13.04 1.45

Wheat 18.58 8.52 10.45 1.16

1 Use represents brassica vegetables, cucurbits, fruiting vegetables, leafy vegetables, soybeans, and sugar beets.

2 Use represents corn (sweet) and cotton.



### Table 3.1 3 . Dose

- based EECs for alpha

- cypermethrin spray application scenarios.- Page 35 of 126

- Crop/Use Dose

- Based EECs (mg a.i./kg)

Food Type Birds Mammals 20g 100g 1000g 15g 35g 1000g

Alfalfa Short Grass 17.96 10.24 4.59 15.04 10.39 2.41

Tall Grass 8.23 4.69 2.10 6.89 4.76 1.10

Br oa dleaf Plants/Small

Insects 10.10 5.76 2.58 8.46 5.85 1.36

Fruit/Pods/Seeds/ Large

Insects 1.12 0.64 0.29 0.94 0.65 0.15

Seeds (Granivores) 0.25 0.14 0.06 0.21 0.14 0.03

Brassica vegetables 1 Short Grass 29.81 17.00 7.61 24.96 17.25 4.00

Tall Grass 13.66 7.79 3.49 11.44 7.91 1.83

Br oa dleaf Plants/Small

Insects 16.77 9.56 4.28 14.04 9.70 2.25

Fruit/Pods/Seeds/ Large

Insects 1.86 1.06 0.48 1.56 1.08 0.25

Seeds (Granivores) 0.41 0.24 0.11 0.35 0.24 0.06

Citrus fruits Short Grass 25.15 14.34 6.42 21.05 14.55 3.37

Tall Grass 11.53 6.57 2.94 9.65 6.67 1.55

Br oa dleaf Plants/Small

Insects 14.15 8.07 3.61 11.84 8.18 1.90

Fruit/Pods/Seeds/ Large

Insects 1.57 0.90 0.40 1.32 0.91 0.21

Seeds (Granivores) 0.35 0.20 0.09 0.29 0.20 0.05

Corn (field, pop, seed) Short Grass 25.06 14.29 6.40 20.98 14.50 3.36

Tall Grass 11.49 6.55 2.93 9.61 6.64 1.54

Br oa dleaf Plants/Small

Insects 14.10 8.04 3.60 11.80 8.16 1.89

Fruit/Pods/Seeds/ Large

Insects 1.57 0.89 0.40 1.31 0.91 0.21

Seeds (Granivores) 0.35 0.20 0.09 0.29 0.20 0.05

Corn (sweet) 2 Short Grass 35.52 20.26 9.07 29.74 20.55 4.77

Tall Grass 16.28 9.28 4.16 13.63 9.42 2.18

Br oa dleaf Plants/Small

Insects 19.98 11.39 5.10 16.73 11.56 2.68

Fruit/Pods/Seeds/ Large

Insects 2.22 1.27 0.57 1.86 1.28 0.30

Seeds (Granivores) 0.49 0.28 0.13 0.41 0.29 0.07

Legume vegetables Short Grass 32.47 18.52 8.29 27.18 18.79 4.36

Tall Grass 14.88 8.49 3.80 12.46 8.61 2.00

Br oa dleaf Plants/Small

Insects 18.26 10.41 4.66 15.29 10.57 2.45

Fruit/Pods/Seeds/ Large

Insects 2.03 1.16 0.52 1.70 1.17 0.27

Seeds (Granivores) 0.45 0.26 0.12 0.38 0.26 0.06

Rice (grain, straw) Short Grass 22.47 12.81 5.74 18.81 13.00 3.01

Tall Grass 10.30 5.87 2.63 8.62 5.96 1.38

Br oa dleaf Plants/Small

Insects 12.64 7.21 3.23 10.58 7.31 1.70

Fruit/Pods/Seeds/ Large

Insects 1.40 0.80 0.36 1.18 0.81 0.19

Seeds (Granivores) 0.31 0.18 0.08 0.26 0.18 0.04

Root and tuber

vegetables (except sugar beet) Short Grass 33.94 19.36 8.67 28.41 19.64 4.55

Tall Grass 15.56 8.87 3.97 13.02 9.00 2.09

Br oa dleaf Plants/Small

Insects 19.09 10.89 4.87 15.98 11.05 2.56

Fruit/Pods/Seeds/ Large

Insects 2.12 1.21 0.54 1.78 1.23 0.28

Seeds (Granivores) 0.47 0.27 0.12 0.39 0.27 0.06- Page 36 of 126

- Sorghum (and other cereals) Short Grass 23.90 13.63 6.10 20.01 13.83 3.21

Tall Grass 10.96 6.25 2.80 9.17 6.34 1.47

Br oa dleaf Plants/Small

Insects 13.45 7.67 3.43 11.26 7.78 1.80

Fruit/Pods/Seeds/ Large

Insects 1.49 0.85 0.38 1.25 0.86 0.20

Seeds (Granivores) 0.33 0.19 0.08 0.28 0.19 0.04

Tree nuts Short Grass 26.39 15.05 6.74 22.10 15.27 3.54

Tall Grass 12.10 6.90 3.09 10.13 7.00 1.62

Br oa dleaf Plants/Small

Insects 14.85 8.47 3.79 12.43 8.59 1.99

Fruit/Pods/Seeds/ Large

Insects 1.65 0.94 0.42 1.38 0.95 0.22

Seeds (Granivores) 0.37 0.21 0.09 0.31 0.21 0.05

Wheat Short Grass 21.17 12.07 5.40 17.72 12.25 2.84

Tall Grass 9.70 5.53 2.48 8.12 5.61 1.30

Br oa dleaf Plants/Small

Insects 11.91 6.79 3.04 9.97 6.89 1.60

Fruit/Pods/Seeds/ Large

Insects 1.32 0.75 0.34 1.11 0.77 0.18

Seeds (Granivores) 0.29 0.17 0.08 0.25 0.17 0.04

1 Use represents brassica vegetables, cucurbits, fruiting vegetables, leafy vegetables, soybeans, and sugar beets.

2 Use represents corn (sweet) and cotton.



### Alpha

- cypermethrin exposures to terrestrial invertebrates are not quantitatively calculate d for

derivation of deterministic RQs. However, risk to this taxon is assessed qualitatively in the Risk Description, Section 4.2.

T he model s SIP v

. 1.0 and STIR v.1.0 were used to evaluate whether risk to terrestrial animals is

of concern for drinking water or inhalation alone. Results for both models indicate that drinking

water and inhalation alone are not routes of concern for terrestrial brids and mammals. Results are provided in Appendix D

.

Additionally, The KABAM model v 1.0 was used to estimate potential risks to birds and mammals from bioaccumulation of hy drophobic organic pesticides in freshwater aquatic ecostystems. Results for the highest use pattern, provided in Appendix D , indicate that risks to birds and mammals are low. This is likely a result of alpha

- cypermethrin being metabolized extensively in th e fish, as shown in the available BCF study with the bluegill sunfish (MRID 42868203).

3. 2

. 3.2. Terrestrial Plants

Exposure of naturally

- occurring terrestrial and semi

- aquatic (wetland) plant species is typically estimated using OPP’s TerrPlant (v1.2.2 ; US EPA, 2006b ) model and is assumed to encompass

areas outside the immediate use site. The TerrPlant model is used to derive EECs in runoff and

drift for terrestrial and semi

- aquatic plants near areas where alpha

- cypermethrin has been applied. Runoff exp osure is assessed in two scenarios: sheet and channel runoff. In the sheet runoff scenario, the treated area generating runoff is assumed to drain into an area with equal size containing seedlings, resulting in 1, 2, or 5% of the a mount applied being depo sited. In the- Page 37 of 126

- 

### channel runoff scenario, a ten

- to

- one ratio of treatment area to receiving area results in 10, 20, or

50% of the amount applied being deposited on soil with emerging or emerged seedlings. Spray drift is also a source of pesticide loading to non

- target areas. TerrPlant estimates EECs based on

app lication rate, application method, chemical solubility in water

, type of runoff and default assumptions of drift

. The EECs for terrestrial and semi

- aquatic plants for a single application of alpha

- cypermethrin could not be calculated because acceptable seedling emergence and vegetative vigor studies have not been submitted. However, a supplemental Tier II vegetative vigor study has been submitted and will be discussed in the Risk Description

.

3.3

. Ecological Effects Characterization

In screening

- level ecological risk assessments, effects characterization describes the types of effects a pesticide can have on aquatic and terrestrial organisms. To date, toxicity tests for amphibian or reptile s are not required; birds are used as surrogates for reptiles and terrestrial

phase amphibians and freshwater fish are used as surrogates for aquatic

- phase amphibians. This characterization is based on the registrant

- submitted toxicity data for birds, mam mals, fish, invertebrates, and plants for alpha

- cypermethrin , two major degradates and a typical formulated product ( BAS 310 40 I ). No data were available in the public literature for alpha

- cypermethrin effects characterization (see below).

In addition t o the data submitted in support of registration, the public version of ECOTOX (ECOTOXicity) database (USEPA, 20 11 ) was searched for additional toxicity data from the open literature. The ECOTOX database is a publicly

- available, quality

- assured, comprehensive tool for locating toxicity data from the open literature and is maintained by EPA Mid

- Continent Ecology Division. More inf ormation on ECOTOX can be found at: http://www

. epa.gov/ecotox. Research papers are thoroughly screened using standard procedures before being accepted into ECOTOX thereby ensuring consistent, high quality information. For alpha

- c ypermethrin and its degradates, no studies were identified in ECOTOX as of April 27, 2012

. However, alpha

cypermethrin has been bridged with racemic cypermethrin and zeta

- cypermethrin, which have

thousands of available studies in ECOTOX.

Given that alpha

- cypermethrin is a new active ingredient with no previous registration in the U.S. or any other country, it is assumed that no ecological incidents exist for alpha

- cypermethrin

. However, alpha

- cypermethrin has been bridged with racemic cypermethrin an d zeta

cypermethrin (as discussed in Appendix A ) , which have 22 reported major incidents (15 fish, 2 avian, 3 mammalian, and 2 terrestrial invertebrates) and 26 reported minor incidents (21 fish and wildlife, 4 plants, and 1 “other non

- target”). Since alph a

- cypermethrin has similar ecological fate and ecotoxicity profiles to racemic and zeta

- cypermethrin, these incidents likely represent the potential incidents from the proposed alpha

- cypermethrin use s . See Appendix E for more information on the reported incidents.

3.3. 1

. Aquatic Toxicity Assessment

The most sensitive acute and chronic effects measurement endpoints available for alpha

cypermethrin exposure to freshwater and estuarine/marine species are summarized in Table

3.1 3

. Where there are no chemical specific data for alpha

- cypermethrin, data are bridged from- Page 38 of 126

- 

### the database available for the cypermethrins (racemic and zeta

- cypermethrin) as described in Appendix A

. All acceptable and supplemental studies available for the registration of alpha

cypermethrin are described below, and data are described in relation to the tested material (i.e., racemic cypermethrin, zeta

- cypermethrin, or alpha

- cypermethrin).

3.1 3 . Summary of most sensitive endpoints from submitted aqua tic toxicity studies for alpha

- cypermethrin

.

Exposure
Scenario Species Exposure
Duration Toxicity

Reference

Value Effects Reference Toxicity Category

Freshwater Fish

Acute Rainbow

trout
( Oncorhynch

us mykiss ) 96 hours LC 50 = 2.2 μg a.i./L Mortality MRID 47944207 Acceptable Very Highly

Toxic

Chronic Fathead

minnow

( Pimephales promelas ) 30 days NOAEC = 0.14 μg a.i./L

LOAEC = 0.33 μg ai/L Growth and mortality MRID 00089039 Acceptable NA

Freshwater Invertebrates

Acute Amphipod

( Hyalella

azteca ) 96 hours EC 50 = 0.0036 μg a.i./L Mortality MRID 44423501 Acceptable Very Highly

Toxic

Chonic Ch r oni

c No adequate data submitted; to assess chronic risk to freshwater invertebrates, a surrogate NOAEC value of 0.00059 μg a.i./L was derived based on acute

- to

- chronic ratio method using acute and chronic data for

estuarine/marine invertebrates. a

Benthic Organisms

Sub

- Chronic Amphipod

( Hyalella

azteca ) 10 days sediment value (experimental data):

NOAEC < 1.8

μg a.i./kg

sediment

LOAEC = 1.8

μg a.i./kg

sediment

pore water value (derived data) b : NOAEC < 0.00 182 μg a.i./L pore water

LOAEC = 0. 00 182 μg a.i./L pore water Mortality and

Growth MRID 44074406

Acceptable Very Highly

Toxic

Chronic No chronic data submitted; to assess chronic risk to benthic organisms, the surrogate chronic NOAEC value for pore water of 0.000781 μg a.i./L from the chronic mysid study will be used. c

Estuarine/Marine Fish Very Highly- Page 39 of 126

- 

### 3.1 3 . Summary of most sensitive endpoints from submitted aqua tic toxicity studies for alpha

- cypermethrin

.

Exposure
Scenario Species Exposure
Duration Toxicity

Reference

Value Effects Reference Toxicity Category

Acute Sheepshead

minnow

( Cyprinidon variegates ) 96 hours LC 50 = 0.95 μg

a.i./L Mortality MRID 00090075 Acceptable Toxic

Chronic No adequate data submitted; to assess chronic risk to estuarine/marine fish, a surrogate NOAEC value of

0. 06 μg a.i./L was derived based on acute

- to

- chronic ratio method using acute and chronic data for

freshwater fish. d

Estuarine/Marine Invertebrates

Acut e Mysid shrimp

( Mysidopsis

bahia ) 96 hours e LC 50 = 0.00475 μg a.i./L Mortality Acc. No. 070562 Acceptable Very Highly

Toxic

Chronic Mysid shrimp

( Mysidopsis

bahia ) 28 days NOAEC = 0.000781 μg

a.i./L

LOAEC = 0.00197 μg/L Weight of

Females reduced MRID 42725301 Acceptable Very Highly

Toxic

Aquatic Plants

Acute Lemna gibba 96 hours EC50 > 1.39 μg a.i./L

NOAEC = 1.39 μg a.i./L No toxicity MRID

47944031 Supplemental Toxicity categories are

not specified for plants

Acute Skeletonema

costatum 96 hours EC50 > 33.5 μg a.i./L

NOAEC = 33.5 μg a.i./L No toxicity MRID

47944032 Acceptable Toxicity categories are

not specified for plants

a The chonic NOAEC estimated for freshwater invertebrates is based on the acute

- to

- chronic ratio method determined by the following mathematical relationship: Estuarine/Marine invertebrate LC50 (0.00475 μg a.i./L ) / Estuarine/Marine invertebrate NOAEC (0.000781 μg a.i./L ) = Freshwater invertebrate LC50 (0.0036 μg a.i./L ) / X (estimated value for Freshwater invertebrate NOAEC), where X = 0.00059 μg a.i./L

. b For benthic organisms, the LOAEC value of 0. 00 1 82 μg a.i./L pore water was calculated as follows. The LOAEC value in whole sediment [ 1.8 μg a.i./kg sediment] is divided by the proportion of organic carbon in the sediment [0.0099 kg OC/kg
whole sediment]. Thus, the LC 50 value in units of OC is 182 μg a.i./kg OC [ 1.8 μg a.i./kg sediment ÷ 0.0099 kg OC/kg sediment]. The equivalent concentration in pore water is based on the definition of the K

oc , K

oc (L/kg OC) = Sediment Conc in OC (mg/kg OC) ÷ Conc in pore water (mg/L).

By rearrangement,

Conc in wat er = Sediment Conc in units of OC ÷ K

oc .

For the cypermethrins, the K

oc is taken as 141,700 [L/kg OC]. Thus, the calculated concentration in pore water corresponding

to the LOAEC value of 182 μg a.i./kg OC is 0. 00 182 μg a.i./L [ 182 μg a.i./kg OC ÷ 141,700 L/kg OC].

c The chronic NOAEC value for the mysid shrimp (0.000781 μg a.i./L ) will serve as a surrogate estimate of the chronic

NOAEC f or benthic organisms in units of μg a.i./L pore water . The mysid was selected as a surrogate because of similari ties in life stages exposed during chronic toxicity tests for both species. In addition the LC50 value for the mysid shrimp and Hyalella

azteca in 96

- hour acute studies are very similar (LC50= 0.00475 μg a.i./L for mysid and LC50 = 0.0036 μg a.i./L ) indicating- Page 40 of 126

- 

### 3.1 3 . Summary of most sensitive endpoints from submitted aqua tic toxicity studies for alpha

- cypermethrin

.

Exposure
Scenario Species Exposure
Duration Toxicity

Reference

Value Effects Reference Toxicity Category

that these species experience similar toxicity to cypermethrin.

d The chron ic NOAEC estimate for estuarine/ marine fish is based on the acute

- to

- chronic ratio method, determined by the following mathematical relationship: Freshwater fish LC 50 ( 2.2 μg a.i./L)/ Freshwater fish NOAEC (0.14 μg a.i./L) =

Estuarine/Marine fish LC 50 (0.95 μg a.i./L)/ X (estimated value for Estuarine/Marine fish NOAEC), where X = 0.06 μg a.i./L.

e The acute toxicity reference value identified to calculate acute RQs for estuarine/marine invertebrates is for a 96

- hour exposure duration, rather than the guideline recommended 48

- hour exposure duration. Although 48

- hour LC 50 values have been reported in other studies, these values are higher than the 96

- hour LC 50 of 0.005 μ g a.i./L. Taking the most conservative approach, EFED will use the lowest LC 50 value reported for estuarine/marine invertebrates.



### 3.3.1.1 Toxicity to Freshwater Fish

The acute toxicity of technical grade racemic cypermethrin to freshwater fish was evaluated in several species, with 96

- hour LC 50 

### values ranging from 0.39 μg a.i./L in rainbow trout (MRID 44546027) to 4.5 μg a.i./L in bluegill sunfish (MRID 44546030). Based on these results,

racemic cypermethrin is categorized as very highly toxic to freshwater fish on an acute basis.

Studies assessing the acute toxicity of two racemic cypermethrin formulations and one alpha

cypermethrin formulation in rainbo w trout were also submitted. The racemic cypermethrin

f

ormulations tested were GFU 061(36% a.i.) and GFU 070 (25.1% a.i.) ; and the alpha

cypermethrin formulation tested was BASF 310 40 I (10.5% a.i. ) . The 96

- hour LC 50 

### values reported for GFU 061, GFU 070 and BASF 310 40 I are 4.7 μ g formulation/L (MRID 00065813), 13.0 μg formulation/L (MRID 000 88947) and 2.2 μg 40 ormulation .i. /L (MRID

47944207 , respectively, indicating that these formulations are very highly toxic to freshwater fish. Comparison of the 96

- hour LC 50 

### value for racemic cypermethrin TGAI (0.39 μg a.i./L) and cypermethrin formulations ( 2

. 2 to 13.0 μg 40 ormulation .i. /L) indicates that the formulated products have a similar order of toxicity to technical grade cypermethrin.

Acute toxicity studies in freshwater fish were also submitted for the racemic cypermethrin degradate 3

- PBA in rainb ow trout (MRID 00089037) and bluegill sunfish (MRID 00089038). Results yield 96

- hour LC 50 

### values of 13.3 and 36.3 mg degradate/L in rainbow trout and bluegill sunfish, respectively. Based on these 96

- hour LC 50 

### values, 3

- phenoxy benzoic acid is categorize d as slightly toxic to freshwater fish on an acute basis and is much less toxic than cypermethrin TGAI to freshwater fish.

An early life

- stage study in fathead minnow was submitted by the registrant to establish the chronic toxicity of racemic cypermethrin to freshwater fish (MRID 00089039). Results of this

30

- day exposure study showed that survival was significantly reduced compared to controls at 0.33 μg a.i./L, yielding a 30

- day NOAEC value for survival of 0.14 μg a.i./L. No treatment

relat ed effects were observed for hatchability or growth. No acceptable chronic toxicity studies for cypermethrin formulations or cypermethrin degradates to freshwater fish were submitted.

3.3.1.2. Toxicity to Freshwater Invertebrates- Page 41 of 126

- 

### Acute toxicity studies of technical grade racemic cypermethrin to freshwater invertebrates

available include a 96

- hour LC 50 

### value for zeta

- cypermethrin of 0.0036 μg a.i./L in Hyalella

azteca (MRID 44423501)

, a 48

- hour E C 50 

### value for racemic cypermethrin of 0.42 μg a.i./L in in daphnid ( MRID 44546031 ) and a 48

- hour EC 50 

### value for alpha

- cypermethrin of 0.067 μg a.i./L om daphnids (MRID 47944208) . Based on these results, racemic cypermethrin can be categorized as very highly toxic on an acute basis. Thoug h data on the acute toxicity of alpha

cypermethrin is available for the daphnid, the amphipod Hyalella azteca is known to be more acutely sensitive to pyrethroids, such as alpha

- cypmerthrin. Therefore, taking the most conservative approach, the lowest LC 50 

### value reported for zeta

- cypermethrin (96

- hour LC 50 

### value of 0.0036 μg a.i./L) is used to evaluate acute toxic exposure of freshwater invertebrates to alpha

- cypermethrin

.

Studies assessing the acute toxicity of three racemic cypermethrin formulations and one alpha

cypermethrin formulation to daphnids were submitted. The racemic cypermethrin formulations tested were GFU 034/A (36% a.i.), GFU 061 (36% a.i.), GFU 070 (24% a.i.) ; the alpha

cypermethrin formulation tested was BASF 310 40 I (10.5% a.i.)

. Results of these studies were reported as EC 50 

### values (for immobility), rather than LC 50 

### values. The 48

- hour EC 50 

### values ranged from 0.64 μg a.i./L (MRID 47944208 ) to 21.6 μg a.i./L (MRID 89040), indicating that these formulations are very highly toxic to daphnids on an acute basis. Comparison of the 48

- hour LC 50 

### /EC 50 

### values for racemic cypermethrin TGAI (0.42 to 2.0 μg a.i./L) and racemic cypermethrin formulations ( 0.64 to 21.6 μg a.i./L) indicates that the formulated products have a

similar order of toxi city to technical grade racemic cypermethrin.

Acute toxicity tests in freshwater invertebrates using the degradate 3

- PBA to daphnids were also submitted. Results yield 48

- hour EC 50 

### values of 89.0 mg degradate/L (MRID 152739) and 111 mg degradate/L (Acc. No. 070562). Based on these acute toxicity values, 3

- phenoxy benzoic acid is categorized as practically non

- toxic to slightly toxic to freshwater invertebrates on an acute basis. Thus, the 3

- phenoxy benzoic acid degradate is much less toxic than the

cype rmethrins TGAI to freshwater invertebrates.

No valid chronic toxicity studies on the technical grade alpha

- cypermethrin in freshwater

invertebrates were submitted. A cute

- to

- chronic ratios based on available acute toxicity data

were calculated based on th e following mathematical relationship:

Estuarine/marine invertebrate LC 50 

### (0.00475μg a.i./L) / Estuarine/marine invertebrate NOAEC (0.000781μg a.i./L) = Freshwater invertebrate LC 50 

### (0. 0036 μg a.i./L)/ X (estimated value for Freshwater invertebrate NOAEC) , where X = 0. 0 0059 μg a.i./L.

Several studies on the toxicity of racemic cypermethrin TGAI to benthic organisms have been submitted. Studies were conducted using two types of experimental protocols, exposure in a

water

- only system and exposure in a w ater

- sediment system. In the water system studies, organisms were exposed to racemic cypermethrin in overlying (surface) water; no sediment was present in the test chamber (these studies are discussed with the freshwater invertebrate studies above). For studies conducted using the water

- sediment system protocol, racemic cypermethrin- Page 42 of 126

- 

### was a pplied to water

- sediment systems and allowed to settle for 2 days; organisms were

introduced to the above water

- sediment systems, and toxicity was assessed after a 10

- day exposure period. However, these studies present a degree of uncertainty because of th e lack of equilibration of spiked sediments with the pore water (e.g., equilibration should have occurred for at least one month). While compounds bound to the sediment present potential toxicity concerns, those residues that have reached equilibrium in th e pore water are considered a greater source of toxic risk to benthic invertebrates (Di Toro et al. , 1991). Therefore the studies presented in this assessment may underestimate sediment toxicity.

Two studies on racemic cypermethrin TGAI were conducted us ing a water

- sediment system, one study with midge (MRID 44074402) and one study with amphipod (MRID 44074406). Both studies were conducted using the same protocol, as described above, using sediments from three sources (Florissant, Mississippi, and Duluth ). All toxicity values for these studies are expressed

in terms of the concentration of racemic cypermethrin in sediment (μg a.i./kg) on Day 0.

Measurement of racemic cypermethrin in sediment and surface water on Days 0 and 10 of exposure indicates that the water

- sediment system was not at equilibrium, thus adding uncertainty to the results of these studies. Results yield 10

- day NOAEC values ranging from less

than 1.8 μg a.i./kg sediment (Florrisant sediment) in amphipods, to 25 μg a.i./kg sediment (Mis sissippi sediment) for midge. LC 50 

### values ranged from 3.6 μg a.i./kg sediment (Florissant sediment) in amphipods to 67 μg a.i./kg sediment in midge (Mississippi sediment). In general, toxicity decreased (as reflected by higher LC 50 

### values), with increasin g organic carbon content of

the sediment. Since a d efinitive NOAEC value is not available for the most sensitive benthic

invertebrate/sediment test (amphipod/Florrisant sediment)

, the lowest 10

- day LOAEC value of

1.8 μg a.i./kg sediment in amphipods will be used to characterize the lower bounds of risk from acute exposure of benthic organisms to alpha

- cypermethrin TGAI in sediment.

In order to assess the risk of sub

- chronic exposure to benthic organisms to the alpha

cypermethrin TGAI based on pore water concentrations, the equivalent toxicity value in pore water is derived using the lowest 10

- day LOAEC value of 1.8 μg a.i./kg sediment in amphipods.

The LOAEC value in whole sediment [ 1.8 μg a.i./kg sediment] is divided by the proportion of organic carbon (OC) in the sediment [0.0099 kg OC/kg whole sediment]. Thus, the LOAEC

value in units of OC is 182 μg a.i./kg OC [ 1.8 μg a.i./kg sediment ÷ 0.0099 kg OC/kg sediment]. The equivalent concentration in pore water is based on the definition of the K

oc 

### ,

Koc (L/kg OC) = [sediment (mg/Kg OC)] / [pore water (mg/L)]

By rearrangement,

[water] = [sediment (mg/Kg OC)] / Koc

For the cypermethrins, the K

oc 

### is 141,700 [L/kg OC] (MRID 42129003). Thus, the calculated concentration in pore water corresponding to the LC 50 

### value of 364 μg a.i./kg OC is 0. 00 128 μg a.i./L [ 182 μg a.i./kg OC ÷ 141,700 L/kg OC]. To assess risk of acute exposure to benthic organisms to alpha

- cypermethrin TGAI in terms of pore water concentrations, the derived

LOAEC value of 0. 00 182 μg a.i. /L is used.- Page 43 of 126

- 

### Chronic toxicity studies for the most sensitive benthic organisms

, Hyalella azteca

, were not
submitted. Previous assessments for racemic and zeta

- cypermethrin calculated acute

- to

- chronic

ratios based on the available acute and c hronic toxicity data for the mysid shrimp b ecause the mysid shrimp is a crustacean and its life cycle is more closely related to the most sensitive amphipod, Hyalella azteca , than the daphnid . For this assessment, however, the chronic mysid

NOAEC value of 0.000781 μg a.i./kg will be used as a su rrogate value to assess chronic risk to benthic organisms from exposure in pore water because of the difficulties in applying an acute

to

- chronic ratio to the available sub

- chronic da ta in order to calculate a chronic endpoint.

3.3.1.3. Toxicit y to Estuarine/Marine Fish

The acute toxicity of technical grade racemic cypermethrin to estuarine/marine fish was evaluated in sheepshead minnow and Atlantic salmon, with 96

- hour LC 50 

### valu es of 0.95 μg a.i./L (MRID 00090075) and 4.3 μg a.i./L (MRID 41968212) respectively, indicating that the racemic cypermethrin TGAI is very highly toxic to estuarine/marine fish on an acute basis. Taking the most conservative approach, the lowest 96

- hour L C 50 

### value of 0.95 μg a.i./L in sheepshead minnow will be used to evaluate acute toxic exposure to estuarine/marine fish. No acute toxicity studies of cypermethrin formulations or cypermethrin degradates in estuarine/marine fish were

submitted.

No valid c hronic toxicity studies on technical grade alpha

- cypermethrin in estuarine/marine fish

were submitted. A cute

- to

- chronic ratios based on available acute toxicity data were calculated based on the following mathematical relationship :

Freshwater LC 50 

### (0.39 μg a.i./L) / Freshwater NOAEC (0. 14 μg a.i./L) =

Estuarine/Marine LC 50 

### (0.95 μg a.i./L)/ X (estimated value for Estuarine/Marine NOAEC), where X = 0.34 μg a.i./L.

This estimated NOAEC of 0.34 μg a.i./L is > 0.1 of the 60

- day EEC 1 

### , indicating the need for fish full life cycel studies per 40 CFR Part 158. No chronic toxicity studies for the formulations or degradates of the cypermethrins in estuarine/marine fish were submitted. This is identified as a data gap.

3.3.1.4. Toxicity to Estuarine/Marin e Invertebrates

Acute toxicity tests with estuarine/marine invertebrates using racemic cypermethrin TGAI were

conducted with several species including shrimp, molluscs, crab and lobster . Toxicity values (EC 50 

### and LC 50 

### ) reported for shrimp range from th e 96

- hour LC 50 

### value of 0.00475 μg a.i./L (Acc. No. 070562) to the 96

- hour LC 50 

### value of 0.01 μg a.i./L (MRID 41068003). Similar results were observed in lobster (96

- hour LC 50 

### = 0.04 μg a.i./L; MRID 41068003) and fiddler crab (96

- hour LC 50 

### = 0.197 μg a.i. /L; MRID 89045). Based on these results, the racemic cypermethrin TGAI is categorized as very highly toxic to estuarine/marine shrimp and

1 60

- d EEC of 0.131 μg a.i./L (based on North Carolina Fruit and coarse droplets, from the RED) ÷ estimated

saltwater NOAEC (0. 3 4 μg a.i./L, see calculations above ) = 0.4.- Page 44 of 126

- 

### crustaceans. Results of acute toxicity tests in molluscs show that the racemic cypermethrin TGAI is moderately to hi ghly toxic to oysters, with a 96

- hour EC 50 

### value of 0.37 mg a.i./L in Eastern oyster (MRID 89049) and a 48

- hour LC 50 

### value of >2.27 mg a.i./L in Pacific oyster (Acc. No. 070562). Results of these studies indicate that molluscs are less susceptible than

c rustaceans to racemic cypermethrin toxicity on an acute basis. Taking the most conservative approach, the 96

- hour LC 50 

### value of 0.00475 μg a.i./L in mysid shrimp will be used to calculate

acute risk to estuarine/marine invertebrates from exposure to alpha

- cypermethrin . No acute toxicity studies for the formulations or degradates of the cypermethrins in estuarine/marine

invertebrates were submitted.

Three studies involving life

- cycle tests in mysid shrimp were submitted by the registrant to

establish the chronic toxicity of racemic cypermethrin to estuarine/marine invertebrates. The NOAEC values reported in these studies range from 0.781 ng a.i./L for effects on first generation mortality, male length and weight and female weight (MRID 42725301), to 1.5 n g a.i./L for number of offspring (Acc. No. 070562) and survival and reproduction (MRID 44546035). Taking the most conservative approach, the lowest NOAEC value of 0.781 ng a.i./L will be used

to characterize chronic risk to estuarine/marine invertebrates from exposure to alpha

cypermethrin

.

3.3.1.5. Toxicity to Aquatic Plants

The acute toxicity of technical grade alpha

- cypermethrin to aquatic vascular plants was evaluated

for Lemna gibba , with a 96

- hour EC 50 

### greater than 1.39 μg a.i./L (MRID # 47944031 ; supplemental ). The acute toxicity of technical grade alpha

- cypermethrin to aquatic non

- vascular plants was evaluated for Skeletonema costatum , with a 96

- hour EC 50 

### greater than 33.5 μg a.i./L (MRID# 47994032 ; acceptable ). Additional supplemental studies are available for the aquatic

non

- vascular plants Anabaena flos

- aquae , Navicula pelliculosa , and Pseudokirchneriella supcapitata that indicate these species are not as sensitive to alpha

- cypermethrin as S. costatum

.

3. 3.2 Terrestrial Effects Characterization

The most sensitive acute and chronic toxicity reference values available for alpha

- cypermethrin exposure to mammals, birds, and terrestrial in vertebrate s are summarized in Table 3.1 4

. Where there are no chemical specific data for alpha

- c ypermethrin, data are bridged from the database available for the cypermethrins (racemic and zeta

- cypermethrin) as described in Appendix A

. The most sensitive measurement endpoints for alpha

- cypmermethrin exposure to terrestrial plants are presented in Tab le 3.1 5

. All acceptable and supplemental studies available for the registration of alpha

- cypermethrin are described below, and data are described in relation to the tested material (i.e., racemic cypermethrin, zeta

- cypermethrin, or alpha

- cypermethrin).

Table 3.14 Summary of most sensitive endpoints from submitted terrestrial toxicity studies for alpha

- cypermethrin.
Species (common

name) Taxa Represented Endpoint Effect Test

Substance

(% a.i.) Reference/

Classification Acute Toxicity

Classification- Page 45 of 126

- 

### Table 3.14 Summary of most sensitive endpoints from submitted terrestrial toxicity studies for alpha

- cypermethrin.
Species (common

name) Taxa Represented Endpoint Effect Test

Substance

(% a.i.) Reference/

Classification Acute Toxicity

Classification

Rattus norvegicus (Laboratory Rat) Mammals LD 50 = 86 mg a.i./kg

- bw Mortality TGAI MRID#

41776115 Acceptable Moderately

toxic

NOAEC = 5 mg a.i./kg/day Decrased F1 pup weight and

growth TGAI MRID#

00090040 Acceptable Not Applicable L OAEC = 25 mg a.i./kg/day

Bobwhite quail ( Colinus

virginianus )

Birds,

terrestrial

phase amphibians, and reptiles LD 50 >2 025 mg a.i./kg bw Mortality TGAI MRID#

47944015 Acceptable Practically

non

- toxic

Zebra finch ( Taeniopygia

guttata ) LD 50 = 1370 mg a.i./kg

- bw Mortality TGAI MRID

47944016 Supplemetnal Slightly toxic

Mallard duck ( Anas platyrhynchos ) LC 50 > 4690 mg a.i./kg diet Mortality TGAI MRID#

47944017 Acceptable Practically

non

- toxic

Bobwhite quail ( Colinus

virginianus )

Mallard duck ( Anas platyrhynchos ) NOAEC = 50 mg a.i./kg

- diet

No toxicity TGAI MRID#

00090073 Acceptable

MRID#

00090074 Acceptable Not Applicable

LOAEC > 50 mg a.i./kg

- diet TGAI Not Applicable

Apis mellifera

(Honey bee) Terrestrial

invertebrates Contact LD 50 = 0.023 μg a.i./bee Moratlity TGAI

Acc. No.

260647 Acceptable Very highly

toxic

Oral

LD 50 = 0.172 μg

a.i./bee Mortality TGAI Very highly

toxic



### Table 3.1 5 Summary of most sensitive endpoints from submitted terrestrial plant toxicity studies for alpha

- cypermethrin

.

Crop Species Endpoint Concentration Test

Substance Reference/

Classification Seedling Emergence

N/A N/A N/A N/A N/A N/A
Vegetative Vigor

Monocot Onion EC 25 > 0.0266 lbs a.i./A Fresh weight TGAI MRID

47944210 Supplemental NOAEC < 0.00333 lbs a.i./A TGAI- Page 46 of 126

- Dicot Oilseed Rape EC 25 > 0.0266 lbs a.i./A Fresh weight TGAI

NOAEC 0.0133 lbs a.i./A TGAI



### 3.3.2.1. Toxicity to Mammals

Mammalian toxicity data submitted to the Agency ’ s Health Effects Division (HED) are used to approximate toxicity to wild mammals. These studies are typically conducted with laboratory rats ( Rattus norvegicus ) or mice ( Mus musculus ). No studies evaluating toxicity to wild mammal species are available, or have been submitted to the Agency for any o f the cypermethrins.

Available mammalian studies were presented in the HED chapter of the Reregistration Eligibility Decision Document (RED) for cypermethrin (US EPA, 2006).

The reported laboratory rat acute oral LD 50 

### value is 86 mg/kg

- bw for racemic cypermethrin (MRID 41776115). The acute dermal LD 50 

### >4920 mg/kg /day for racemic cypermethrin, based on a study conducted with rats (MRID 00056800). An acute inhalation study conducted with rats

resulted in an LC 50 

### >2.5 mg/L for cypermethri n (MRID 4239570 2). Based on the reported laboratory rat oral LD 50 

### value , cypermethrin has moderate acute toxicity to small mammals.

In the available 3

- generation rat reproduction study, the NOAEL is 5 mg/kg/day based on decreased F1 pup body weight and body weight gain (MRID 00090040). In the submitted chronic mammalian dietary study with racemic cypermethrin, the NOAEL is 6 mg/kg/day based on clinical signs of neurotoxicity and mortality in males at the 20.4 mg/kg/day treatment level

and dec r eased body weights in female s at the 18.1 mg/kg/day treatment level (MRID 44536801).

3.3.2.2. Toxicity to Birds

The results of the single acute oral toxicity study available for the cypermethrins indicate that the

racemic cypermethrin is practically non

- toxic to avian species on an acute oral basis. The acute

oral LD 50 

### value for bobwhite quail ( Colinus virginianus ) is >2000 mg a.i./kg

- bw and no clinical signs of toxicity were observed at any treatment level (MRID 44546024).

A cute oral t oxicity of alpha

- cypermethrin to a passerine species was evaluated for the zebra finch ( Taeniopygia guttata ) . The study (MRID 47944016) is classified as supplemental for qualitative use only. In addition to signs of stress in all treatment and control grou ps, diarrhea was evident in all treatment groups, calling into question the effective dose received by the animals. However, results of this study indicate that alpha

- cypermethrin is slightly toxic to passerine birds (LD 50 

### = 1370 mg a.i./kg

- bw).

The resul ts of the sub

- acute dietary toxicity studies available for alpha

- cypermethrin and racemic cypermethrin indicate that they can be classified as practically non

- toxic to avian species on an acute dietary basis. The LC 50 

### for cypermethrin is greater than 2,634 mg a.i./kg

- diet for mallard

duck ( Anas platyrhynchos ) (MRID 00090071) and and LC 50 

### for alpha

- cypermethrin is greater- Page 47 of 126

- 

### than 4,690 mg a.i./kg

- diet for bobwhite quail (MRID 47944017) . In th ese stud ies , the LC 50 

### value was determined based on the repellent nature of the treated feed, which resulted in decreased food consumption and body weight.

The results of avian reproduction studies available for racemic cypermethrin showed no adverse effects at 50 mg a.i./kg

- diet, which was the highest dose tested.

3.3.2.3. Toxicity to Terrestrial Invertebrates

The Agency guidelines for terrestrial invertebrate tests are for honey bees ( Apis mellifera ). The

acute contact LD 50 

### value for alpha

- cyperemthrin is 0. 0 33 μg a.i./ bee and the oral LD 50 

### value for racemic cypermethrin is 0.172 μg a.i./bee (Accession Number 260647). Based on these results,

the alpha

- cypermethrin and racemic cypermethrin are classified as ‘highly toxic’ to honey bees on an acute exposure basis.

In addition, the Agency received one semi

- field study and one field study for the honey bee (MRIDs 47944204 and 47944206, respectively; both are classified as supplemental for qualitative use only). Though there are certain limitations with these studies, including a lack of residue analysis to confirm the integrity and independence of the control and treatment groups, they do provide information on the risks of alpha

- cypermethrin exposure to honey bees. Both studies suggest that honey bee mortality increases after exposure to alpha

- cypermethrin in a

semi

- field or field setting.

3.3.2.4. Toxicity to Terrestrial Plants

The acut e toxicity of technical grade alpha

- cypermethrin to terrestrial plants was evaluated for monocots (onion, Allium cepa ; and oat, Avena sativa ) and dicots (pea, Pisum sativum ; oilseed

rape, Brassica napus ; carrot, Daucus carota ; and sunflower, Helianthus ann uus ). The study (MRID 47944210) is classified as supplemental for qualitative use only because a definitive

EC 25 

### and NOAEC were not determined for the most sensitive monocot endpoint (onion fresh weight), in addition to other guideline deviations ( e.g., st udy was conducted with TGAI instead of the recommended TEP) . However, a definitive NOAEC value of 0.0133 lbs a.i/A was determined for the most sensitive dicot endpoint (oilseed rape fresh weight) . Th is NOAEC value represents roughly half of the maximum sin gle application rate for the proposed uses of alpha

cypermethrin and suggests that risks to plants may be possible . This information may be used in risk characterization for plants.

4. Risk Characterization

4.1. Risk Estimation

Toxicity data and exposur e estimates are used to evaluate the potential for adverse ecological

effects on non

- target species. This screening

- level assessment for alpha

- cypermethrin relies on the deterministic RQ method to provide a metric of potential risks. The RQ provides a comparison of exposure estimates to toxicity endpoints ( i.e. , the estimated exposure- Page 48 of 126

- 

### concentrations are divided by acute and chronic toxicity values). The resulting unitless RQs are compared to the Agency’s LOCs, as shown in Table 2.3

. LOCs are used by t he Agency to indicate when the use of a pesticide, as directed by the label, has the potential to cause adverse

effects to non

- target organisms.

4.1.1. Aquatic Organisms

The highest scree n ing

- level aquatic EEC s based on the maximum application rates f or each proposed use pattern w ere used to derive RQs. These exposure estimates represent

concentrations in surface water ( Table 3. 9 ). Peak EECs are used to represent acute exposure to fish, aquatic invertebrates, and aquatic plants, and the highest 21

- da y and 60

- day average EECs represent chronic exposure to aquatic invertebrates and f ish, respectively. Because of alpha

cypermethrin’s persistence, each subsequent year may be affected by the previous year’s application.

4.1.1.1. Fish and Invertebrates

Table 4.1 lists RQs calculated for fish and invertebrates (freshwater and estuarine/marine) exposed to alpha

- cypermethrin , based on the acute EECs generated from PRZM /EXAMS and

Tier I Rice Model modeling scenarios. Results of acute toxicity studies in fr eshwater and

estuarine/marine fish ( Table 3.13 ) indicate that alpha

- cypermethrin is “highly toxic” to freshwater fish on an acute exposure basis

. RQ s for freshwater and estuarine/marine fish are above the Agency’s acute risk to listed species LOC (0. 0 5) for the proposed uses of alpha

cypermethrin, as well as the Agency’s acute risk to non

- listed species LOC of 0.5 for some of the

p roposed uses

. RQs for freshwater and estuarine/marine invertebrates are all well above the

acute risk to non

- listed species LOC for all of the proposed uses.- Page 49 of 126

- 

### Table 4.1. Acute Risk Quotients for Fish and Invertebrates Exposed to Alpha

- Cypermethrin at the Highest EECs Using the Most Sensitive of the Available Endpoints.

Use EECs (ppb) Freshwater Fish RQs

LC 50 = 2.2 μg ai/L Freshwater Invertebrate RQs

LC 50 = 0.0036 μg

ai/L Estuarine/Marine Fish RQs

LC 50 = 0.95 μg

ai/L Estuarine/Marine Invertebrate RQs

LC 50 = 0.00475 μg

ai/L

Peak Acute 1,2 Acute 1,2 Acute 1,2 Acute 1,2

Alfalfa 0.04 0. 02 11.11 1 0.04 8.42 1

Brassica vegetables 3 0.07 0. 03 19.44 1 0.07 2 14.74 1

Citrus fruit 0.17 0. 08 2 47.22 1 0.18 1 35.79 1

Corn (field, pop, seed) 0.32 0. 15 2 88.89 1 0.34 1 67.37 1

Corn (sweet) 0.45 0.21 2 125.00 1 0.47 2 94.74 1

Cotton 0.62 0.28 2 172.22 1 0.65 1 130.53 1

Legume vegetables 0.25 0.11 2 69.44 1 0.26 2 52.63 1

Root and tuber vegetables 0.08 0.04 22.22 1 0.08 2 16.84 1

Sorghum (and other cereals) 0.21 0.10 2 58.33 1 0.22 2 44.21 1

Sugar beets 0.08 0.04 22.22 1 0.08 2 16.84 1

Tomato 0.08 0.04 22.22 1 0.08 2 16.84 1

Tree nuts 0.20 0.09 2 55.56 1 0.21 2 42.11 1

Wheat 0.08 0.04 22.22 1 0.08 2 16.84 1

Rice (Tier I Rice Model) 0.54 0.24 2 150.00 1 0.57 1 113.68 1

1 Acute risk to non

- listed species LOC for aquatic fish is 0.5

2 Acute risk to listed species LOC for aquatic fish is 0.05

3 Use represents brassica vegetables, cucurbits, fruiting vegetables, leafy vegetables, soybeans, and sugar beets.



### Table 4. 2 lists the chronic RQs for fish and invertebrates (freshwater and estuarine/marine) exposed to alpha

- cypermethrin. RQs for chronic exposures to freshwater and estuarine/marine

fish fell below the Agency’s chronic risk to listed and non

- listed species LOC (1.0) for all of the proposed uses of alpha

- cypermethrin except for the proposed use on rice

. However, RQs for

chronic exposures to freshwater and estuarine/marine invertebrates are well above the chronic

risk to listed and non

- listed species LOC. The Tier I rice model only calculates a peak concentration in the water that is released from the rice field immediately follo wing application of the compound. Therefore, chronic EECs can only be estimated less than the peak since there would be some amount of degradation and/or dissipation between when the peak occurs (immediately following application) and 21 or 60 days followi ng the application.- Page 50 of 126

- 

### Table 4.2. Chronic Risk Quotients for Fish and Invertebrates Exposed to Alpha

Cypermethrin at the Highest EECs Using the Most Sensitive of the Available Endpoints.

Use EECs (ppb) Freshwater Fish RQs

NOAEC = 0.14 μg ai/L Freshwater Invertebrate RQs

NOAEC = 0.00059 μg ai/L Estuarine/Marine Fish RQs

NOAEC = 0. 06 μg ai/L Estuarine/Marine Invertebrate RQs

NOAEC = 0.000781 μg ai/L

21

- day 60

- day Chronic Chronic Chronic Chronic

Alfalfa 0.01 0.004 0.03 16.95 0. 0 7 12.80

Brassica vegetables 1 0.01 0.01 0.07 16.95 0. 16 12.80

Citrus fruit 0.02 0.01 0.07 33.90 0. 16 25.61 Corn (field, pop, seed) 0.03 0.02 0.14 50.85 0. 33 38.41

Corn (sweet) 0.04 0.03 0.21 67.80 0. 50 51.22

Cotton 0.06 0.03 0.21 101.69 0. 50 76.82 Legume vegetables 0.03 0.01 0.07 50.85 0. 16 38.41

Root and

tuber vegetables 0.02 0.01

0.07 33.90 0. 16 25.61 Sorghum (and other

cereals) 0.03 0.02

0.14 50.85 0. 33 38.41 Sugar beet 0.01 0.01 0.07 16.95 0. 16 12.80

Tomato 0.01 0.01 0.07 16.95 0. 16 12.80

Tree nuts 0.02 0.01 0.07 33.90 0. 16 25.61

Wheat 0.01 0.01 0.07 16.95 0. 16 12.80

Rice (Tier I Rice

Model) <0.54 <0.54 NA NA NA NA

1 Use represents brassica vegetables, cucurbits, fruiting vegetables, leafy vegetables, soybeans, and sugar beets.

Bold values greater than chronic risk to listed and nonlisted aquatic animals LOC of 1.0 NA = Not applicable, Tier I rice model is not able to calculate.



### Table 4. 3 lists the acute and chronic RQs calculated for benthic organisms exposed to alpha

cypermethrin in pore water , based on the acute EECs generated from PRZM /EXAMS

. Results

of sub

- chronic toxicity studies in benthic organisms ( Table 3.13 ) indicate that alph a

cypermethrin is “highly toxic” to benthic invertebrates on an acute exposure basis

. Sub

- chronic

and c hronic RQs for benthic organisms are above the Agency’s acute and chronic risk to listed

and non

- listed species

.- Page 51 of 126

- 

### Table 4. 3 . Acute and Chronic Risk Quotients for Benthic Invertebrates Exposed to Alpha

- Cypermethrin at the Highest EECs Using the Most Sensitive of the Available Endpoints.

Use Pore Water EECs (ppb) Benthic Invertebrate RQs

LOAEC = 0.00 182 μg ai/L Benthic Invertebrate RQs

NOAEC = 0.000 781 μg ai/L

21

- day Sub

- Chronic 2 Chronic

Alfalfa 0.001 > 0.55 1.28

Brassica vegetables 1 0.001
> 0.55 1.28

Citrus fruit 0.002 > 1.10 2.56 Corn (field, pop, seed) 0.004
> 2.20 5.12
Corn (sweet) 0.007 > 3.85 8.96

Cotton 0.007 > 3.85 8.96 Legume vegetables 0.003
> 1.65 3.84

Root and

tuber vegetables 0.002

> 1.10 2.56 Sorghum (and other

cereals) 0.004

> 2.20 5.12

Tree nuts 0.004 > 2.20 5.12

Wheat 0.001 > 0.55 1.28

1 Use represents brassica vegetables, cucurbits, fruiting vegetables, leafy vegetables, soybeans, and sugar beets.

2 S ince the most sensitive toxicity endpoint from the s ub

- chronic benthic invertebrate study is a non

- definitive endpoint, RQs represent the minimum RQ possible

. The magnitude of the true RQ is uncertain.

Bold values greater than chronic risk to listed and nonlisted aquatic animals LOC of 1.0



### 4.1.1. 2

. Aquatic Plants

Although alpha

- cypermethrin does exhibit effects on both Lemna gibba and Skeletonema

costatum , these effects are at much higher concentrations than those estimated for the highest proposed alpha

- cypermethrin uses. For both taxa, both listed and nonlisted RQs are <0.01, while

the LOCs are 1.0.

4.1.2. Terrestrial Organisms

4.1.2.1. Mammals

Acute and chronic dose

- based and chronic dose

- based RQs were calculated for the proposed new chemical uses of alpha

- cypermethrin based on the information shown in Table 3.9

. Dose

- based acute mammalian RQs for the proposed new uses of alpha

- cypermethrin range from < 0.01 to 0.16 (as shown in Table 4.2 )

. Most proposed uses result in acute l isted species LOC exceedances, except for proposed uses on alfalfa and wheat. RQs that exceed the listed species

LOC are for small and medium sized mammals exposed to alpha

- cypermethrin on short grass only. LOCs were not exceeded for mammals exposed to alpha

- cypermethrin on tall grass, broadleaf plants, small insects, fruits, pods, large insects, or seeds.- Page 52 of 126

- 

### Table 4.2. Mammalian Dose

- Based Acute RQ Values for New Uses of Alpha

- Cypermethrin

.

Use Application

Rate

lbs ai/A ( #app ) Body Weight

(g) Mammalia n Acute Dose

- based RQs for Specified Food Items

Short

Grass Tall Grass Broadleaf

Plants/Small

Insects Fruits/Pods /Lg Insects Seeds

Alfalfa 0.025 (3) 15 0.08 0.04 0.04 < 0.01 < 0.01

35 0.07 0.03 0.04 < 0.01 < 0.01

1000 0.04 0.02 0.02 < 0.01 < 0.01

Brassica vegetables 1 0.025 (6) 15 0.13 0.06 0.07 0.01 < 0.01

35 0.11 0.05 0.06 0.01 < 0.01

1000 0.06 0.03 0.03 < 0.01 < 0.01

Citrus fruits 0.025 (8) 15 0.11 0.05 0.06 0.01 < 0.01

35 0.10 0.04 0.05 0.01 < 0.01

1000 0.05 0.02 0.03 < 0.01 < 0.01

Corn (field, pop, seed) 0.025 (4) 15 0.11 0.05 0.06 0.01 < 0.01

35 0.09 0.04 0.05 0.01 < 0.01

1000 0.05 0.02 0.03 < 0.01 < 0.01

Corn (sweet) 2 0.025 (6) 15 0.16 0.07 0.09 0.01 < 0.01

35 0.13 0.06 0.08 0.01 < 0.01

1000 0.07 0.03 0.04 < 0.01 < 0.01

Legume vegetables 0.025 (6) 15 0.14 0.07 0.08 0.01 < 0.01

35 0.12 0.06 0.07 0.01 < 0.01

1000 0.07 0.03 0.04 < 0.01 < 0.01

Rice (grai n
, straw) 0.025 (4) 15 0.10 0.05 0.06 0.01 < 0.01

35 0.09 0.04 0.05 0.01 < 0.01

1000 0.05 0.02 0.03 < 0.01 < 0.01

Root and

tuber vegetables (except sugar beet) 0.025 (6) 15 0.15 0.07 0.08 0.01 < 0.01

35 0.13 0.06 0.07 0.01 < 0.01

1000 0.07 0.03 0.04 < 0.01 < 0.01

Sorghum (and other cerials) 0.025 (5) 15 0.11 0.05 0.06 0.01 < 0.01

35 0.09 0.04 0.05 0.01 < 0.01

1000 0.05 0.02 0.03 < 0.01 < 0.01

Tree nuts 0.025 (5) 15 0.12 0.05 0.07 0.01 < 0.01

35 0.10 0.05 0.06 0.01 < 0.01

1000 0.05 0.02 0.03 < 0.01 < 0.01

Wheat 0.025 (5) 15 0.09 0.04 0.05 0.01 < 0.01

35 0.08 0.04 0.05 0.01 < 0.01

1000 0.04 0.02 0.02 < 0.01 < 0.01

1 Use represents brassica vegetables, cucurbits, fruiting vegetables, leafy vegetables, soybeans, and sugar beets.

2 Use represents corn (sweet) and cotton.

Bolded value indicates that the acute listed species LOC is exceeded (RQ > 0.1)

.



### Chronic d ose

- based mammalian RQs for the proposed new uses of alpha

- cypermethrin range from 0.01 to 2.71 (as shown in Table 4. 3 ) . All proposed uses result in chronic non

- listed and listed species LOC exceedances for small and medium sized mammals exposed to alpha

c ypermethrin on short grass. Chronic non

- listed and listed species LOCs are also exceeded for small and medium sized mammals exposed to alpha

- cypermethrin on tall grass, broadleaf plants,- Page 53 of 126

- 

### and small insects for some of the proposed uses. RQs are higher for s maller mammals due to an increased food ingestion rate associated with the higher met abolic rate of smaller mammals.

Table 4. 3

. Mammalian Dose

- Based Chronic RQ Values for New Uses of Alpha

Cypermethrin

.

Use Application

Rate

lbs ai/A ( #app ) Body Weight

(g) Mammalia n C hronic Dose

- based RQs for Specified Food Items

Short

Grass Tall Grass Broadleaf

Plants/Small

Insects Fruits/Pods /Lg Insects Seeds

Alfalfa 0.025 ( 3 ) 15 1.37 0.63 0.77 0.09 0.02

35 1.17 0.54 0.66 0.07 0.02

1000 0.63 0.29 0.35 0.04 0.01

Brassica vegetables 1 0.025 ( 6 ) 15 2.27 1.04 1.28 0.14 0.03

35 1.94 0.89 1.09 0.12 0.03

1000 1.04 0.48 0.58 0.06 0.01

Citrus fruits 0.025 ( 8 ) 15 1.92 0.88 1.08 0.12 0.03

35 1.64 0.75 0.92 0.10 0.02

1000 0.88 0.40 0.49 0.05 0.01

Corn (field, pop, seed) 0.025 ( 4 ) 15 1.91 0.87 1.07 0.12 0.03

35 1.63 0.75 0.92 0.10 0.02

1000 0.87 0.40 0.49 0.05 0.01

Corn (sweet) 2 0.025 (6) 15 2.71 1.24 1.52 0.17 0.04

35 2.31 1.06 1.30 0.14 0.03

1000 1.24 0.57 0.70 0.08 0.02

Legume vegetables 0.025 (6) 15 2.47 1.13 1.39 0.15 0.03

35 2.11 0.97 1.19 0.13 0.03

1000 1.13 0.52 0.64 0.07 0.02

Rice (grai n
, straw) 0.025 (4) 15 1.71 0.78 0.96 0.11 0.02

35 1.46 0.67 0.82 0.09 0.02

1000 0.78 0.36 0.44 0.05 0.01

Root and

tuber vegetables (except sugar beet) 0.025 (6) 15 2.59 1.19 1.45 0.16 0.04

35 2.21 1.01 1.24 0.14 0.03

1000 1.18 0.54 0.67 0.07 0.02

Sorghum (and other cerials) 0.025 (5) 15 1.82 0.83 1.02 0.11 0.03

35 1.56 0.71 0.87 0.10 0.02

1000 0.83 0.38 0.47 0.05 0.01

Tree nuts 0.025 (5) 15 2.01 0.92 1.13 0.13 0.03

35 1.72 0.79 0.97 0.11 0.02

1000 0.92 0.42 0.52 0.06 0.01

Wheat 0.025 (5) 15 1.61 0.74 0.91 0.10 0.02

35 1.38 0.63 0.77 0.09 0.02

1000 0.74 0.34 0.42 0.05 0.01

1 Use represents brassica vegetables, cucurbits, fruiting vegetables, leafy vegetables, soybeans, and sugar beets.

2 Use represents corn (sweet) and cotton.

Bolded value indicates that the chronic LOC (RQ > 1) for non

- listed and listed mammalian species is exceeded.



### Chro nic dietary

- based RQs are based on effects associated with chemical concentrations in feed.

C hronic dietary

- based RQs are well below the non

- listed and listed species LOCs for the proposed new chemical uses of alpha

- cypermethrin (RQs range from 0.01 to 0.31)

. Therefore- Page 54 of 126

- 

### risks to mammalian species from chronic dietary exposure to alpha

- cypermethrin is expected to

be low.

4.1.2.2. Birds

Acute RQs were not calculated for birds because only non

- definitive acute and sub

- acute t o xicity endpoints are available. Alpha

- cypermethrin is categorized as practically non

- toxic to mallard duck and bobwhite quail on an acute and subacute oral and dietary basis. A cu te risk to avian species is expected to be low.

Chronic

- based avian RQs are based on effects associated with chemical concentrations in feed. Chronic dietary

- based RQs are well below the non

- listed and listed species LOCs for the proposed new chemical uses of alpha

- cypermethrin (RQs range from 0.0 2 to 0. 62 ). Therefore chronic risks to avian species are expected to be low.

4.1.2.3

. Terrestrial Invertebrates

Risk assessments are not conducted for ter restrial invertebrates at the screening

- level at this time.

Characterization of exposure relative to known toxicity endpoints for terrestrial invertebrates will be discussed in the Risk Description section

.

4.1.2.4

. Non

- target Terrestrial Plants

Potential effects to riparian and upla nd vegetation are assessed deriving RQs from terrestrial plant seedling emergence and vegetative vigor EC 25 

### and NOEAC endpoints . Based on the

results of the submitted supplemental terrestr ial plant toxicity tests for technical grade alpha

cypermethrin

, there is the potential for effects to occur at proposed label rates . The maximum proposed single application rate for alpha

- cypermethrin is 0.025 lbs a.i./A, which is nearly

double the no e ffect concentration for dicot s pecies (NOAEC = 0.0133 lbs a.i./A for oilseed rape fresh weight ) . However, deficiencies in this study described in Section3.3.2.4 make it unsuitable for use in calculating RQs, so risks to terrestrial plants from the proposed new chemical uses

remains unce rtain.

4.2. Risk Description

The results of risk estimation i ndicate that proposed uses of alpha

- cypermethrin are likely to adversely affect non

- listed fish and aquatic invertebrates on both an acute and chronic exposure

basis , while risks to aquatic plants are low

. In addition, the results indicate that proposed uses of alpha

- cypermethrin have the potential to affect non

- listed and listed terrestrial mammals.

However

, risk s to terrestrial birds appear to be below the Agency’s levels of concern.

4. 2.1 Exposure to Aquatic Organisms- Page 55 of 126

- 

### The Tier II model Pesticide Root Zone Model (PRZM v3.12.2; May 12, 2005; Carousel et al.

, undated) linked with EXposure Analysis Modeling System (EXAMS v2.98.4.6; Apr. 25, 2005; Burns, 2004) via the PRZM/EXAMS model shell (PE v5.0, Nov. 15, 2006), i.e.

, PRZM/EXAMS) and the Tier I Rice Model (v1.0, May 8, 2007) were used to estimate screening

level exposure concentrations in aquatic environments. The PRZM model simulates pesticide

movement and transformation on and across the agricultural field resulting from crop applications. The EXAMS model simulates pesticide concentrations in water due to loading via runoff, erosion, and spray drift, assuming a standard 1

- ha pond, 2

- m deep (20,000 m 3 

### ) with no

outlet that borders a 10

- ha treated field. Simulations are for multiple (usually 30) years, from which the Agency estimates peak values that are expected to recur on average once every ten years, based on time series of daily estimated concentrations.

The Tier I Rice Model was used to estimate screening

- level exposure to alpha

- cypermethrin that may occur in water bodies receiving release water from rice paddies that were treated with alpha

cypermethrin. This model was used to assess the proposed use on rice seed because the

PR ZM/EXAMS exposure models do not specifically address the unique rice growing environment and the model is approved for use in risk assessment. The model produces a single exposure value that represents a dissolved concentration within a rice paddy. This single value is used to approximate both acute and chronic exposures.

Model uncertainties are discussed in greater detail in Section 4.3

.

4.2.2 Risks to Aquatic Animals

This risk assessment of alpha

- cypermethrin shows that aquatic systems are potentially at risk from acute and chronic toxic exposure to this chemical. Evaluation of this risk to aquatic organisms was approached by dividing the aquatic system into two general compartments, the

water co lumn and the benthos.

The first compartment, the water column, which is defined as the aquatic area between surface and the benthos (approximately 6 inches above the bottom) represents an area where organisms

are free

- swimming and can feed and breed at t he surface, mid water and/or on the benthos (sediment). Direct pesticidal contact (e.g., gill lamella, ingestion, and integument) to these organisms is assumed to be from the surface water via drift and/or runoff. The toxicity assessment points are the acu te LC 50 

### / EC 50 

### and chronic NOAEC that are generated through standard water column toxicity tests.

The second aquatic compartment to be considered is the benthos, which is composed of sediments and an area 6 inches above the sediment (epibenthos). The bent hos is composed of a diversity of aquatic invertebrates (e.g., insect larvae, crustaceans, mollusks) and species of fish (e.g., catfish, loachs), as well as certain critical life stages of organisms that reside in the water column; the benthos is also the initial breeding strata and nursery area for several species of fish, especially commercial species such as salmonids. The benthos can also be a source of food- Page 56 of 126

- 

### items for several species of fish that are actively feeding on the organisms in the sediment an d/or capturing organisms that are emerging from this area.

Aquatic Animals: Water Column Exposure

Several freshwater fish acute exposure studies were submitted to the Agency for racemic cypermethrin TGAI using the rainbow trout , all indicating that racemic cypermethrin is highly

toxic to freshwater fish

. Additionally, there is a study, also conducted with the rainbow trout, that was conducted using the BASF 310 40 I product (a single ai formulation). This study resulted in an endpoint similar to t he TGAI study ( 2.2 μg ai/L vs 0. 39 μg ai/L), indicating that inert ingredients in the formulation do not enhance alpha

- cypermethrin’s toxicity to fish. T he most sensitive endpoint derived from the available alpha

- cypermethrin studies w as compared to the highest expected aquatic exposure values, and all are above the Agency’s levels of concern

. Rainbow trout was the most sensitive species to alpha

- cypermethrin among those studied, with

an LC 50 

### of 0. 39 μg ai/L, and resulted in RQ s that ran ged from 0.15 to 1.38 . These RQs are all greater than the non

- listed species LOC

.

For estuarine/marine fish, t he acute toxicity of technical grade racemic cypermethrin was evaluated in sheepshead minnow and Atlantic salmon, with 96

- hour LC 50 

### values of 0 .95 μg a.i./L (MRID 00090075) and 4.3 μg a.i./L (MRID 41968212) respectively, indicating that the racemic cypermethrin TGAI is very highly toxic to estuarine/marine fish on an acute basis. The most sensitive endpoint derived from the available studies was compared to the highest expected aquatic exposure values, resulting in RQs above the Agency’s levels of concern (ranging from 0.17 to 0.57).

Although there is a definitive endpoint for chronic exposure to freshwater fish from a study with fathead minnow, a chronic exposure endpoint for estuarine/marine fi sh is not available

. Therefore, an acute to chronic ratio (ACR) from the freshwater fish studies (~3 X) was applied to
th e available acute estuarine/marine fish endpoint

. C hronic RQ s for freshwater and estuarine/marine fish are all well below the Agency’s level of concern for all proposed uses.

Acute toxicity studies of technical grade racemic cypermethrin to freshwater i nvertebrates

available include a 96

- hour LC 50 

### value for zeta

- cypermethrin of 0.0036 μg a.i./L in Hyalella

azteca (MRID 44423501), a 48

- hour EC 50 

### value for racemic cypermethrin of 0.42 μg a.i./L in in daphnid (MRID 44546031) and a 48

- hour EC 50 

### value for a lpha

- cypermethrin of 0.067 μg a.i./L om daphnids (MRID 47944208). Available information on BASF 310 40 I product (a single ai formulation of alpha

- cypermethrin) indicates that the inert ingredients in the formulation do not enhance the toxicity of alpha

- cypermethrin to freshwater invertebrates. For estuarine/marine invertebrates, t he acute toxicity of technical grade cypermethrin was evaluated

in shrimp, molluscs, and crustaceans. Based on these studies , alpha

- cypermethrin can be categorized as very highl y toxic on an acute basis to freshwater and estuarine/marine

invertebrates

. The most sensitive endpoint derived from the available studies was compared to the highest expected aquatic exposure values

. R esulting RQs greatly exceed the Agency’s levels

of co ncern for listed and non

- listed species (ranging from 16.7 to 150 , for freshwater species, and- Page 57 of 126

- 

### from 12.6 to 113 for estuarine/marine species ) , indicating that freshwater and estuarine/marine invertebrates are at risk from exposure to alpha

- cypermethrin

.

Although there is a definitive endpoint for chronic exposure to estuarine/marine invertebrates from a study with the mysid shrimp , a chronic exposure endpoint for freshwater invertebrates is not available. Therefore, an acute to chronic ratio (ACR) from the estuarine/marine invertebrate studies (~ 2 X) was applied to the available acute freshwater invertebrate endpoint . Chronic RQs

for freshwater and estuarine/marine invertebrates range from 16.95 to 101.69 and from 12.8 to 76.8, respectively

.

Aquatic A nimals: Sediment Exposure

Risk estimates for benthic organisms show that alpha

- cypermethrin poses sub

- chronic and chronic risks to benthic organisms, based on sub

- chronic and chronic RQs calculated using pore water EECs ( Table 4.3 ). However, it should be noted that there are uncertainties regarding acute and chronic risk estimates for benthic organisms. First, the sub

- chronic NOAEC value for p ore water and the chronic NOAEC for pore water that were used to generate RQs were not

determined in controlled l aboratory studies. Rather, sub

- chronic RQs for pore water were derived using a toxicity value estimated with the Equilibrium Partitioning Theory and the

definition of the K

oc 

### , and the chronic RQs for pore water were generated based on the NOAEC

value for the mysid shrimp (details provided in the Ecological Effects Characterization section and the previous section entitled, Aquatic Animals: Water Column Exposure).

Second, the sub

- chronic sediment toxicity value (in terms of whole sediment) used to estima te risk and to generate acute pore water and chronic pore water and sediment toxicity values was obtained from a study using a water

- sediment system that was not at equilibrium; sediment concentrations decreased throughout the exposure period. Since resid ues that have reached equilibrium in the pore water are considered a greater source of toxic risk to benthic invertebrates (Di Toro et al. , 1991), the studies presented in this assessment may underestimate sediment toxicity and equilibration should have oc curred for at least one month prior to testing. If the exposure system had been at equilibrium, it is likely that the sub

- chronic and chronic toxicity reference values for sediment and pore water would be lower, resulting in RQs that are higher than those derived in this assessment. However, even with these uncertainties, there are

sub

- chronic and chronic risks to benthic organisms for all modeled crop uses.

Based on the available sub

- chronic toxicity data (the lowest sub

- chronic NOAEC for benthic organi sms; < 0.00 182 μg a.i./L pore water and < 1.8 μg a.i./kg sediment), it is expected that a 21

- day pore water EEC of approximately 0.00 181 μg a.i./L pore water would be sufficiently low to

achieve sub

- chronic RQ values for all benthic organisms that are less than the endangered species LOC ( 1.0 ). This means that the highest peak pore water and sediment EEC of 0.00 7 μg a.i./L pore water would have to be reduced by ~ 74.1 %.

Based on the available chronic toxicity data (the lowest chronic NOAEC for benthic organ isms

of 0.000 781 μg a.i./L pore water), it is expected that a 21

- day pore water EEC of approximately- Page 58 of 126

- 

### 0.000 78 0 ppb would be sufficiently low to achieve chronic RQ values for all benthic organisms that are less than the chronic LOC (1). This means that th e h ighest 21

- day pore water EEC of

0.00 7 μg a.i./L pore would have to be reduced by ~ 88.8 %.

Aquatic Animals: Mesocosm Studies

In addition to the aquatic animal guideline studies, the Agency received two mesocosm studies that provide information on the potential lingering effects of alpha

- cypermethrin to water column and benthic dwelling invertebrates under more realistic environmental conditions . In the first study (MRID 48425009; supplemental), t hree stainless steel tanks were established for this

meso cosm study. Two of the three tanks were treated with FASTAC (alpha

- cypermethrin) , at nominal concentrations of 1.8 and 2.4 μg/L; the third served as a negative control. Detected alpha

- cypermethrin concentrations fell from 1.17 μg/L to 0.02 μg/L by day 16 with radioactively labeled benzyl (lesser nominal concentration), and from 1.24 μg/L (measured on day two) to 0.04 μg/L on day 16 with the radioactively labeled cyclopropyl (higher nominal concentration). The study authors report the alpha

- cypermethrin h alf

- life in water as two to three days. In sediment, the radioactively labeled alpha

- cypermethrin concentrations increased from day 0, with maximum concentrations of FASTAC recorded on day 16 (0.36 and 0.49 μg/core (assessed for the top cm of the sediment core) for benzyl and cyclopropyl labels, respectively). I n situ bioassays with Gammarus pulex revealed acute toxicity, with 100% mortality within 24 hours of first exposure through day 16 for cages suspended in the solution. For Gammarus in cages resting on the sediment surface, no organism survived for more than 24 hours for the first 27 days following treatment, and 96 hour mortality exceeded control mortality through day 105.

In the second study (MRID 48425010; supplemental), t hree po nds (10m x 5m x 0.8m water depth), two treatment and one negative control, were established to study the fate and effects of FASTAC (100g/L emulsifiable concentrate) in the aquatic environment. The two treatment ponds were each treated at a rate of 15 g a .i./ha; one through direct incorporation, the other oversprayed. FASTAC residues in water and sediment, and toxicity to Gammarus pulex were assessed at various points throughout the study. Recovery of FASTAC from the treated ponds ranged from 0.36 to 0.0 3 μg/L and from 1.09 to 0.04 μg/L on days one and eight for the overspray and sub

- surface applications respectively. Analysis of sediment samples determined FASTAC concentrations on day 16 as 5% of the total applied; falling to <2% of the concentration ap plied by day 47. FASTAC concentrations in the treatment ponds were acutely

toxic to Gammarus through day 4, and lethality was observed for all animals within 24 hours of exposure. Acute toxicity was observed to a lesser degree through day 33.

4.2.3 R isks to Aquatic Plants

Based on the available information on Lemna gibba and Skeletonema costatum , the proposed

uses of alpha

- cypermethrin do not exceed the Agency’s LOC for aquatic plant (1.0) for nonlisted or listed plants. While RQs were not calculate d in the Risk Estimation section due to the lack of

definitive IC 50 

### values, there were effects noted in the studies. The lowest NOAEC among the- Page 59 of 126

- 

### vascular and nonvascular studies is 1.39 μg ai/L for Lemna gibba (based on biomass and cell density). At that concentration, the RQ is less than 0.01 whereas the LOC is 1.0. In addition, supplemental studies using other aquatic nonvascular species indicate that they are less senstitive to alpha

- cypermethrin than L. gibba. Therefore, potential risk to aquatic plan ts from the proposed

uses of alpha

- cypermethrin is expected to be low.

4.2. 4

. Risks to Mammals

Dose

- based acute mammalian RQs for a ll proposed uses result in listed species LOC exceedances, except for proposed uses on alfalfa and wheat. RQs that exceed the listed species LOC are for small and medium sized mammals exposed to alpha

- cypermethrin on short grass only. In addition, dose

- based chronic RQs for a ll proposed uses result in chronic non

- listed and listed species LOC exceed ances for small and medium sized mammals exposed to alpha

cypermethrin on short grass . In addition, some of the proposed uses result in chronic non

- listead and listed species LOC exceedances for small and medium sized mammals exposed to alpha

cypermethrin on tall grass, broadleaf plants, and small insects . RQs are higher for smaller mammals due to an increased food ingestion rate associated with the higher metabolic rate of

smaller mammals. However, c hronic dietary

- based RQs are well below the non

- listed an d listed species LOCs for the proposed new chemical uses of alpha

- cypermethrin (RQs range from 0.01 to 0.31)

.

4.2. 5

. Risk to Birds

Acute RQs were not calculated for birds because only non

- definitive acute and sub

- acute toxicity endpoints are available. No t reatment

- related sublethal effects were observed in either mallard

duck or bobwhite quail studies at the highest concentrations t ested. Therefore, a lpha

cypermethrin is categorized as practically non

- toxic to mallard duck and bobwhite quail on an acute and subacute oral and dietary basis. However, a supplemental oral toxicity study with the

zebra finch indicate that alpha

- cypermet hrin may be slightly toxic to passerine bird species on an

acute basis (LD 50 

### = 1370 mg a.i./kg

- bw). Due to study deficiencies described in Section 3.2.2.2

it was not suitable for use in this risk assessment. C hronic dietary

- based RQs , based on the

availabl e chronic toxicity data for the mallard duck and bobwhite quail, are well below the non

listed and listed species LOCs for the proposed new chemical uses of alpha

- cypermethrin (RQs range from 0.02 to 0.62).

The potential for direct mortality of nonlisted and listed birds (and to terrestrial

- phase amphibian and reptiles for which birds serve as surrogates) from acute, subacute and chronic exposures of alpha

- cypermethrin for all proposed uses is not expected.

4.2. 6

. Potential Effects on Terrestrial Invertebrates

Although EFED does not quantitatively estimate risk to non

- target terrestrial invertebrates, risks can be assessed qualitatively. This hazard assessment shows that alpha

- cypermethrin exposure can be expected to result in acute toxicity to h oney bees and is considered to be highly toxic on- Page 60 of 126

- 

### both a contact (LD 50 

### = 0. 0 33 ug a.i./bee) and an oral basis (LD 50 

### = 0.172 ug a.i./bee). In addition to the acute exposure data, the Agency received asupplemental semi

- field study and a supplemental full fie ld study that provide information on the effects of alpha

- cypermethrin TEP to honey bees under more realistic environmental conditions for the hive. In the semi

- field study (MRID 47944204; supplemental) honey bee ( Apis mellifera ) brood and whole colonies w ere exposed to alpha

- cypermethrin by foliar application of the test material t o full bloom lacy phacelia ( Phacelia tanacetifolia ) at a nominal rate of 0.03 lb ai/A (30 g ai/ha) in 400 L water/ha. Fields, consisting of three treatment groups (negative contr ol, treated, and reference (ai: fenoxycarb) groups; each group contained three replicates), were covered with tunnel tents (12 x 5 x 3.5 m; area covered 60 m 2 

### ). The exposure phase was concluded 8 days after application and observations were continued up t o 20 days post

- application. Assessments of m ortality, flight intensity, behavior of the bees , strength of the colonies, and development of the bee brood were conducted throughout pre

- and post

- application. Results of the study indicate that alpha

cypermet hrin may result in significant effects on the mortality and early bee brood development at a rate of 0.03 lb ai/A (30 g ai/ha). Most of the adverse effects to honey bees observed were transient (e.g., mortality significantly elevated for one day following application but tailing off; and reduced foraging for two days after application but rebounding). However, the percentage of

brood terminated before a successful hatch (ca. 65%) indicates that alpha

- cypermethrin has potential to be of chronic concern to colony health.

In the field study (MRID 47944206; supplemental), honey bee ( Apis mellifera ) brood and whole

colonies were exposed to alpha

- cypermethrin TEP by foliar application of the test material t o full bloom lacy phacelia ( Phacelia tanacetifolia ) at a nominal rate of 0.03 lb ai/A (30 g ai/ha) in 400 L water/ha. Sample locations included a treatment plot (2000 m 2 

### ) and a control plot (2400 m 2 

### ). The exposure phase was concluded 28 days after application. Assessments of m ortality, foraging activity ( flight density), behavior of the bees, pollen collection, colony assessments (food stores, brood status, and hive populations), hive weight, and strength of the colonies were conducted through out pre

- and post

- application. Results of the field study indica te that alpha

- cypermethrin does not have an effect on mortality or brood development; however, statistical analyses were not conducted and colony replicate data was not available for analysis.

In addition, results of an acute study with earthworms yielde d a 48

- hour contact LC 50 

### value of 26.09 ug a.i./cm 2 

### for racemic cypermethrin applied to filter paper

. Based on the data available at this time, acute and chronic risk to non

- target insects and terrestrial invertebrates resulting from the proposed alpha

- cyp ermethrin uses cannot be precluded.

Screening

- level risk assessments do not typically evaluate risks to terrestrial invertebrates; however, toxicity information for beneficial insects is used to develop precautionary label language where necessary. Based on the available data, precautionary label language for bees is

necessary for end

- use products with alpha

- cypermethrin

. The current label for BAS 310 40 I contains the following language: “This product is highly toxic to bees exposed to direct treatment

o r residues on blooming crops or weeds. DO NOT apply this product or allow it to drift to blooming crops if bees are visiting the treatment area”.

4.2. 7

. Risk to Terrestrial Non

- target Plants- Page 61 of 126

- 

### The acute toxicity of technical grade alpha

- cypermethrin to terrestrial plants was evaluated for monocots (onion, Allium cepa ; and oat, Avena sativa ) and dicots (pea, Pisum sativum ; oilseed

rape, Brassica napus ; carrot, Daucus carota ; and sunflower, Helian thus annuus ). The study (MRID 47944210) is classified as supplemental for qualitative use only because a definitive

EC 25 

### and NOAEC were not determined for the most sensitive monocot endpoint (onion fresh weight), in addition to other guideline deviations ( e.g., study was conducted with TGAI instead of the recommended TEP). However, a definitive NOAEC value of 0.0133 lbs a.i/A was determined for the most sensitive dicot endpoint (oilseed rape fresh weight). This NOAEC value represents roughly half of the max imum single application rate for the proposed uses of alpha

cypermethrin and suggests that risks to plants may be possible.

While there is uncertainty in the potential risks to plants because toxicity was observed in the supplemental study and the study

, risk to nontarget terrestrial plants is not expected. It is presumed that additional data regarding the toxicity of alpha

- cypermethrin to terrestrial plants

would have minimal impact on the risk conclusions in this risk assessment.

4.3. Uncertainties and Data Gaps

As discussed in Appendix A , the registrat for BAS 310 40 I , BASF, submitted a minimal dataset to support their strategy to bridge data for the enriched enantiomeric mixture alpha

- cypermethrin with the data previously submitted in support of the registration for the racemic mixture cypermethrin and the enriched enantiomeric mixture zeta

- cypermethrin

. As a result of the Agency’s acceptance of this strategy, ecological fate and ecotoxicity data gaps for alpha

cypermethrin will be fulfilled by th e database for the previously registered cypermethrins (i.e.,

racemic and zeta

- cypermethrin). Additional u ncertainties and datagaps for alpha

- cypermethrin

are discussed below

.

4.3.1. Fate and Transport Unce r tanties

The environmental fate database was b ridged from the cypermethrins to alpha

- cypermethrin. Data specific for alpha

- cypermethrin suggest that the alpha enriched mixture may be less persistent than that of the cypermethrins (zeta and racemic cypermethrin), therefore environmental exposures may b e over estimated

. Appendix A outlines the specific data that were conducted using alpha

- cypermethrin as the test material and where data were bridged from

the racemic or zeta

- cypermethrin.

4.3.2. Effects Uncertainties

There are no chronic exposure toxicity data for freshwater invertebrates or estuarine/marine fish

. Therefore, acute

- to

- chronic ratios (ACRs) based on the appropriate relationships were applied to each of the taxa (e.g., an ACR based on estuarine/marine in vertebrates, for which there are both

acute and chro n ic toxicity data , was applied to freshwater invertebrates) . The ACR is considered- Page 62 of 126

- 

### protective for the purpose of this risk assessment; however, the application of an ACR in the

absence of actual data doe s introduce uncertainty to the risk assessment.

There are no chronic exposure toxicity data for the benthic invertebrate Hyalella azteca

. Therefore, t he chronic NOAEC value for the mysid shrimp (0.000781 μg a.i./L) served as a surrogate estimate of the ch ronic NOAEC for benthic organisms in units of μg a.i./L pore water. The mysid was selected as a surrogate because of similarities in life stages exposed during chronic toxicity tests for both species. In addition the LC50 value for the mysid shrimp and Hya lella azteca in 96

- hour acute studies are very similar (LC50= 0.00475 μg a.i./L for mysid and LC50 = 0.0036 μg a.i./L) indicating that these species experience similar toxicity to cypermethrin. However, use of the mysid shrimp, a saltwater species, as a su rrogate for H.

azteca , a freshwater species, does introduce uncertainty to the risk assessment.

5. Federally Threatened and Endangered (Listed) Species C oncern s

Section 7 of the Endangered Species Act, 16 U.S.C. Section 1536(a)( 2), requires all federal agencies to consult with the National Marine Fisheries Service (NMFS) for marine and anadromous listed species, and/ or the United States Fish and Wildlife Service ( US FWS) for listed wildlife and freshwater organisms, if they are proposing an "action" that may affect listed species or their designated critical habitat. Each federal agency is required under the Act to ensure that any action they authorize, fund, or carry out is not likely to jeopardize the continued

existence of a listed species or result in the destruction or adverse modification of designated critical habitat. To jeopardize the continued existence of a listed species means "to engage in an action that reasonably would be expected, directly or indirectly, to reduc e appreciably the likelihood of both the survival and recovery of a listed species in the wild by reducing the reproduction, numbers, or distribution of the species" (50 C.F.R. § 402.02).

To facilitate compliance with the requirements of the Endangered Sp ecies Act (subsection (a)(2)), the Office of Pesticide Programs has established procedures to evaluate whether a proposed registration action may directly or indirectly appreciably reduce the likelihood of both the survival and recovery of a listed species in the wild by reducing the reproduction, numbers, or distribution of any listed species (USEPA, 2004). After the Agency’s screening level risk assessment is conducted, if any of the Agency’s listed species ’ LOCs are exceeded for either

direct or indirec t effects, an analysis is conducted to determine if any listed or candidate species

may co

- occur in the area of the proposed pesticide use or areas downstream or downwind that could be contaminated from drift or runoff/erosion. If listed or candidate spec ies may be present in the proposed action area, further biological assessment is undertaken. The extent to which listed species may be at risk is considered

, which then determines the need for the development of a more comprehensive consultation package, as required by the Endangered Species Act.

The federal action addressed herein is the proposed new registration of alpha

- cypermethrin on agricultural use sites ; it is expected that its use could occur nationwide

.- Page 63 of 126

- 

### 5.1. Action Area

For listed species assessment purposes, the action area is considered to be the area affected

direct ly or indirectly by alpha

- cypermethrin use and not merely the immediate area where alpha

cypermethrin is applied. At the initial baseline , the risk as sessment considers broadly described taxonomic groups and conservatively assumes that listed species within those broad groups are

co

- located with the pesticide treatment area. This means that listed terrestrial plants and wildlife

are assumed to be locat ed on or adjacent to the treated site and listed aquatic organisms are assumed to be located in a surface water body adjacent to the treated site. The assessment also assumes that the listed species are located within an assumed area, which has the relati vely highest potential exposure to the pesticide, and that exposures are likely to decrease with

distance from the treatment area. Section 3.1 of this risk assessment presents the proposed pesticide use sites that are used to establish initial co

- location of species with treatment areas.

5. 2

. Taxonomic Groups Potentially at Risk

If the assumptions associated with the baseline action area result in RQs that are below the listed species LOCs, a "no effect" determination conclusion is made with respect to listed species in that taxa, and no further refinement of the action area is necessary. Furthermore, RQs below the listed spe cies LOCs for a given taxonomic group indicate no concern for indirect effects on listed species that depend upon the taxonomic group for which the RQ was calculated. However, in situations where the screening assumptions lead to RQs in excess of the list ed species LOCs for a given taxonomic group, a potential for a "may affect" conclusion exists and may be associated with direct effects on listed species belonging to that taxonomic group or may extend to indirect effects upon listed species that depend up on that taxonomic group as a resource. In such cases, additional information on the biology of listed species, the locations of these species, and the locations of use sites are considered to determine the extent to which screening assumptions regarding a n action area apply to a particular listed organism. These subsequent refinement steps will consider how this information would impact the action area for a particular listed organism and potentially include areas of exposure that are downwind and downstr eam of the pesticide use

site.

Assessment endpoints, exposure pathways, and the conceptual model s addressing proposed new alpha

- cypermethrin uses, and the associated exposure and effects analyses conducted for the alpha

- cypermethrin baseline risk assessme nt are in Sections 2 to 3 . The assessment endpoints

used in the baseline risk assessment include those defined operationally as reduced survival and reproductive impairment for both aquatic and terrestrial animal species and survival, reproduction, and gr owth of aquatic and terrestrial plant species from both direct acute and chronic exposures. These assessment endpoints are intended to address the standard set forth in the Endangered Species Act requiring federal agencies to ensure that any action they a uthorize does not appreciably reduce the likelihood of both the survival and recovery of a listed species in the wild by reducing the reproduction, numbers, or distribution of the species. Risk estimates (RQs) which, integrating exposure and effects, are calculated for broad based taxonomic groups

in the screening

- level risk assessment presented in Section 4.- Page 64 of 126

- 

### Both acute endangered species and chronic risk LOCs are considered in the baseline risk assessment to identify direct and indirect effects to taxa o f listed species. This section identifies direct effect concerns, by taxa that are triggered by exceeding endangered LOCs in the baseline risk assessment, with an evaluation of the potential probability of individual effects for exposures that may occur a t the established endangered species LOC. Data on exposure and effects

collected under field and laboratory conditions are evaluated to make determinations on the predictive utility of the direct effect screening assessment findings to listed species. For alpha

cypermethrin

, risk from chronic exposure is presumed for mammals

. Potential acute risk to listed fish, aquatic

- phase amphibians , and aquatic invertebrates is indicated based on exceedance

of the LOC.

Table 5.1. Potential Effects to Federally L isted Taxa Associated with Direct or Indirect Effects from the Proposed New Uses of Alpha

- Cypermethrin

.

Listed Taxon Direct Effects Indirect Effects a

Terrestrial and semi

- aquatic plants

- monocots No Yes

Terrestrial and semi

- aquatic plants

- dicots No Yes

Birds No Yes

Terrestrial

- phase amphibians and reptiles No Yes

Mammals Yes Yes Aquatic nonvascular plants No Yes

Aquatic vascular plants No Yes

Freshwater fish Yes Yes Aquatic

- phase amphibians Yes Yes

Freshwater crustaceans Yes Yes

Mollusks Yes Yes

Marine/estuarine fish Yes Yes

Marine/estuarine invertebrates Yes Yes

a until an endangered species assessment is complete, indirect effects to all species cannot be precluded- Page 65 of 126

- 

### 5. 2 .1. Probit Dose

- Response Analysis

The Agency uses the probit dose

- response relationship as a tool for providing additional information on the potential for acute direct effects to aquatic and terrestrial animals (USEPA, 2004). As part of this evaluation, the acute RQ for listed species is presented in terms of the chance of an individual event ( i.e. , mortality or immobilization) should exposure at the EEC actually occur for a species with sensitivity to alpha

- cypermethrin on par with the acute toxicity endpoint selected for RQ calculation. To accomplish this inter pretation, the Agency uses the slope of the dose

- response relationship available from the toxicity study used to establish the acute toxicity measures of effect for each taxonomic group that is relevant to this assessment. The individual effects probabili ty associated with the acute RQ is based on the mean estimate of the slope and an assumption of a probit dose

- response relationship. In addition to a single effects probability estimate based on the mean, upper and lower estimates of the effects probabili ty are also provided to account for variance in the slope, if available. Based on the available acute toxicity for alpha

- cypermethrin , a summary of the probit dose

- response analysis is provided in

Table 5.2 . If no dose response information is available t o estimate a slope for this analysis, a default slope assumption of 4.5 (with lower and upper bounds of 2 to 9) (Urban and Cook, 1986)

is used.

Individual effect probabilities are calculated based on an Excel spreadsheet tool IECV1.1 (Individual Effect C hance Model Version 1.1) developed by the U.S. EPA, OPP, Environmental

Fate and Effects Division (June 22, 2004 ). The model allows for such calculations by entering the mean slope estimate (and the 95% confidence bounds of that estimate) as the slope para meter for the spreadsheet. The desired threshold for the probability of an individual effect is entered as the listed species LOC. In addition, the probability of an individual effect is also derived based on the calculated acute RQ, if available.- Page 66 of 126

- 

### Table 5.2. Summary of Alpha

- Cypermethrin Probit Dose Response Analysis for Listed Species

Taxa (study type) Acute Effect Slope (95% C.I.) Chance of Individual Effect at Listed Species LOC (95% C.I.) Chance of Individual

Effect at Derived Acute RQ 1,2, 3 (95 % C.I.)

Bird oral dose No mortality observed 1 in 2.9E+05 (1 in 44 to 1 in 8.86E+18) Not calculated; no mortality observed

Bird dietary No mortality observed 1 in 2.9E+05 (1 in 44 to 1 in 8.86E+18) Not calculated; no mortality observed

Mammal oral dose Mortality Slope = 3.5 (0.12

– 7.21) 1 in 4.3 E+0 3 (1 in 2.21 to 1 in

3.57 E+1 2 ) 1 in 3.74E+02 (1 in 2.16 to 1 in 2.09E+08) 1

Freshwater Fish Mortality

Default Slope = 4.5 (2

– 9) 1 in 4.18E+08 (1 in 2.16E+02 to 1 in

1.75E+31 ) 1 in 1.38 (1 in 1.64 to 1 in 1.12) 2

Freshwater i nvertebrates Mortality

Default Slope = 4.68 ( 2.35

– 7.02 ) 1 in 1.76E+09 (1 in 8.96E+02 to 1 in

3.01E+19 ) 1 in 1 (1 in 1 to 1 in 1) 3

1 Acute RQ for mammals = 0. 16

. 2 Acute RQ for freshwater Fish = 1.38.

3 Acute RQ for freshwater invertebrates = 150

.



### As shown in Table 5.2 , t he probability for acute direct effects ( i.e. , mortality) to individual listed fish (based on the most sensitive species , rainbow trout ) and the highest derived RQ value is 1 in

1.38 . This reflects an average slope of 4.5. If the true dose response curve were steeper, the chance of an individual increases (e.g. slope of 9, chance is 1 in 1.12 ). The chance of an individual effect for aquatic invertebrates, based on the most sensitiv e species, Amphipod , is 1 in

1

. Based on this information, it is likely that the proposed use of alpha

- cypermethrin will cause acute direct effects to listed fish and invertebrate species.

5. 2 .2. Listed Species Occurrence Asso ciated with Alpha

- Cyperme thrin Use

T he goal of the co

- location analysis is to determine whether sites of pesticide use are geographically associated with known locations of listed species [following the convention of the Services, the word ‘species’ in this assessment may apply to a ‘species’, ‘subspecies’, or an Evolutionary Signi ficant Unit (ESU)]. At the screening level, this analysis is accomplished using the LOCATES database (version 2.10.3). The database uses location information for listed species at the county level and compares it to agricultural census data (from 2002) f or crop production at the same county level of resolution. The product is a listing of Federally

- listed species that are located in counties known to produce the crops upon which the pesticide will be

used. A list of potentially directly affected species associated with the proposed new uses of alpha

- cypermethrin is provided in Appendix F

. Species potentially indirectly affected include all listed species

.

This preliminary analysis indicates that there is a potential for alpha

- cypermethrin use to overl ap with listed species and that a more refined assessment is warranted. The more refined assessment should involve clear delineation of the action area associated with proposed uses of alpha

- cypermethrin and the best available information on the temporal and spatial co

- location of- Page 67 of 126

- 

### listed species with respect to the action area

. This analysis has not been conducted for this

assessment.- Page 68 of 126

- 

### 6. References

Carousel, R.F., J.C. Imhoff, P.R. Hummel, J.M. Cheplick, A.S. Donigian, Jr., L.A. Suarez.

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### USEPA 2009 . Guidance for Selecting Input Parameters in Modeling the Environmental Fate and

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USEPA. 2011 b . Water Models. U.S. Environmental Protection Agency, Pesticides: Science and Policy, Models and Databases. Last updated Aug. 8, 2011. Online at: http://www.epa.gov/oppefed1/models/water/

USEPA. 2011 c

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### DP barcode 391491.

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161

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48425002 Dijk, A. (1993) Hydrolysis Determination of Carbon 14

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42620501 Clifton, J. (1992) Environmental Fate Studies: Hydrolysis Studies of Cypermethrin in Aqueous Buffered Solutions: Lab Project Number:

191E1192E1: P

- 2771. Unpublished study prepared by FMC Corp. 77 p.

161

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### 48425003 Concha, M.; Yan, Z.; Beigel, C. (2001) BAS 310 I (Alphacypermethrin): Aqueous Photolysis. Project Number: ENV/01/037, 903W, E/00/009. Unpublished study prepared by PTRL West, Inc. 171 p.

42395701 Estigoy, L.; Ruzo, L.; Shepler, K. (1992) Photodegradation of ?carbon 14

- acid|

and ?carbon 14

- alcohol| Cypermethrin in Buffered Aqueous Solution at pH 7 by Natural Sunlight: Revised: Lab Project Number: 247/248W: 247/248W

- 1: 191E1290E1. Unpub

- lished study prepared by Pharmacology and Toxicology

Research Research Lab (PTRL

- West) and FMC Corp. 144 p

.

161

- 3 Photodegradation

- soil

MRID Citation Reference

42129001 Estigoy, L.; Ruzo, L.; Shepler, K. (1991) Photodegradation of Car

- bon 14

- Acid

and Carbon 14

- Alcohol Cypermethrin in/on Soil by Natural Sunlight: Lab Project Number: 249/250W: 191E1390E1: PC

- 0159. Unpublished study prepared by PTRL West. 115 p

162

- 1 Aerobic soil metabolism

MRID Citation Reference

42156601 Ramsey, A. (1991) Environmental Fate Studies: Aerobic Soil Metabolism of Cypermethrin in a Sandy Loam Soil: Lab Project Number: 191E2190E1. Unpublished study prepared by FMC Corp. 99 p.

48425006 Gedik, L.; Keirs, D. (2001) [Carbon 14]

- Alphacyper methrin (BAS 310 I): Degradation in Soil Under Aerobic Conditions. Project Number: ENV/01/012, 399307, AL/620/013. Unpublished study prepared by Inveresk Research International. 119 p.

162

- 2 Anaerobic soil metabolism

MRID Citation Reference

42156602 Ramsey, A. (1991) Environmental Fate Studies: Anaerobic Soil Metabolism of Cypermethrin in a Sandy Loam Soil: Lab Project Number: 191E2590E1. Unpublished study prepared by FMC Corp. 93 p.

162

- 4 Aerobic aquatic metab.

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- 

### 48425011 Mamouni, A. (1993) Fastac (Benzyl

- Carbon 14): Degradation and Metabolism in Aquatic Systems. Project Number: 305864, AL/630/011. Unpublished study prepared by RCC Umweltchemie Ag. 166 p.

48425012 Voelkl, S. (1993) 14C

- Alphacypermethrin (Cyclopropyl

- 1

- 14C): Degradation and Metabolism in Aquatic Systems. Project Number: 316326, AL/630/012. Unpublished study prepared by RCC Umweltchemie Ag. 128 p.

45920801 Curry, S. (2003) Aerobic Aquatic Metabolism of (Carbon 14)

- Zeta

Cy permethrin: Lab Project Number: 194E2202E1: P

- 3592. Unpublished study prepared by FMC Corporation. 187 p.

162

- 3 Anaerobic aquatic metab.

MRID Citation Reference

44876105 Ramsey, A. (1998) Anaerobic Aquatic Metabolism of (carbon

- 14)

- zeta

Cypermethrin: Lab Project Number: 194E2697E1: P

- 3329. Unpublished study prepared by FMC Corporation. 164 p.

163

- 1 Leach/adsorp/desorption

MRID Citation Reference

48425008 Hill, A. (1993) [Benzyl

- Carbon 14] WL85875 (Fastac): Adsorption/Desorption in Three Soils. Project Number: SBTR/93/042, AL/620/011. Unpublished study prepared by Sittingbourne Research Center, Biotechnology and Tox. 47 p.

42129003 Froelich, L. (1991) Soil Mobility Studies: Adsorption/Desorption Studies of Cypermethrin: Lab Project Number: 191E3290E1. Unpub

- lished study prepared by FMC Corp. 65 p.

42129002 Curry, S. (1991) Leaching of Carbon 14

- Cypermethrin in Soil Follow

- ing

Aero bic Aging: Lab Project Number: 191E3190E1. Unpublished study prepared by FMC Corp. 97 p.

164

- 1 Terrestrial field dissipation

MRID Citation Reference

48425014 Forbes, S.; Knight, C. (1983) Analysis of Soil from UK for Residues of

WL85871

- Soil Persistence Trial

- First Year. Project Number: SBGR/83/162, SRC18083, AL/790/006. Unpublished study prepared by Sittingbourne- Page 72 of 126

- 

### Research Center, Biotechnology and Tox. 10 p.

48425015 Forbes, S.; Burden, A. (1983) Analysis of Soil from UK (Reculver) for Residues of WL85871 (Fastac)

- Soil Persistence Trial

- Second Year. Project Number: SBGR/84/005, SRC18083, AL/790/007. Unpublished study prepared by Sittingbourne Research Cente r, Biotechnology and Tox. 10 p.

48425016 Forbes, S.; Wales, G. (1985) Analysis of Soil from UK (Reculver) for Residues of Fastac (WL85871)

- Soil Persistence Trial

- Third Year. Project Number: SBGR/85/070, SRC42285, AL/790/008. Unpublished study prepared by Sittingbourne Research Center, Biotechnology and Tox. 13 p.

48425017 Bosio, P. (1983) Residues of WL 85871 and Metabolites in Soil from U.K. Treated with Fastac 1981/82 Trials. Project Number: BEGR/83/040, AL/790/009. Unpublished study prepared by Sitt ingbourne Research Center, Biotechnology and Tox. 9 p.

48425019 Forbes, S.; Wales, G. (1985) Analysis of Soil from UK (Hoath) for Residues of Fastac (WL85871)

- Soil Persistence Trial

- Third Year. Project Number: SBGR/85/072, SRC42285. Unpublished study prepared by Sittingbourne Research Center, Biotechnology and Tox. 14 p.

48425020 Forbes, S.; Mackay, C. (1983) Analysis of Soil from UK (Coates) for Residues

of WL85871 (Fastac)

- Soil Persistence Trial

- First Year. Project Number: SBGR/83/418, SRC18083. Unpublished study prepared by Sittingbourne Research Center, Biotechnology and Tox. 10 p.

48425021 Forbes, S.; Wales, G. (1985) Analysis of Soil from UK (Coates) for Residues of Fastac (WL85871)

- Soil Persistence Trial

- Second Year. Project Number: SBGR/85/071, SRC42285, AL/790/013. Unpublished study prepared by Sittingbourne Research Center, Biotechnology and Tox. 12 p.

48425022 Coveney, P.; Forbes, S. (1986) Ana lysis of Soil from UK(Coates) for Residue of Fastac (WL85871)

- Soil Persistence Trial

- Third Year. Project Number: SBGR/86/201, SRC42286, AL/790/014. Unpublished study prepared by Sittingbourne Research Center, Biotechnology and Tox. 14 p.

42459601 Lepper t, B. (1992) Ammo 2.5 EC Insecticide

-- Terrestrial Field Dissipation: Lab Project Number: 191E4191E1: RAN

- 0239. Unpublished study prepared by FMC Corporation. 182 p.

6.2. Submitted Ecotoxicity Studies



## 71

- 1 Avian Single Dose Oral Toxicity

MRID Citation Reference- Page 73 of 1 26

- 25769 2016140 Ross, D.B.; Cameron, D.M.; Roberts, N.L. (1977) The Acute Oral Toxicity (LD50) of PP 383 to the Mallard Duck. (Unpublished study received Dec 31,

1979 under 10182

- EX

- 19; prepared by Huntingdon Research Centre, submitted by ICI Americas, Inc., Wilmington, D el.; CDL:241598

- G)

90070 2016174 Roberts, N.L.; Fairley, C. (1980) The Acute Oral Toxicity (LDI50^) of Cypermethrin to the Mallard Duck: ICI 302/80305; CTL/8/994. (Unpublished study received Dec 30, 1981 under 10182

- 64; pre

- pared by Huntington

Research Centre, England, submitted by ICI Americas, Inc., Wilmington, Del.; CDL:070561

- B)

44546024 2016193 Johnson, A. (1998) Acute Toxicity (LD50) to Bobwhite Quail: Betacypermethrin: Lab Project Number: PWT 129: PWT 129/962076. Unpublished study prepared by Hu ntingdon Life Sciences Ltd. 38 p.

92027002 Registrant Summary Edwards, P. (1990) ICI Americas Inc. Phase 3 Summary of MRID 00090070. The Acute Oral Toxicity (LD50) of Cypermethrin to the Mallard Duck: Report No. CTL/C/994; Study No. ICI/302/80305.: 10 p.



## 71

- 2 Avian Dietary Toxicity

MRID Citation Reference

90071 2016164 Roberts, N.L.; Fairley, C.; Woodhouse, R.N. (1980) The Subacute Dietary Toxicity (LCI50^) of Cypermethrin to the Mallard Duck: ICI 330/WL/80812; 55 1(a)/3. (Unpublished study received Dec 30, 1981 under 10182

- 64; prepared by Hungtindon Research Centre, England, submitted by ICI Americas, Inc., Wilmington, Del.; CDL: 070561

- C)

90072 2016165 Roberts, N.L.; Fairley, C.; Woodhouse, R.N. (1981) The Subacute Di

- etary Toxicity (LCI50^) of Cypermethrin to the Bobwhite Quail: ICI 331 WL/80811; 5E.1(a)/4. (Unpublished study received Dec 30, 1981 under 10182

- 64; prepared by Huntingdon Research Centre, England, submitted by ICI Americas, Inc., Wilmington, Del.; CDL: 070561

- D)

44546025 2016184 Johnson, A. (1998) Dietary (LC50) to the Mallard Duck: Betacypermethrin: Lab Project Number: PWT 128: PWT 128/962075. Unpublished study prepared by Huntingdon Life Sciences Ltd. 40 p.

44546026 2016185 Johnson, A. (1998) Dietary LC( 50) to the Bobwhite Quail: Betacypermethrin: Lab Project Number: PWT 127: PWT 127/962074. Unpublished study prepared by Huntingdon Life Sciences Ltd. 40 p.

92027003
O f

90072 Registrant Summary Edwards, P. (1990) ICI Americas Inc. Phase 3 Summary of MRID 00090072. The Subacute Dietary Toxicity (LC50) of Cypermethrin (PP383) to the Bobwhite Quail: Report No. ICI331WL/80811; Study No. ICI331WL/80811. Prepared by Huntingdon Research Centre 11 p.

92027004
O f

90071 Registrant Summary Edwards, P. (1990) ICI Am ericas Inc. Phase 3 Summary of MRID 00090071. The Subacute Dietary Toxicity (LC50) of Cypermethrin (PP383) to the Mallard Duck: Report No. ISK/ICIWL284/79835. Prepared by Huntingdon Research Centre 11 p.



## 71

- 4 Avian Reproduction

MRID Citation Reference- Page 74 of 126

- 90073 DER not

located

reviewed in

1981 Roberts, N.L.; Fairley, C.; Chanter, D.O.; et al. (1981) The Effect of the Dietary Inclusion of Cypermentrin on Reproduction in the Mallard Duck: ICI 341/8164; CTL/C/1091. (Unpublished study re

- ceiv ed Dec 30, 1981 under

10182

- 64; prepared by Huntingdon Re

- search Centre, England, submitted by ICI Americas, Inc., Wil

- mington, Del.; CDL:070561

- E)

90074 2016144 Roberts, N.L.; Fairley, C.; Chanter, D.O.; et al. (1981) The Effect of Dietary Inclusion of Cypermethrin on Reproduction in the Bob

- white Quail: ICI 342/81341; CTL/C/1105. (Unpublished study re

- ceived Dec 30, 1981 under

10182

- 64; prepared by Huntingdon R e

- search Centre, England, submitted by ICI Americas, Inc., Wil

- mington, Del.; CDL:070561

- F)

92027005 Registrant Summary Edwards, P. (1990) ICI Americas Inc. Phase 3 Summary of MRID 00090074. The Effect of Dietary Inclusion of Cypermethrin on Reproducti on in Bobwhite Quail: Report No. CTL/C/1105; Study No.: ICI342/81341.: 15 p.

92027006 Registrant Summary Edwards, P. (1990) ICI Americas Inc. Phase 3 Summary of MRID 00090073. The Effect of the Dietary Inclusion of Cypermethrin on Reproduction in the Mal lard Duck: Report No. CTL/C/1091; Study No.: ICI341/8164.: 15 p.



## 72

- 1 Acute Toxicity to Freshwater Fish

MRID Citation Reference

62791 See 65812 Hill, R.W.; Maddock, B.G.; Harland, B.J. (1980) Determination of the Acute Toxicity of Cypermethrin (PP 383) to Bluegill Sunfish (Lepomis macrochirus): BL/B/2011. (Unpublished study received Dec 5, 1980 under

279

- EX

- 86; prepared by Imperial Chemical Indust ries, Ltd., England, submitted by FMC Corp., Philadelphia, Pa.; CDL:243861

- AE)

62792 DER not

located

Reviewed in

1982 Hill, R.W.; Maddock, B.G.; Harland, B.J. (1980) Determination of the Acute Toxicity of Cypermethrin (PP 383) to Rainbow Trout (Salmo gairdneri): BL/B/2006. (Unpublished study received Dec 5, 1980 under 279

- EX

- 86; prepared by Imperial Chemical Industries, L td., England, submitted by FMC Corp., Philadelphia, Pa.; CDL:243861

- AF)

65812 2016475 Hill, R.W.; Maddock, B.G.; Harland, B.J. (1980) Determination of the Acute Toxicity of Cypermethrin (PP 383) to Bluegill Sunfish (Lepomis macrochirus): BL/B/2011. (Unpublished study received Dec 29, 1980 under

10182

- EX

- 19; prepared by Imperial Chemical Ind ustries, Ltd., England, submitted by ICI Americas, Inc., Wilmington, Del.; CDL:244017

- D)

65813 DER not

located

reviewed in

1981 Hill, R.W.; Maddock, B.G.; Harland, B.J. (1980) Determination of the Acute Toxicity of GFU 061, a 36% w/v Formulation of Cype rmethrin to Rainbow Trout (Salmo gairdneri): BL/B/2016. (Unpublished study received Dec 29,

1980 under 10182

- EX

- 19; prepared by Imperial Chemical Industries, Ltd., England, submitted by ICI Americas, Inc., Wilmington, Del.; CDL:244017

- E)

65814 DER not

l. ocated Hill, R.W.; Maddock, B.G.; Harland, B.J. (1980) Determination of the Acute Toxicity of GFU 061, a 36% w/v Formulation of Cypermethrin to Bluegill Sunfish (Lepomis macrochirus): BL/B/ 2017. (Unpublished study received Dec 29, 1980 under 10182

- EX

- 19; prepared by Imperial Chemical Industries, Ltd., England, submitted by ICI Americas, Inc., Wilmington, Del.;
CDL:244017

- F)- Page 75 of 126

- 65816 Permethrin study Hill, R.W.; Young, B.E. (1978) The Acute Toxicity of Permethrin Acid and

3

- Phenoxy Benzyl Alcohol to Rainbow Trout (Salmo gairdneri): BL/B/1918. (Unpublished study received Dec 29, 1980 under 10182

- EX

- 19; prepared by Imperial Chemical Industries, Ltd., England, submitted by ICI Americas, Inc., Wilmington, Del.; CDL:244017

- J)

88947 2016176

2079552 =

contract draft Hill, R.W.; Maddock, B.G.; Comber, M.H.I. (1981) Cypermethrin: Determination of the Acute Toxicity of Formulation GFU 070 to Rainbow Trout (?~Salmo gairdneri~?): BL/B/2093. (Unpublished study received Dec 30, 1981 under 10182

- 64; prepared by Imperial Chemical Industries, Ltd., submitted by ICI Americas, Inc., Wilmington, Del.; CDL:070558

- C)

88948 2016177 Hill, R .W.; Maddock, B.G.; Comber, M.H.I. (1981) Cypermethrin. Determination of the Acute Toxicity of Formulation GFU 070 to Bluegill Sunfish (?~Le pomis macrochirus~?): BL/B/2099. (Unpub

- lished study received Dec 30, 1981 under 10182

- 64; prepared by Imperial Chemical Industries, Ltd., submitted by ICI Americas, Inc., Wilmington, Del.;
CDL:070558

- D)

89036 DER not

located Reiff, B.; Pearson, N.; Ree s, H.J.; et al. (1978) The Effect of Suspended Solids on the Toxicity of WL 43467 to Rainbow Trout (?~Salmo gairdneri~?): Group Research Report TLGR.0007.78. (Un

- published study received Dec 30, 1981 under 10182

- 64; prepared by Shell Research, Ltd., Engla nd, submitted by ICI Americas, Inc., Wilmington, Del.; CDL:070562

- A)

89037 2016146 Hill, R.W.; Young, B.E.; Comber, M.H.I. (1981) Determination of the Acute Toxicity of 3

- Phenoxy Benzoic Acid to Rainbow Trout (?~Salmo gairdneri~?): Brixham Report No. Bl/ B/2038. (Unpub

- lished study received Dec 30, 1981 under 10182

- 64; prepared by Imperial Chemical Industries, Ltd., England, submitted by ICI Americas, Inc., Wilmington, Del.;
CDL:070562

- B)

89038 2016147 Hill, R.W.; Young, B.E.; Comber, M.H.I. (1981) Determination of the Acute Toxicity of 3

- Phenoxy Benzoic Acid to Bluegill Sunfish (?~Lepomis macrochirus~?): Brixham Report No. BL/B/2086. (Un

- published study received Dec 30, 1981 under 10182

- 64; prepared by Imperial Chemical Industries, Ltd., England, s ubmitted by ICI Americas, Inc., Wilmington, Del.;
CDL:070562

- C)

41068002 Open lit Coats, J.; O'Donnell

- Jeffery, N. (1979) Toxicity of four synthetic pyrethroid

insecticides to rainbow trout. Bulletin of Enviro

- mental Contamination and Toxicology 23:250

- 255.

41068003 Open lit McLeese, D.; Metcalfe, C.; Zitko, V. (1980) Lethality of permethrin, cypermethrin and fenvalerate to salmon, lobster and shrimp. Bulletin of Environmental Contamination and Toxicology 25:950

- 955.

41068004 Open lit Stephenson, R. (1981) Aquatic toxicology of cypermethrin: I acute toxicology to some freshwater fish and invertebrates in labora

- tory tests. Aquatic Toxicology 2:175

- 185.

41968208 2016167 Overman, M.; Barron, M.; Vaishnav, D. (1990) Cypermethrin

- S (FMC 56701): Acute T oxicity to Rainbow Trout (Oncorhynchus mykiss) Under

Flow

- through Test Conditions: Lab Project Number: 3903026

- 0700

- 3140. Unpublished study prepared by Environmental Science and Engineering, Inc. 48 p.- Page 76 of 126

- 41968209 2016173 Vaishnav, D.; Yurk , J. (1990) Cypermethrin (FMC 45806): Acute Toxi

- city to Rainbow Trout (Oncorhynchus mykiss) Under Flow

- through Test Conditions: Lab Project Number: 3903026

- 0750

- 3140. Unpub

- lished study prepared by Environmental Science and Engineering, Inc. 46 p.

445 46027 2016194 Sousa, J. (1998) (Carbon 14)

- Cypermethrin

-- Acute Toxicity to Rainbow Trout (Oncorhynchus mykiss) Under Flow

- Through Conditions: Final Report: Lab Project Number: 97

- 11

- 7166: 12442.1096.6223.108. Unpublished study prepared by Springborn Labs., Inc. 91 p.

44546028 2016196 Sousa, J. (1998) Cypermethrin Technical

-- Acute Toxicity to Rainbow Trout (Oncorhynchus mykiss) Under Flow

- Through Conditions: Final Report: Lab Project Number: 98

- 1

- 7213: 12442.1096.6222.108. Unpublished study prepared by Springborn Labs., Inc. 78 p.

44546029 2016186 Sousa, J. (1998) (Carbon 14)(Beta)

- Cypermethrin

-- Acute Toxicity to Bluegill Sunfish (Lepomis macrochirus) Under Flow

- Through Conditions: Final Report: Lab Project Number: 97

- 12

- 7177: 12442.1096.6225.105. Unpu blished study prepared by Springborn Labs., Inc. 91 p.

44546030 2016187 Sousa, J. (1998) Cypermethrin Technical

-- Acute Toxicity to Bluegill Sunfish (Lepomis macrochirus) Under Flow

- Through Conditions: Final Report: Lab Project Number: 97

- 12

- 7195: 12442.1 096.6224.105. Unpublished study prepared by Springborn Labs., Inc. 76 p.

92027007 Registrant

summary Adams, D. (1990) ICI Americas Inc. Phase 3 Summary of MRID 00065812. Cypermethrin Technical PP383: Determination of the Acute Toxicity to Bluegill Sunfish (Lepomis macrochirus): Report No. BL/B/2011; Study No.: F342/D. Prepared by ICI Brixham Laboratory 13 p.

92027008 Registrant Summary Adams, D. (1990) ICI Americas Inc. Phase 3 Summary of MRID 00089038

. 3

- Phenoxybenzoic Acid: Determination of the Acute Toxicity to Bluegill Sunfish (Lepomis macrochirus): Report No. BL/2086; Study No.: G145/D.: 12 p

92027009 Registrant Summary Adams, D. (1990) ICI Americas Inc. Phase 3 S ummary of MRID 00088948. Cypermethrin (PP383): Determination of the Acute Toxicity of a 2lb/US gallon formulation to Bluegill Sunfish (Lepomis macrochirus): Report No. BL/B/2099; Study No.: G244/C. Prepared by ICI Brixham Laboratory 13 p.

92027010 Regist rant Summary Hill, R. (1990) ICI Americas Inc. Phase 3 Summary of MRID 00089037 . 3

- Phenoxybenzoic Acid: Determination of the Acute Toxicity of the Active Ingredient (99% Purity w/w) to Rainbow Trout (Salmo gairdneri): Report No. BL/B/2038; Study No.: G 145 /C. Prepared by ICI Brixham Laboratory 12 p.

92027011 Registrant Summary Treacy, C. (1990) ICI Americas Inc. Phase 3 Summary of MRID 00062792. Cypermethrin (PP383): Determination of the Acute Toxicity of Active Ingredient (91. 5% purity) to Rainbow Trout (Salmo gairdneri) Report No. BL/B/2006; Study No.: F342/B.: 12 p.

92027012 Registrant Summary Coleman, C. (1990) ICI Americas Inc. Phase 3 Summary of MRID

00088947 . Cypermethrin: Determination of the Acute Toxicity of a 25% w/w

Formulation to Rainbow Trout (Salbo gairdneri): Report No. BL/B/2093; Study No.: G244/B.: 12 p.

92027013 Registrant Summary Treacy, C. (1990) ICI Americas Inc. Phase 3 Summary of MRID 00065813

. Cypermethrin: Determination of the Acute Toxicity of Formulation GFU 061

to Rainbow Trout (Salmo gairdneri): Report No. BL/B/2016; S No. F617/B.:- Page 77 of 126

- 12 p.



## 72

- 2 Acute Toxicity to Freshwater Invertebrates

MRID Citation Reference

62793 Or

92027014 2016162 Edwards, P.J.; Brown, S.M.; Sapiets , A.S. (1980) Cypermethrin (PP383): Toxicity of Technical and Formulated Material to First Instar Daphnia magna: Report Series RJ 0110B. (Unpublished study received Dec 5, 1980

under 279

- EX

- 86; prepared by Imperial Chemical Industries, Ltd., England,

submi tted by FMC Corp., Philadelphia, Pa.; CDL:243861

- AG)

65815 See 62793 Edwards, P.J.; Brown, S.M.; Sapiets , A.S.; et al. (1980) Cypermethrin (PP383): Toxicity of Technical and Formulated Material to First Instar Daphnia magna: Report Series RJ 0110B. (Unpublished study received Dec 29, 1980 under 10182

- EX

- 19; prepared by Imperial Chemical Industries, Ltd., Eng land, submitted by ICI Americas, Inc., Wilmington, Del.;
CDL:244017

- H)

65817 Permethrin study Getty, C.; Wilkinson, W.; Davies, P.J.; et al. (1978) Permethrin Acid and

3

- Phenoxybenzyl Alcohol : Toxicity to First Instar Daphnia magna: Report
Series RJ 0042 B. (Unpublished study received Dec 29, 1980 under 10182

- EX

- 19; prepared by Imperial Chemical Industries, Ltd., submitted by ICI Americas, Inc., Wilmington, Del.; CDL:244017

- K)

88949 DER not

located Edwards, P.J.; Brown, S.M.; Swaine, H.; et al. (1981) Cy permethrin (PP383): Toxicity of Formulation GFU070 to First Instar ?~Daphnia magna~?: Report Series RJ 0199B. (Unpublished study received Dec 30,

1981 under 10182

- 64; prepared by Imperial Chemical Industries, Ltd., England, submitted by ICI Americas, Inc., Wilmington, Del.; CDL:070558

- E)

89040 2016162 Edwards, P.J.; Brown, S.M.; Swaine, H.; et al. (1980) Cypermethrin (PP383): Toxicity of Formulation GFU061 to First Instar~Daphnia~

? ~magna~?: Report Series RJ 0149B. (Unpublished study received Dec 30, 1981 under 10182

- 64; prepared by Imperial Chemical In

- dustries, Ltd., submitted by ICI Americas, Inc., Wilmington, Del.; CDL:070562

- E)

89041 2016150 Stephenson, R.R.; Bennett, D.; Fra ncis, W.H.P.; et al. (1980) The Acute Toxicity of Cypermethrin (WL 43467) to the Freshwater Shrimp (?~Gammarus pulex~?) and Larvae of the Mayfly, (?~Cloeon~ ?~dipterum~?), in Continuous

- flow Tests: Group Research Report TLGR.80.079. (Unpublished study rece ived Dec 30, 1981 under 10182

- 64; prepared by Shell Research, Ltd., England, submitted by ICI Americas, Inc., Wilmington, Del.; CDL:070562

- G)

89042 DER nor

located

reviewed in

1982

- core Jaber , M.J.; Hawk, R.E. (1981) The Acute Toxicity of Cypermethrin to Crayfish (?~Orconectes sp~?.): Report Series TMUE0008/B. (Unpublished study received Dec 30, 1981 under 10182

- 64; sub

- mitted by ICI Americas, Inc., Wilmington, Del.; CDL:070562

- H)

89046 201 6153 Edwards, P.J.; Brown, S.M.; Swaine, H.; et al. (1980) 3

- Phenoxy

- benzoic Acid: Toxicity to First Instar~Daphnia magna~?:Report Series RJ 0148B. (Unpublished study received Dec 30, 1981 under 10182

- 64; prepared by Imperial Chemical Industries, Ltd., su bmitted by ICI Americas, Inc., Wilmington, Del.; CDL:070562

- L)- Page 78 of 126

- 89048 2016155 Edwards, P.J.; Brown, S.M.; Hamer, M.J.; et al. (1980) Cyper

- methrin: Acute Toxicity to the Mayfly, Baetis rhodani: Report Series RJ 0173B. (Unpublished study received Dec 30, 1981 under 10182

- 64; prepared by Imperial Chemical Industries, Ltd., sub

- mitted by ICI Americas, Inc., Wilmington, Del.; CDL:070562

- N)

140833 2016149 Stephenson, R.R.; Sherwood, C.M.; Bennett, D.; et al. (1980) The Acute Toxicity of WL 43467 to Some Fr eshwater Invertebrates in Static Water Tests: Group Research Report TLGR.80.040. (Un

- published study received Dec 30, 1981 under 10182

- 64; prepared by Shell Research, Ltd., England, submitted by ICI Americas, Inc., Wilmington, Del.; CDL:070562

- F)

410680 04 Open lit Stephenson, R. (1981) Aquatic toxicology of cypermethrin: I acute toxicology to some freshwater fish and invertebrates in labora

- tory tests

. Aquatic Toxicology 2:175

- 185.

41968210 2016168 Ward, T.; Boeri , R. et al. (1991) Acute Toxicity of FMC 56701 Tech

- nical and Cypermethrin Technical to the Daphnid, Daphnia magna: Lab Project

Number: 90186

- FMC: A90

- 3310. Unpublished study prepared by Resource Analysts, Inc. 46 p.

43293501 DER not

located

contract d raft

available Wheat, J.; Evans, J. (1994) Zetacypermethrin Technical and Cypermethrin Technical: Comparative Acute Toxicity to the Water Flea (Daphnia magna),

under Flow

- Through Test Conditions: Lab Project Number: J9210001B: A92/3636. Unpublished study p repared by Toxikon Environmental Sciences. 76 p.

44074401 DER not

located Rapley, J.; Hamer, M. (1996) Cypermethrin: Toxicity to Chironomus riparius and Hyalella azteca: Lab Project Number: RC0002: 95JH082. Unpublished study prepared by Zeneca Agrochemic als. 15 p.

44074402 2063977 Gentle, W.; Goggin, U.; Rapley, J.; et al. (1996) Cypermethrin: Toxicity to
Chironomus tentans in Sediment

- Water Systems: Lab Project Number: RC0001: 96JH007. Unpublished study prepared by Zeneca Agrochemicals. 31 p.

4407440 6 2063978 Farrelly, E.; Gentle, W.; Goggin, U.; et al. (1996) Cypermethrin: Toxicity to Hyalella azteca in Sediment

- Water Systems: Lab Project Number: RC0006: 95JH228. Unpublished study prepared by Zeneca Agrochemicals. 30 p.

44423501 DER not

located Hamer, M. (1997) Cypermethrin: Acute Toxicity of Short

- Term Exposures to Hyalella Azteca: Lab Project Number: TMJ3904B. Unpublished study prepared by Zeneca Agrochemicals. 10 p.

44546031 2016188 Putt, A. (1998) (Carbon 14)(Beta)Cypermethrin

-- Acute Toxici ty to Daphnids (Daphnia magna) Under Flow

- Through Conditions: Final Report: Lab Project Number: 97

- 9

- 7079: 12442.1096.6227.115. Unpublished study prepared by Springborn Labs., Inc. 95 p.

44546032 2016189 Putt, A. (1998) Cypermethrin Technical

-- Acute Toxi city to Daphnids (Daphnia magna) Under Flow

- Through Conditions: Final Report: Lab Project Number: 97

- 11

- 7138: 12442.1096.6226.115. Unpublished study prepared by Springborn Labs., Inc. 74 p.

92027014 Registrant Summary Hamer, M. (1990) ICI Americas Inc. Phase 3 Summary of MRID

00062793 . Cypermethrin (PP383): Toxicity of Technical and Formulated Material to First Instar Daphna (sic) magna: Report No.: RJ011OB; Study No.: PP383/CN/01. Prepared by ICI Agrochemicals, Jealott's Hill Research- Page 79 of 126

- Station. 17 p.

92027015 Registrant Summary Hamer, M. (1990) ICI Americas Inc. Phase 3 Summary of MRID

00089046. 3

- Phenoxybenzoic Acid: Toxicity to First Instar Daphna (sic) magna: Report No.: RJ0148B; Study No.: PP383/CN/03. Prepared by ICI Agrochemicals, Jealott's Hill Research Station. 14 p.

92027016 Registrant Summary Hamer, M. (1990) ICI Americas Inc. Phase 3 Summary of MRID

00065817 . Permethrin Acid and 3

- Phenoxybenzyl Alcohol: Toxicity to First Instar Daphnia Magna: Report No.: RJ0042B; Study No.: PP557/CN/0 1. Prepared by ICI Agrochemicals Jealott's Hill Research Station 18 p.

92027017 Registrant Summary Hamer, M. (1990) ICI Americas Inc. Phase 3 Summary of MRID

00152739 . 3 Phenoxybenzoic Acid: Toxicity to First Instar Daphnia magna (II): Report No.: RJ0318B; PP563/CN/01. Prepared by ICI Agrochemicals Jealott's Hill Research Station 14 p.

31225 DER not

located Leblanc, G.A. (1976) Acute Toxicity of FMC

- 30980 to Daphnia magna: ACT 011.12. (Unpublished study received Sep 28, 1976 under 279

- EX

- 63; prepared by EG&G, Bionomics, submitted by FMC Corp., Philadelphia, Pa.;
CDL:227762

- E)

152739 2016175 Everett, C.J., M.J. Hamer and I.R. Hill (1983) 3

- Phenoxybenzoic Acid:

Toxici ty to First Instar Daphnia magna (II). Report Series RJ 0318B. Prepared and Submitted by ICI Plant Protection Division, Bracknell, Berkshire, England. EPA MRID No. 152739.



## 72

- 3 Acute Toxicity to Estuarine/Marine Organisms

MRID Citation Reference

89043 2016151

2016161 Jaber , M.J.; Hawk, R.E. (1981) The Acute Toxicity of Cypermethrin to Pink Shrimp (Penaeus duorarum): Report Series TMUE004/B. (Unpublished study received Dec 30, 1981 under 10182

- 64; sub

- mitted by ICI Americas, Inc., Wilmington, Del.; CDL:070562

- I)

89044 201 6166 Jaber, M.J.; Hawk, R.E. (1981) The Acute and Chronic Toxicity of Cypermethrin to Mysid Shrimp (?~Mysidopsis bahia~?): Report Series TMUE0005/B. (Unpublished study received Dec 30, 1981 under 10182

- 64; submitted by ICI Americas, Inc., Wilmington, Del.; CDL:070562

- J)

89045 2016152 Jaber, M.J.; Hawk, R.E. (1981) The Acute Toxicity of Cypermethrin to Fiddler Crabs (?~Uca pugilator~?): Report Series TMUE0003/B. (Unpublished study received Dec 30, 1981 under 10182

- 64; sub

- mitted by ICI Americas, Inc., Wil mington, Del.; CDL:070562

- K)

89049 2016154 Jaber, M.J.; Hawk, R.E. (1981) The Acute Toxicity of Cypermethrin to Eastern Oysters (Crassostrea virginica): Report Series TMUE0009/B. (Unpublished study received Dec 30, 1981 under 10182

- 64; submitted by
ICI A mericas, Inc., Wilmington, Del.; CDL:070562

- O)

89050 2016143 Hill, R.W.; Thompson, R.S.; Comber, M.H.I. (1981) Investigation of the Acute Toxicity of PP 383 to Larvae of the Pacific Oyster (Crassostrea gigas): Brixham Report No. BL/B/2088. (Unpub

- lished study received Dec 30, 1981 under 10182

- 64; prepared by Imperial Chemical Industries, Ltd., England, submitted by ICI Americas, Inc.; Wilmington, Del.; CDL:070562

- P)- Page 80 of 126

- 90075 DER not

located Jaber , M.J.; Hawk, R.E. (1981) The Acute Toxicity of Cypermethrin to Sheepshead Minnows (?~Cyprinodon variegatus?~): Report Series TMUE0002/B. (Unpublished study received Dec 30, 1981 under 10182

- 64; submitted by ICI Americas, Inc., Wilmington, Del.; CDL:079561

- G)

41968211 2016171 Overman, M.A., M.G. Barron and D.D. Vaishnav (1990) Cypermethrin

- S (FMC 56701): Acute Toxicity to Sheepshead Minnow ( Cyprinodon variegates ) under Flow

- Through Test Conditions. Laboratory Project No.

3903026

- 0600

- 3140. Study Performed by Environmental Science and Engineering, Inc., Gainesville, FL. Submitted by FMC Corporation, Philadelphia, PA. EPA MRID No. 31968211.

41968212 2016170 Chandler, A. (1990) FMC 45806: Acute Toxicity to Sheepshead Minnow (Cyprinodon variegatus) Under Flow

- through Test Conditions: Lab Project

Number: 3903026

- 0350

- 3140. Unpublished study prepared by Environmental Science and Engineering(ESE), Inc. 43 p.

41968213 2016169 Ward, T.; Boeri, R. (1991) Acute Toxicity of FMC 56701 Technical and Cypermethrin Techn ical to the Mysid, Mysidopsis bahia: Lab Project

Number: 90187

- FMC: A90

- 3309. Unpublished study prepared by Resource Analysts, Inc. 52 p.

42364701 Registrant

rebuttal Anon. (1992) Response to the EPA's Review of MRID 41968212 Cypermethrin: Acute Toxicity to Sheepshead Minnows Under Flow

- Through Test Conditions: Unpublished study prepared by FMC Corp. 8 p.

44546033 2016195 Dionne, E. (1998) Cypermethrin Technical

-- Acute Toxicity to Sheepshead Minnow (Cyprinodon variegatus) Under Flow

- Through Conditions: Final Report: Lab Project Number: 97

- 12

- 7197: 12442.1096.6230.505. Unpublished study prepared by Springborn Labs., Inc. 75 p.

44546034 2016187 Sousa, J. (1998) (Carbon 14)(Beta)

- Cypermethrin

-- Chronic Toxicity to Sheepshead Minnow (Cyprinodon variegatus) Under Flow

- Through Conditions: Final Report: Lab Project Number: 97

- 1

- 7212: 12442.1096.6231.505. Unpublished study prepared by Springborn Labs., Inc. 91 p.

44561209 2016191 Putt, A. (1998) (Carbon

- 14) Beta

- Cypermethrin

-- Acute Toxicity to Mysids (Mysidopsis bahia) Under Flow

- Through Conditions: Final Report: Lab Project Number: 97

- 11

- 7153: 12442.1096.6229.515. Unpublished stu dy prepared by Springborn Laboratories, Inc. 79 p.

44561210 2016190 Putt, A. (1998) Cypermethrin Technical

-- Acute Toxicity to Mysids (Mysidopsis bahia) Under Flow

- through Conditions: Final Report: Lab Project Number: 98

- 1

- 7224: 12442.1096.6228.815. Unpub lished study prepared by Springborn laboratories, Inc. 76 p.

92027018 Registrant Summary Royal, P. (1990) ICI Americas Inc. Phase 3 Summary of MRID 00090075. Cypermethrin: Acute Toxicity of Technical Material for Sheepshead Minnow (Cyprinodon variegatus) : Report No.: TMUE 0002/B.: 15 p.

92027019 Registrant Summary Royal, P. (1990) ICI Americas Inc. Phase 3 Summary of MRID 00089049. Cypermethrin: The Acute Toxicity to Eastern Oysters (Crassostrea virginica): Report No. TMUE 0009/B. Prepared by Springborn Laboratories, Inc. 13 p.

92027020 Registrant Summary Royal, P. (1990) Ici Americas Inc. Phase 3 Summary of MRID 00089043. Cypermethrin: Determination of the Acute Toxicity of Technical Material to- Page 81 of 126

- Pink Shrimp (Penaeus duorarum): Report No. TMUE 0004/B. Prepared by Springborn Laboratories, Inc. 15 p.

92027021 2016166 Registrant Summary Royal, P. (1990) ICI Americas Inc. Phase 3 Summary of MRID 00089044. Cypermethrin: Determination of Acute Toxicity to Mysid Shrimp (Mysidopsis bahia): Report No. TMUE 000 5/B. Prepared by Springborn Laboratories, Inc. 12 p.

92027022 Registrant Summary Royal, D. (1990) ICI Americas Inc. Phase 3 Summary of MRID 00089045. Cypermethrin: Determination of the Acute Toxicity of Technical Material to the Fiddler Crab (Uca pugilat or): Report No. TMUE 0003/B. Prepared by Springborn Laboratories, Inc. 15 p.

89051 Stability test Ussary, J.P.; Fitzpatrick, R.D.; Foreman, L.A.; et al. (1981) Cy

- permethrin Stability in Marine Laboratory Test Systems: Report Series TMU0558/B. (Unpublis hed study received Dec 30, 1981 under 10182

- 64; submitted by ICI Americas, Inc., Wilmington, Del.; CDL:070562

- Q)

46591503 Contract draft

available Putt, A. (2005) Cypermethrin

- Toxicity to Estuarine Amphipods (Leptocheirus plumulosus) During a 28

- Day Sediment Exposure. Project Number: 13656/6111. Unpublished study prepared by Springborn Smithers Laboratories. 85 p.

Accession

No.

070562 2016143

2016 156 Thompson, R.S. (1981) Investigation of the Acute Toxicity of PP383 to Larvae of the Pacific Oyster ( Crassostrea gigas ). Unpublished Report by the Brixham Laboratory of Imperial Chemical Industries, Ltd., Submitted 12/28/81 by ICI Americas Inc., Wilming ton, Delaware.

42444601 2016178

2016179 Ward, Timothy J., Robert L. Boeri and Mark A. Palmieri (1992) Acute Toxicity of FMC 56701 Technical and Cypermethrin Technical to the Mysid, Mysidopsis bahia . FMC Study Number A91

- 3454. Submitted by FMC Corporation. Performed by EnviroSystems Division, Resource Analysts, Inc. Hampton, New Hampshire. MRID No. 42444601.



## 72

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

MRID Citation Reference

25770 2016141 Hill, R.W.; Maddock, B.G.; Hart, B. (1976) Determination of the Acute Toxicity of PP383 to Rainbow Trout (Salmo gairdnerii): Report No. BL/B/1711. (Unpublished study received Dec 31, 1979 under 10182

- EX

- 19; prepared by Imperial Chemical Industries, Ltd., s ubmitted by ICI Americas, Inc., Wilmington, Del.; CDL: 241598

- H)

25771 2016142 Hill, R.W.; Maddock, B.G.; Hart, B.; et al. (1977) Determination of the Acute Toxicity of PP 383 to Bluegill Sunfish (Lepomis macrochirus): Report No. BL/B/1775. (Unpublished study received Dec 31, 1979 under 10182

- EX

- 19; prepared by Imperial Chemical Industries, Ltd., submitted by ICI Americas, Inc., Wilmington, Del.; CDL:241598

- I)

31224 DER not

located Bentley, R.E. (1976) Acute Toxicity of FMC

- 30980 to Bluegill (Lepomis

ma crochirus): NCT 634.61. (Unpublished study received Sep 28, 1976

under 279

- EX

- 63; prepared by EG&G, Bionomics, submitted by FMC Corp., Philadelphia, Pa.; CDL:227762

- D)- Page 82 of 126

- 89039 2016148 Jaber, M.J.; Hawk, R.E. (1981) The Toxicity of Cypermethrin to Fathead

M innow (Pimephales promelas) Embryos and Larvae: Report Series TMUE0007/B. (Unpublished study received Dec 30, 1981 under 10182

- 64; submitted by ICI Americas, Inc., Wilmington, Del.; CDL:070562

- D)

89047 2016163 Edwards, P.J.; Hamer, M.J.; Bull, J.M.; et al. (1981) Cypermethrin: 21 Day~Daphnia magna~Life Cycle Study: Report Series RJ 0177B. (Unpublished study received Dec 30, 1981 under 10182

- 64; pre

- pared by Imperial Chemical Industries, Ltd., submitted by ICI Americas, Inc., Wilmington, Del.; CDL:070562

- M)

42725301 2016180 Wheat, J. (1993) FMC

- 30980(carbon 14)

- Cypermethrin: Chronic Toxicity to the Mysid, Mysidopsis bahia, Under Flow

- Through Test Conditions: Lab Project Number: J9205004A. Unpublished study prepared by Toxikon Environmental Sciences. 63 p.

42898301 2016182 Wheat, J. (1993) FMC

- 30980 ((carbon 14) labeled Cypermethrin): Chronic

Life

- Cycle Toxicity to the Water Flea, Daphnia magna, Under Flow

- through Test Conditions: Lab Project Number: J9205004B: A91

- 3479. Unpu blished study prepared by Toxikon Environmental Sciences. 71 p.

44546035 2016192 Sousa, J. (1998) (Carbon 14)(Beta)

- Cypermethrin

-- Chronic Toxicity to Mysids (Mysidopsis bahia) Under Flow

- Through Conditions: Final Report: Lab Project Number: 97

- 12

- 7170: 1 2442.1096.6232.530. Unpublished study prepared by Springborn Labs., Inc. 101 p.

92027023 Registrant Summary Royal, P. (1990) ICI Americas Inc. Phase 3 Summary of MRID 00089039

. Cypermethrin: Early Life Stages Test Fathead Minnow (Pimephales promelas): Re port No. TMUE 0007/B. Prepared by Springborn Laboratories, Inc. 14 p.

92027024 Registrant Summary Royal, P. (1990) ICI Americas Inc. Phase 3 Summary of MRID 00089044

. Cypermethrin: Invertebrate Life

- Cycle Test in Mysid Shrimp (Mysidopsis bahia): SLI TMUE 0005/B.: 16 p

92027025 Registrant Summary Hamer, M. (1990) ICI Americas Inc. Phase 3 Summary of MRID 00089047

. Cypermethrin: 21 Day Daphnia magna Life

- cycle Study: Report No.: RJ0177B; PP383/CN/04. Prepared by ICI Agrochemicals Jealott's Hill Research Station 17 p.

4 6591503 2086352 Marine Amphipod 28 Day Whole Sediment toxicity



## 850.1300 Daphnid chronic toxicity test

MRID Citation Reference

47885103 Contract draft

available Cafarella , M. (2008) Cypermethrin: Full Life Cycle Toxicity Test with Water Fleas, Daphnia magna under Flow

- Through Conditions: Reformatted Final Report. Project Number: 1084/012/231, A2007/6309. Unpublished study prepared by Springborn Smithers Laboratories (Europ e). 87 p.

47944027 DER not

located Garforth, B. (1982) WL 85871 and Cypermethrin: Chronic Toxicity to Daphnia magna. Project Number: AL/523/001/OCR, AL/523/001, SBGR/82/119. Unpublished study prepared by Sittingbourne Research Center. 46 p.- Page 83 of 126

- 

## 72

- 5 Life cycle fish

MRID Citation Reference

40102101 Status report Hill, R.; Tapp, J. (1987) Status Report at Day 30 Post

- hatch Cypermethrin (PP383) Fathead Minnow Lifecycle Study: Lab. Pro

- ject ID: (P171/C). Unpublished study prepared by Imperial Chem

- ical Industries PLC, Brixham Laboratory. 7 p.

40427901 Status report Hill, R.; Tapp, J. (1987) Status Report on Cypermethrin (PP383) Fathead Minnow Lifecycle Study (P171/C): Laboratory Project I D P171/C. Unpublished study prepared by Imperial Chemicals Industries PLC. 13 p.

40529601 Status report Hill, R.; Tapp , J. (1988) Status Report of Cypermethrin (PP383) Fathead Minnow Lifecycle Study (P171/c). Laboratory Project ID P171/C. Unpublished study prepared by Imperial Chemicals Industries PLC, England. 4 p.

40641701 DER not

located Tapp, J.; Hill, R.; Maddock, B.; et al. (1988) "Cypermethrin: Determination of Chronic Toxicity to Fathead Minnow (Pimephales promelas) Full Lifecycle": Laboratory Project ID BL/B/3173. Unpublished study prepared by ICI PLC, Brixham Laboratory. 189 p.

41092101 addendum Tapp, J. (198 8) Cypermethrin: Determination of Chronic Toxicity to Fathead Minnow (Pimephales Promelas) Full Lifecycle. Addendum to Brixham Laboratory Report No. BL/B/3173: Laboratory ID No. FT5/86/P171/C. Unpublished study prepared by ICI Brixham Labor

- atory. 12 p.

92027026 Registrant

summary Adams, D. (1990) ICI Americas Inc. Phase 3 Summary of MRID 40641701

. Cypermethrin: Determination of the Chronic Toxicity to Fathead Minnow (Pimephales promelas): Report Nos. BL/B/3173/3507; Study No. P171/C.: 19 p.

40102100 Interim report Imperial Chemical Industries PLC (1987) Interim Report on Fish Lifecycle Study of Cypermethrin in Response to Data Call

- in Notice. Compilation of 1 study.



## 72

- 6 Aquatic org. accumulation

MRID Citation Reference

42868203 Check Fate

Data Giroir, E.; Stuerman, L. (1993) Cypermethrin (carbon 14) Bioconcentration by Bluegill Sunfish (Lepomis macrochirus): Lab Project Number:
191E5491E1: 40018: PC

- 0189. Unpublished study prepared by ABC Labs, Inc. 311 p.



## 72

- 7 Simulated or Ac tual Field Testing

MRID Citation Reference

40125601 Suitability

evaluation Cole, J.; Brantly, T.; Hodges, J.; et al. (1987) Cypermethrin: Evaluation during 1986 of "Speir II" (Alabama, USA) Farm Pond Drainage Basin and Ecosystem for Suitability for a 1987 Cyper

- methrin Study: I: Laboratory- Page 84 of 126

- Project ID: RJ0553B. Unpublished study prepared by Imperial Chemical Industries. 382 p.

40125602 Suitability

evaluation Cole, J.; Brantly, T.; Hodges, J.; et al. (1987) Cypermethrin: Evaluation during 1986 of "Mayo" (Alabama, USA) Farm Pond Drain

- age Basin and Ecosystem for Suitability for a 1987 Cypermethrin Study: I: Laboratory Project ID: RJ0557B. Unpublished study prep ared by Imperial Chemical Industries. 376 p.

40125603 Suitability

evaluation Hill, I.; Cole, J. (1987 ) Comparison of "Speir II" and "Mayo" Farm Ponds (Alabama) USA: Laboratory Project ID: M4428B. Unpublished study prepared by Imperial Chemical Industries . 20 p.

40804501 2016160 Rea, D.; Brantly, T.; Grimmett, J.; et al. (1988) Cypermethrin: Evaluation of the Impact of Aerially Sprayed Cypermethrin on the Aquatic Ecosystem of a Farm Pond in the Drainage Basin of a Cotton Crop: 1987: Laboratory Project ID RH0629B. Unpublished study prepared by ICI Agrochemicals. 744 p.

40804502 Suitability

evaluation Cole, J.; Brantly, T.; Hodges, J.; et al. (1988) Cypermethrin: Evaluation during 1986 of "Speir II" (Alabama, USA) Farm Pond Drainage Basin and Ecosystem fo r Suitability for a 1987 Cypermethrin Study: II: Laboratory Project ID RJ0591B. Unpub

- lished study prepared by ICI Agrochemicals. 508 p.

41011501 addendum Sadler, J. (1989) Cypermethrin: Addendum to RJ0629B: Evaluation of the Impact of Aerially Sprayed Cypermethrin on the Aquatic Eco

- system of a Farm Pond in the Drainage Basin of a Cotton Crop: 1987: Project ID:

PP383

- CF

- 04/2. Unpublished study prepared by Jeallot's Hill Research Station. 14 p.

41218801 Progress report Palmieri , M. (1989) Aquatic Mesocosm Study of Pesticide Products Containing the Active Ingredient Cypermethrin: Progress Rept. 1: Study No.

A89

- 2847. Unpublished study prepared by Wildlife International, Ltd. 17 p.

41336201 Progress report Palmieri, M. (1989) Aq uatic Mesocosm Study of Pesticide Products Containing the Active Ingredient Cypermethrin: Progress Report 3: FMC Study No. A89

- 2847. Unpublished study prepared by Wildlife International, Ltd. and FMC Corp. 5 p.

41403101 Progress report Palmieri, M. (1990 ) Aquatic Mesocosm Study of Pesticide Products Containing the Active Ingredient Cypermethrin: Progress Report 4: Lab Project Number: A89

- 2847. Unpublished study prepared by Wildlife International, Ltd. in association with FMC Corp. 55 p.

41466301 Progres s report Palmieri, M. (1990) Aquatic Mecocosm Study of Pesticide Products Containing the Active Ingredient Cypermethrin: Progress Report. Unpublished study prepared by Wildlife International, Ltd. 7 p.

41541101 Progress report Palmieri, M. (1990) Aquatic Mesocosm Study of Pesticide Products Containing the Active Ingredient Cypermethrin: Progress Report 6: Lab Project No. A89

- 2847. Unpublished study prepared by Wildlife International, Ltd. 14 p.

41616201 Progress report Palmieri , M. (1990) Aquatic Mesocosm Study of Pesticide Products Containing the Active Ingredient Cypermethrin: Progress Report 7: Project

Number: A89

- 2847. Unpublished study prepared by Wildlife International, Ltd., and FMC Corp. 14 p.- Page 85 of 126

- 41670701 Progress report Palmeri, M. (1990) Aquatic Mesocosm Study of Pesticide Products Containing the Active Ingredient Cypermethrin: Progress Report 8: Lab Project Number: A89

- 2847. Unpublished study prepared by Wildlife International, Ltd., and FMC Corp. 14 p.

41732501 Progr ess report Palmieri, M. (1990) Aquatic Mesocosm Study of Pesticide Product Containing the Active Ingredient Cypermethrin: Progress Report 9: Project

Number: A89

- 2847. Unpublished study prepared by Wildlife International, Ltd and FMC Corp. 13 p.

41800601 Progress report Palmieri, M. (1991) Aquatic Mesocosm Study of Pesticide Products Containing the Active Ingredient Cypermethrin: Progress Report 10. Lab Project Number: A89

- 2847. Unpublished study prepared by Wildlife International, Ltd. and FMC Corp. 12 p.

41862501 Progress report Palmieri, M. (1991) Aquatic Mesocosm Study of Pesticide Products Containing the Active Ingredient Cypermethrin: Progress Report 11: Lab Project Number: A89

- 2847. Unpublished study prepared by Wildlife International, Ltd. & FMC Corp. 58 p.

42148201 DER not

located Palmieri , M.; Freda, J.; Krueger, H.; et al. (1991) An Evaluation of the Impact of Cypermethrin Exposure on Managed Aquatic Ecosystems: Lab Project Number: 104

- 160: A89

- 2847. Unpublished study prepared by
Wildlife International Ltd. 1612 p.

40125604 Protocol Hil l, I. (1987) Protocol

-- Cypermethrin: A Study of the Impact of Aerially Sprayed Cypermethrin on the Aquatic Ecosystem of a Farm Pond in the Drainage Basin of a Cotton Crop: Laboratory Project ID: 383/CF/04. Unpublished study prepared by Imperial Chemical In dustries. 31 p.

40967301 Addendum Sadler, J.; Hill, I. (1989) Cypermethrin: Addendum to RJ0629B ...; Evaluation of the Impact of Aerially Sprayed Cypermethrin on the Aquatic Ecosystem of a Farm Pond in the Drainage Basin of a Cotton Crop; 1987: Project I D; PP383

- CT

- 04/1. Unpublished study prepared by ICI Agrochemicals. 11 p.

41293901 Progress report Palmieri, M. (1989) Aquatic Mesocosm Study of Pesticide Products Containing the Active Ingredient Cypermethrin: Progress Report 2: Lab Project Number: A89/2 847. Unpublished study prepared by Wildlife International, Ltd. in Association with FMC Corp. 5 p.

42081101 Progress report Palmieri, M. (1991) Aquatic Mesocosm Study of Pesticide Products Containing the Active Ingredient Cypermethrin: Progress Report 14 : Lab Project Number: A89

- 2847. Unpublished study prepared by Wildlife International, Ltd. and FMC Corp. 8 p.

Acc No.

250506

128704 2016157 Jaber , M.; Hawk, R. (1983) Cypermethrin: Aquatic Ecological Effects under Field Use Conditions in Cotton: Selma, Alabama, 1980: Re

- port Series TMUE0026/B. (Unpublished study received Mar 24, 1983 under 10182

- 65; submitted by ICI Americas, Inc., Wilming

- ton, D E; CDL:250506

- A)

152737 DER not

located Getty, C.; Wilkinson, W.; Swaine, H.; et al. (1983) Cypermethrin: Effects of Multiple Low Rate Applications on Experimental Ponds: Report No. RJ0182B. Unpublished study prepared by Imperial Chemical Industries
PLC. 62 p.

155770 Open lit Crossland, N. (1982) Aquatic toxicology of cypermethrin. II. Fate and biological effects in pond experiments. Aquatic Toxicology 2:205

- 222

.- Page 86 of 126

- 155772 Open lit Crossland, N.; Shires, S.; Bennett, D. (1982) Aquatic toxicolofy of

cyperm ethrin. III. Fate, and biological effects of spray drift deposits in fresh water adjacent to agricultural land. Aquatic Toxicology 2:253

- 270

. 

## 141

- 1 Honey bee acute contact

MRID Citation Reference

155740 2016158 Bull, J.; Wilkinson, W. (1980) Cypermethrin: Laboratory Determina

- tion of the Acute Toxicity to Honeybees of Technical Material and an Emulsifiable Concentrate (GFU 061): Report Series: RJ 0169B. Unpublished study prepared by ICI Plant Protection Div. 35 p.

44544208 2016183 Halsall, N. (1998) Betacypermethrin 10 EC: Acute Toxicity to Honey Bees (Apis mellifera): Lab Project Number: PWT 131/963589: PWT 131. Unpublished study prepared by Huntingdon Life Sciences Ltd. 29 p.

92027047 Registrant Summary Lew is, G. (1990) ICI Americas Inc. Phase 3 Summary of MRID 00155740. Cypermethrin: Acute Contact and Oral Toxicity to Honey Bees (Apis mellifera: Report No. RJ0169B; Study No.: PP383/CM/01. Prepared by ICI Agrochemicals Jealott's Hill Research Station. 14 p.

92027048 Registrant Summary Lewis, G. (1990) ICI Americas Inc. Phase 3 Summary of MRID 40274001. Cypermethrin: Toxicity of Residues on Foliage to Honey Bees (Apis mellifera): Report No. RJ0587B; Study No.: PP383CM03. Prepared by ICI Agrochemicals Jealott 's Hill Research Station. 13 p.

47800504 Open lit

- DER

not located Decourtye, A.; Devillers, J.; Genecque, E.; et al. (2005) Comparative Sublethal Toxicity of Nine Pesticides on Olfactory Learning Performances of the Honeybee Apis mellifera. Archives of Environmental Contamination and Toxicology 48:242

- 250.

47800530 Open lit

- DER

not located Chauzat, M.; Carpentier, P.; Martel, A.; et al. (2009) Influence of Pesticide Residues on Honey Bee (Hymenoptera: Apidae) Colony Health in France.

Environ. Entomol. 38(3):514

- 523.



## 141

- 2 Honey bee residue on foliage

MRID Citation Reference

40274001 2016159 Gough, H.; Jackson, D.; Wilkinson, W. (1987) Cypermethrin: Toxicity of Residues on Foliage to Honey Bees (Apis mellifera): Laborato

- ry Project ID: RJ0587B. Unpublished study prepared by ICI Plant Protection Division. 27

p.

41699401 Registrant

summary Lewis, G. (1990) Phase 3 Summary of MRID 40274001 : Cypermethrin: Toxicity of Residues on Foliage to Honey Bees (Apis mellifera): Lab Proj ect Number: RJ0587B: PP383CM03. Unpublished study pre

- pared by ICI Agrochemicals, Jealotts Hill Research Station. 13 p.



## 141

- 3 Toxicity to Non Target Insects

5009995 Open lit

2079040 Waddill , V.H. (1978) Contact toxicity of four synthetic pyrethroids and methomyl to some adult insect parasites. Florida Entomologist 61(1):27

- 30.- Page 87 of 126

- 127368 Open lit Harris, C.; Turnbull, S. (1978) Laboratory studies on the contact toxicity and activity in soil of four pyrethroid insecticides . Canadian Entomologist 110(Mar):285

- 288. (Submitter AW

- 81

- 0099; also In unpublished submission received Apr 8, 1983 under 39398

- 16; submitted by Sumitomo Chemical America, Inc., New York, NY; CDL:249939

- B)



## 850.1790 Ch ironomid Sediment Toxicity Test

MRID Citation Reference

46871501 Summary of multiple

studies Giddings, J. (2006) Overview of Sediment Toxicity Studies with Synthetic Pyrethroids. Project Number: 06723, 06273. Unpublished study prepared by Compliance Services International. 62 p.



## 850.7100 Data reporting for environmental chemistry methods

MRID Citation Reference

47053001 DER not

located Robinson, N. (2007) Residue Analytical Method for the Determination of Residues of Bifenthrin, Cypermethrin, Cyfluthrin, Deltamethrin, Esfenvalerate, Fenpropathrin, Lambda

- cyhalothrin and Permethrin in Sediment. Unpublished study prepared by Syngenta Jealo tts Hill International. 185 p.

47053002 DER not

located Reed, R. (2006) Laboratory Validation: Validation of the Residue Analytical Method: Residue Analytical Method for the Determination of Residues of Bifenthrin, Cypermethrin, Cyfluthrin, Deltamethrin, Esfenvalerate, Fenpropathrin, Lambda

- Cyhalothrin and Permethrin in Sediment: Final Report. Project Number: MLI/06/02, ML06/1286/PWG. Unpublished study prepared by Morse Laboratories Inc. 418 p.



## 850.1735 Whole sediment: acute freshwater invertebra tes

MRID Citation Reference

47946601 Contract draft

available Picard, C. (2009) 10

- Day Toxicity Test Exposing Freshwater Amphipods (Hyalella azteca) to Cypermethrin Applied to Glen Charlie Pond Sediment
Under Static

- Renewal Conditions. Project Number: 13656/6130, 100808/OPPTS/10/DAY/HYALELLA/MA/SED. Unpublished study prepared by Springborn Smithers Laboratories. 117 p.

47946602 Contract draft

available Picard, C. (2009) 10

- Day Toxicity Test Exposing Freshwater Amphipods (Hyalella azteca) to Cypermethrin Applied to Formulated Sediment Under
Static

- Renewal Conditions. Project Number: 13656/6129. Unpublished study prepared by Springborn Smithers Laboratorie s. 118 p.

47946603 Contract draft

available Picard, C. (2009) 10

- Day Toxicity Test Exposing Freshwater Amphipods (Hyalella azteca) to Cypermethrin Applied to California Sediment 2 Under
Static

- Renewal Conditions. Project Number: 13656/6127. Unpublished

st udy prepared by Springborn Smithers Laboratories. 119 p.

47946604 Contract draft

available Picard, C. (2009) 10

- Day Toxicity Test Exposing Freshwater Amphipods (Hyalella azteca) to Cypermethrin Applied to CA Sediment 1 Under Static

-- Page 88 of 126

- Renewal Conditions. Pro ject Number: 13656/6126. Unpublished study prepared by Springborn Smithers Laboratories. 118 p.

47946605 Contract draft

available Picard, C. (2009) 10

- Day Toxicity Test Exposing Freshwater Amphipods (Hyalella azteca) to Cypermethrin Applied to California Sediment 3 Under
Static

- Renewal Conditions. Project Number: 13656/6128, 100808/OPPTS/10/DAY/HYALELLA/CAS3. Unpublished study prepared by Springborn Smithers Laboratories. 116 p.

46591504 2086351 Putt, A. (2005) Cypermethrin

- Toxicity to Midge (Chironomus tentans) During a 10

- Day Sediment Exposure. Project Number: 13656/6110. Unpublished study prepared by Springborn Smithers Laboratories. 88 p.

46725701 2086353 Putt, A. (2005) Cypermethrin

- Life

- Cycle Toxicity Test with Midge (Chironomus tentans) During a 60

- Day Sediment Exposure. Project Number: 13656/6112. Unpublished study prepared by Springborn Smithers Laboratories. 117 p.



# Non Guideline Selections

90000 2016265

summary pg 29 Brown, S.M.; Edwards, P.J. (1980) Cypermethrin (PP383): Effects on Earthworms,~Lumbricidae?~: Report Series RJ 0151B. (Unpublished study received Dec 30, 1981 under 10182

- 64; prepared by Imperial Chemical Industries, Ltd., England, su bmitted by ICI Americas, Inc., Wilmington, Del.; CDL:070559

- O)

90001 2016265

summary pg 29 Cole, J.F.H.; Wilkinson, W. (1980) Cypermethrin (PP383): Effects on Soil Microarthropods: Report Series RJ 0150B; 5B 4/6. (Unpub

- lished study received Dec 30, 1981 under 10102

- 64; prepared by Imperial Chemical Industries, Ltd., England, submitted by ICI Americas, Inc., Wilmington, Del.; CDL:070559

- P)

90059 2016265

summary pg 56

2016265

summary pg
57 Curl, E.A.; Milner, S.D. (1980) Cy permethrin: Accumulation and De

pletion of Radioactive Residues in the Tissues of Mallard Duck and Bobwhite Quail following Daily Dosing: Report Series RJ 0147B. (Unpublished study received Dec 30, 1981 under 10182

- 64; prepared by Imperial Chemical Indust ries Ltd., England, submit

- ted by ICI Americas, Inc., Wilmington, Del.; CDL:070560

- K)

Leahey 1977. Similar study with Permethrin and Mallard and Japanese
Quail

138935 DER not

located Hill, I. (1984) A Review of the Effects of Pyrethrum and Synthetic

P yrethroids on Non

- target Organisms in Terrestrial and Aquatic Environments: Report Series RJ0349B. (Unpublished study re

- ceived Jan 30, 1984 under 10182

- 65; prepared by Imperial Chemi

- cal Industries, Ltd., Eng., submitted by ICI Americas, Inc., Wilmingto n, DE;
CDL:252348

- A)

149692 DER not

located Rajakulendran, S.; Plapp, F. (1982) [Comparative Toxicities of Five Synthetic Pyrethroids to Various Parasites and Predators]. Un

published compilation. 8 p.

149693 DER not

located Zoecon Corp. (1983) Effects on Pollinators:[Fluvalinate]. Unpub

- lished compilation. 15 p.

155785 Open lit Stephenson, R.; Choi, S.; Olmos

- Jerez, A. (1984) Determining the- Page 89 of 126

- toxicity and hazard to fish of a rice insecticide. Crop Protec

- tion 3(2):151

- 165.

155 797 Check SETAC publications Hill, I.; Hamer, M. (1984) The Influence of Adsorption and Degradation on the Toxicity of Permethrin, Cyperthrin and Cyhalothrin to Aquatic Organisms. Unpublished documents presented at the SETAC Fifth Annual Meeting, November, 1984; Washington, D.C. 2 p.

40135801 DER not

located Kaminski, B. (1987) Cypermethrin: Effect on Earthworms and Bio

accumulation Potential of Residues. Unpublished study prepared by ICI Americas. 7 p.

40135802 DER not

located Arnold, J.; Edwards, P. (1983) Cypermethrin: Effects on Earthworms Lumbricidae of Repeated Annual Field Applications: Lab Project ID: RJ0311B. Unpublished study prepared by ICI Plant Protec

- tion Division. 36 p.

40135803 DER not

located Curl, E.; Leahey , J. (1984) Permethrin and Cypermethrin: Character

isation of Radioactive Residues Found in Earthworms Which Have Been Exposed to Soil Treated with [Carbon 14]

- Permethrin and [Carbon 14]

- Cypermethrin: Lab Project ID: RJ0343B. Unpublished study prepared by ICI Plant Protection Division. 36 p.

40135804 DER not

located Edwards, P.; Arnold, J. (1984) Cypermethrin and Permethrin: Accumu

lation of [Carbon 14]

- Cypermethrin and [Carbon 14]

- Permethrin Equivalents by the Earthworms Allolobophora calliginosa and L um

bricus terrestris: Lab Project ID: RJ0341B. Unpublished study prepared by ICI Plant Protection Division. 30 p.

40135805 DER not

located Collis, W.; Leahey, J. (1984) Cypermethrin: Evaluation of Bio

accumulation Potential in Quail Dosed with Earthwor ms Containing Cypermethrin Derived Residues: Lab Project ID: RJ0330B. Unpub

lished study prepared by ICI Plant Protection Division. 35 p.

40135806 DER not

located Cavell, R.; Leahey, J.; Lloyd, S. (1984) Cypermethrin: Evaluation of

Bioaccumulation Poten tial in Rats Dosed with Earthworms Con

- taining Cypermethrin Derived Residues: Lab. Project ID: RJ0352B. Unpublished study prepared by ICI Plant Protection Division. 35 p.

40135807 DER not

located Leahey, J.; Curl, E.; Edington, C.; et al. (1985) Permeth rin and Cypermethrin: Identification of a Major Component of the Radio

- active Residue in Earthworms Exposed to Soil Treated with [Carbon

- 14]

- Benzyl

- labeled Cypermethrin (Addendum to RJ0343B): Lab Project No.: RJ0391B. Unpublished study prepared by ICI Pla nt Protection Division. 21 p.

40359505 Open lit

DER not

located Watters, F.; White, N.; Cote, D. (1983) Effect of temperature on toxicity and persistence of three pyrethroid insecticides applied to fir plywood for the control of the red flour beetle (coleoptera: Tenebrionidae. Journal of Economic Entomology 76: 11

- 16.

44388401 Registrant

Assessment Maund, S.; Travis, K.; Hendley, P.; et al. (1997) Evaluation of the Ecological Risks of Cotton Pyrethroids to Aquatic Ecosystems: Lab Project Number: RC0009B. Unpublished study prepared by Zeneca Agrochemical (Zeneca Ltd.). 30 p.

44396501 Registrant

Assessment Solomon, K. (1997) Review of the Laboratory Aquatic Organism Toxicity Data for the Cotton Pyrethroids: Distributional Analysis of the Acute- Page 90 of 126

- Toxicity Data. Unpublished study prepared by University of Guelph. 76

p.

44396502 Registrant

Assessment Travis, K. (1997) A Modified Tier II Aquatic Exposure Analysis of Cotton Pyrethroids, Incorporating Landscape

- Level Exposure Factors: Lab Project Number: PYRETHROIDS \ 3. Unpublished study prepared by Zeneca Agrochemical (Zenec a Ltd). 221 p.

44396503 Registrant

Assessment Giddings, J. (1997) Aquatic Mesocosm and Field Studies with Cotton Pyrethroids: Observed Effects and Their Ecological Significance: Lab Project Number: 97

- 6

- 7014: 13656.0497.6100.900. Unpublished study prepared by Springborn Labs., Inc. 102 p.

44396504 R egistrant

Assessment Ritter, A.; Williams, W.; Cheplick, J. (1997) Tier 1 and Tier 2: Modeling of Pyrethroid Exposure to Aquatic Nontarget Organisms Associated with Use on Cotton: Lab Project Number: WEI 794.01: PWG. Unpublished study prepared by Waterborn e Environmental, Inc. (WEI). 80 p.

45245501 Registrant

Assessment Soderlund, D.; Clark, J.; Mullin, L. et al. (2000) Pyrethroid Insecticides: Is there a Common Mechanism of Mammalian Toxicity?: Lab Project
Number: PWG FQPA 2000

- 01. Unpublished study prep ared by Pyrethroid Working Group. 144 p.

45867701 DER not

located

- not a cypermethrin study Smith, E.; Du Preez, L.; Solomon, K. (2003) Field Exposure of Xenopus laevis to Atrazine and Other Triazines in South Africa: Exposure
Characterization and Asses sment of Laryngeal and Gonadal Responses: Final Report: Lab Project Number: SA

- 01B: 109

- 02: C1. Unpublished study prepared by The Institute of Environmental and Human Health, Texas Tech University and School of Environmental Sciences and Development Potche fstroom, University for CHE. 91 p.

45867709 DER not

located

– not

a cypermethrin study Smith, E.; Du Preez, L.; Solomon, K. (2003) Field Exposure of Xenopus laevis to Atrazine and Other Triazines in South Africa: Feasibility Study
for Site Characterizati on and Assessment of Laryngeal and Gonadal Responses: Final Report: Lab Project Number: SA

- 01A: 2011

- 02: C1. Unpublished study prepared by The Institute of Environmental and Human Health Texas Tech University and School of Environmental
Sciences and Develo pment Potchefstroom University for CHE. 104 p.

46051301 Registrant

Assessment Ritter, A.; Williams, W. (2003) Tier 2 Modeling of Pyrethroid Compounds Exposure to Aquatic Nontarget Organisms Associated with Use on Cotton: Final Report. Project Number: WEI/794/03. Unpublished study prepared by Waterborne Environmental, Inc. (WEI). 180 p.

47050501 Registrant

Assessment Breckenridge, C.; Holden, L. (2007) Evidence for Separate Mechanism of Action for Type I and Type II Pyrethroid Insecticides. Project Num ber:
PWG/TOX/2007/01. Unpublished study prepared by Pyrethroid Working Group. 144 p.

47050502 Open lit Burr, S.; Ray, D. (2004) Structure

- Activity and Interaction Effects of 14 different Pyrethroids on Voltage

- Gated Chloride Ion Channels. Toxicological Sc iences 77(2):341

- 346.

47506602 DER not

located Hall, L.; Killen, W.; Anderson, R. (2008) A Comparison of Sediment Sampling Methods for Pyrethroids in Urban/Residential Sediments of California Streams and Additional Pyrethroid Sampling in Pleasant
Grove Cr eek Backwater Surrogate Sites

- Pyrethroid: Assessment.- Page 91 of 126

- Project Number: T001584/08. Unpublished study prepared by Wye Research and Education Center. 62 p.

47506603 DER not

located Hall, L.; Killen, W.; Anderson, R.; et. al. (2008) An Assessment of

Benthic Communities with Concurrent Physical Habitat, Pyrethroid, and Metals Analysis in an Urban and Residential Stream in California in

2006 and 2007

- Pyrethroid: Assessment. Project Number: T001523/08. Unpublished study prepared by Wye Research and Education Cen ter and Northern Illinois University. 229 p.

47543609 Published deNoyelles, F.; Dewey, S.; Huggins, D.; et al. (1994) Aquatic Mesocosms in Ecological Effects Testing: Detecting Direct and Indirect
Effects of Pesticides. P. 577

- 603 in Ecological Risk Assessment,
CRC Press.

47929401 Progress report Giddings, J. (2009) Pyrethroid Working Group Sediment Toxicity Testing Program: Progress Report #1: (Hyalella azteca). Project Number: 09713. Unpublished study prepared by Compliance Services

International. 26 p.

47929402 Overview Giddings, J. (2009) Pyrethroid Working Group Sediment Toxicity Testing Program: Overview of Part 1 (Comparison of Sediments with Different Organic Content): (Hyalella azteca). Project Number: 09718. Unpublished study prepared by Co mpliance Services International. 25

p.

47929403 Progress report Giddings, J. (2009) Pyrethroid Working Group Sediment Toxicity Testing Program: Progress Report #2: (Hyalella azteca). Project Number: 09744. Unpublished study prepared by Compliance Services International. 11 p.

47929404 Registrant

Assessment Hall, L.; Killen, W.; Anderson, R.; et al. (2009) An Assessment of the Potential Influence of Physical Habitat, Pyrethroids and Metals of
Benthic Communities in a Residential Stream in California in 2008: (Tubificidae, Paratanytarsus sp., Hyalella sp., Phy sa sp., Dugesia tigrina and Dero digatata): Final Report. Project Number: T001605/09. Unpublished study prepared by Compliance Services International. 126

p.

47929405 DER not

located Hall, L.; Killen, W.; Alden, R. (2007) An Assessment of Benthic Communities with Concurrent Physical Habitat, Pyrethroid, Metals and PAH Analysis in an Urban and Residential Stream in California: (Seed Shrimp, Snails, Chironomids, Oligochaetes and Black Fl ies). Unpublished study prepared by Wye Research and Education Center, and Northern Illinois University. 173 p.

47929406 DER not

located Hall, L.; Killen, W.; Anderson, R. (2009) A Comparison of Targeted Sedimemt Sampling Methods for Pyrethroids in Urban/ Residential Sediments of a California Stream in 2008: (Hyalella azteca): Final Report. Project Number: T001763/09. Unpublished study prepared by Wye Research and Education Center. 56 p.

47944033 Comparison

summary Wisk, J. (2010) Comparison of Ecotoxicolo gy Endpoints for Alpha

Cypermethrin and Cypermethrin. Project Number: 2010/7002965/OCR, 2010/7002965. Unpublished study prepared by BASF Agricultural Products Center. 9 p.- Page 92 of 126

- 41068006 Open lit

different

chemical Bradbury, S.; Coats, J.; McKim, J. (1985) Dif ferential toxicity and uptake
of two fenvalerate formulations in fathead minnows (Pimepholes promelas). Environmental Toxicology and Chemistry 4:531

- 541.



## 129064 Zeta

- Cypermethrin Ecoeffects Bibliography

72

- 2 Acute Toxicity to Freshwater Inverte brates

MRID Citation Reference

41968210 2046958
Contract draft Ward, T.; Boeri, R. et al. (1991) Acute Toxicity of FMC 56701 Tech

nical and Cypermethrin Technical to the Daphnid, Daphnia magna: Lab Project Number: 90186

- FMC: A90

- 3310. Unpublished study prepared by Resource Analysts, Inc. 46 p.

43293501 2046962
Contract draft Wheat, J.; Evans, J. (1994) Zetacypermethrin Technical and Cyp ermethrin Technical : Comparative Acute Toxicity to the Water Flea (Daphnia magna), under Flow

- Through Test Conditions: Lab Project Number: J9210001B: A92/3636. Unpublished study prepared by Toxikon Environmental Sciences. 76 p.



## 72

- 1 Acute Toxicity to Fr eshwater Fish

41868208 or
41968208? 2046956
Contract draft Overman, M.A., M.G. Barron and D.D. Vaishnav (1990) Cypermethrin

- S (FMC 56701): Acute Toxicity to Rainbow Trout ( Oncorhynchus mykiss )

Under Flow

- Through Test Conditions. Laboratory Project ID 3903026

- 0700

- 3140. FMC Study No. A89

- 2935

- 01. Prepared by Environmental Science and Engineering, Inc., Gainesville, FL. Submitted by FMC Corporation, Philadelphia, PA. EPA MRID No. 41968208.



## 7

- 3 Acute Toxicity to Estuarine/Marine Organisms

MRID Cit ation Reference

41968211 2046959
Contract draft Overman, M.; Barron, M.; Vaishnav, D. (1990) Cypermethrin

- S (FMC 56701): Acute Toxicity to Sheepshead Minnow (Cyprinodon variega

tus ) under Flow

- through Test Conditions: Lab Project Number:

3903026

- 0600

- 3140: A89

- 2937

- 01. Unpublished study prepared by Environmental Science and Engineering, Inc. 47 p.

41968213 2046961
Contract draft Ward, T.; Boeri , R. (1991) Acute Toxicity of FMC 56701 Technical and Cypermethrin Technical to the Mysid, Mysidopsis bahia: Lab Project

Number: 90187

- FMC: A90

- 3309. Unpublished study prepared by Resource Analysts, Inc. 52 p.

42411001

or 41968212 2046960

contract
draft

- signed copy missing Yurk, J.; Chandler, A. (1992) FMC 45806 : Acute Toxicity to Sheepshead Minnow (Cyprinodon variegatus) under Flow

- through Test Conditions: Amended Final Report : Lab Project Number: A89

- 3111: 3903026

- 0350

- 3140: C

- BIO90.1/FMC458CV.2. Unpublished study prepared by Hunter/ESE, Inc. 43 p.

42444601 2016179 in

109702 Cypermethrin Ward, T.; Boeri, R.; Palmieri, M. (1992) Acute Toxicity of FMC 56701 Technical and Cypermethrin Technical to the Mysid, Mysidopsis bahia: Final Report: Lab Proj ect Number: 91186

- FMC: A91

- 3454.- Page 93 of 126

- Unpublished study prepared by Resource Analysts, Inc. 50 p.

41968212 2046960 Chandler, A.B. (1990) FMC 45806: Acute Toxicity to Sheepshead Minnow ( Cyprinodon variegates ) Under Flow

- Through Test Conditions. Laboratory Proj ect No. 3903026

- 0350

- 3140. Study Performed by Environmental Science and Engineering, Inc., Gainesville, FL. Submitted by FMC Corporation, Philadelphia, PA. EPA MRID No.

42968212.- Page 94 of 126

- 

### Appendix A. Alpha

- Cypermethrin Bridging Strategy

EFED’s Interim Policy for Stereoisomeric Pesticides ( 2000 ) outlines the minimal dataset required to determine whether enriched enantiomeric mixtures are of greater environmental concern than the already registered racemic mixture. This data is necessary be cause enantiomers may exhibit selective geological effects (stereoselectivity) towards inherently chiral

- rich organisms. As part of the bridging strategy for alpha

- cypermethrin, the registrant, BASF, submitted the required minimal dataset for the Agency to assess the relative behavior of the enriched enantiomeric mixture, alpha

- cypermethrin, versus the racemic mixture, cypermethrin (PC Code 109702).

In a memorandum, dated May 10, 2011, the Agency denied the bridging strategy for alpha

- cypermethrin

to racemic and zeta

- cypermethin (USEPA, 2011; DP358283), citing lack of sufficient information to evaluate the environmental fate and toxicity data. Additional meetings and submissions were completed concluding with the current appendix outlining the Agency’s approach to briding the data from the

racemic and zeta

- cypermethrin to alpha

- cypermethrin.

The agency has previously allowed the environmental fate and ecotoxicity database for cypermethrin to bridge with the enriched enantiomeric mixture, zeta

- cypermeth rin (PC Code 129064). Based on the

similarities in the chemical properties and toxicological endpoints discussed below , environmental fate and ecotoxicity data are bridged between racemic cypermethrin and the enriched isomeric mixtures (i.e., alpha

- cypmert hin and zeta

- cypermethrin) . For the purposes of risk assessment, chemical

- specific alpha

cypermethrin data will be used where available. Where there are no chemical specific data for alpha

cypermethrin, data will be bridged from the database available for the cypermethrins (racemic and zeta

cypermethrin).

Comparison of Racemic Cypermethrin with the Zeta

- and Alpha

- Cypermethrin

Racemic cypermethrin consists of eight stereoisomers with two optically active centers (designated “R” and “S”). The isomers fa ll into four groups of two each. As seen in Table 1 below, zeta

- cypermethrin also consists of the same eight stereoisomers, but in different proportions. Zeta is enriched in isomers with the second “S” configuration. However, both racemic and zeta cyper methrin contain 50% cis and

50% trans isomers. Alpha

- cypermethrin consists of only two of the eight stereoisomers, both of which are “cis.” These two isomers make up 22% of racemic and 25% of zeta

- cypermethrin.

The result of this comparison is that racem ic and zeta cypermethrin are more similar to each other, than either of them is to alpha

- cypermethrin. In racemic, each of the 4 isomer groups is 22

- 28% of the total, and in zeta, each group is 25% of the total. Alpha contains 100% of cis

- 2 isomers, and none of the other three isomers groups. Therefore, if there are differences in the environmental fate of the eight isomers, this will be reflected as greater differences between racemic and zeta on one hand, and alpha on the other

hand.

Table A.1: Comp arison (%) of s tereoisomer composition of

r acemic, z eta

- and a lpha

- c ypermethrin Isomer group Isomer Racemic cypermerthrin Zeta cypermethrin Alpha cypermethrin

Cis

- 1 1R, cis

- R 14 3 0
1S, cis

- S 14 22 0 Group subtotal 28 25 0

Cis

- 2 1R, cis

- S 11 22 50- Page 95 of 126

- 

### 1S, cis

- R 11 3 50 Group subtotal 22 25 100

Trans

- 3 1R, trans

- S 11 22 0
1S, trans

- R 11 3 0 Group subtotal 22 25 0

Trans

- 4 1R, trans

- R 14 3 0
1S, trans

- S 14 22 0 Group subtotal 28 25 0 cis isomers (%) 50 50 100

Rationale for Bridging Fate Data

EFED received acceptable or supplemental data for the following studies using alpha

- cypermethrin :

• Aqueous photolysis,

• H ydrolysis,

• A dsorption/desorption,

• A erobic aquatic metabolism, and

• A erobic soil metabolism.

Table A. 2 provides a comparison of environmental fate data available for cypermethrin and alpha

cypermethrin. T he hydrolysis (67 days for vs. 188 , for alpha

- and racemic, respectively ), aqueous photolysis (5 days vs. 36), and aerobic soil metabolism (21 days vs. 60 ) data for alpha

- cypermethrin indicate that it is somewhat less persistent than the racemic or enriched isomeric mixture zeta

cypermethrin. However, t he aerobic aquatic metabolism and aerobic soil metabolism studies for alpha

cypermethrin were conducted on one sediment or soil, respectively, so differences between the enriched isomeric and racemic mixtures may not be fully understood.

The 2000 EFED Interim Policy for Stereoisomeric Pesticides states, 

### an aerobic soil metabolism study (GLN 162

- 1/835.3300) i s required as part of the minimal data set for enantiomeric enriched mixtures. If the biotransformation rates and degradation products are substantially similar for the racemic and the enantiomeric enriched mixture, then no additional environmental fate d ata are needed. If on the other hand, the biotransformation rates and degradation products for the racemic and enantiomeric enriched mixture differ in a manner that suggests greater potential risk, then additional environmental fate data may be required o n a case

- by

- case basis. EFED has not

received alpha

- cypermethrin specific data for soil photolysi s and anaerobic soil metabolism; however, the registrant provided citations for racemic cypermethrin and zeta

- cypermethrin data that was used in the Reregistra tion Eligibility Decision for Cypermethrin (RED, USEPA 2005). Where there are no chemical specific data for alpha

- , data are bridged from the database available for the cypermethrins (racemic and

zeta

- cypermethrin).

Table A.2 . Available fate data for the cypermethrins.

Input Parameter Racemic Cypermethrin Endpoint Alpha

Cypermethrin Endpoint Data Source (s)

Soil Photolysis Half

life 55 days NA Cyper

– MRID 42129001

Aqueous Photolysis

Half

- life 36.2 days 5 days Cyper

- MRID 42395701 Alpha

- MRID 48425003- Page 96 of 126

- Aerobic Soil

Metabolism Half

- life 60 days 2 8 days Cyper

– MRID 42156601 Alpha

– MRID 48425006

Anaerobic soil

Metabolism Half

- life 53.3 days (sandy loam, acid label) 63 days (sandy loam, alcohol label) NA Cyper

- MRID 42156602

Aerobic Aquatic

Metabolism Half

- life (20°C) 8.9 days 10.1 days 2.8

, 11 days Cyper

- MRID 45920801 Alpha

- MRID 48425011 and 48425012

Anaerobic Aquatic

Metabolism Half

- life 13.8 days (clay loam, benzyl label) 16.5 days (clay loam, cyclopropyl label) NA Cyper

- MRID 44876105

Adsorption/Desorption (Koc) 328,500 (Sand) 134,900 (Sandy loam) 82,600 (Silty loam) 20,800 (Clay loam) 26,492

– 144,662 Cyper

- MRID 42129003 Alpha

– MRID 48425008

Hydrolysis Half

- life (pH 7 , 25 °C ) 188 days 67 days Cyper

– MRID 42620501 Alpha

- MRID 48425002



### Rationale for Bridging Eco logical d ata

EFED received acceptable or supplemental data for the following studies using alpha

- cypermethrin :

• Avian oral toxicity,

• Avian oral toxicity with a passerine species,

• Avian dietary toxicity,

• Avian reproduction,

• Honeybee acute contact toxicity,

• Acute freshwater fish toxicity,

• Acute freshwater invertebrate toxicity,

• Aquatic vascular plant toxicity,

• Aquatic nonvascular plant toxicity, and

• Tier II vegetative vigor.

Tables A.3 through A.5 provide a comparison of ecotoxicity data available for racemic cypermethrin,

zeta

- cypermethrin and alpha

- cypermethrin. Based on the available information, alpha

- cypermethrin has equal or lesser toxicity than either the racemic or zeta mixture. Where there are no chemical specific data for alpha

- , data are bridged from the database available for the cypermethrins (racemic and zeta

cypermethrin).

TABLE A. 3 . Available ecological effects data for terrestrial animals exposed to cypermethrins.

Guideline Description Racemic Cypermethrin Endpoint Alpha

Cypermethrin Endpoint Zeta

Cypermethrin Endpoint Data Gap? Comments

850.2100 Avian oral toxicity Bobwhite quail LD50 > 2,000 mg a.i./kg

- bw (MRID 44546024 Acceptable) Bobwhite quail LD50 > 2025 mg a.i./kg

- bw

NOAEL = 2025

mg a.i./kg

- bw NA No The alpha

cypermethrin data

will be used.- Page 97 of 126

- (MRID 47944015 Acceptable)

850.2100 Avian oral toxicity

Passerine NA Zebra finch LD50 = 1370 mg a.i./kg

- bw NOAEL < 504 mg a.i./kg

- bw (MRID 47944016) Supplemental Qualitative) NA Yes The passerine data

available is based on a supplemental study and may not be acceptable for calculating RQs.

850.2200 Avian dietary toxicity Mallard duck LC50 > 2,634 mg a.i./kg

- diet (MRID 00090071 Acceptable) Bobwhite quail

LC50 > 4690 mg a.i./kg

- diet

NOAEC = 63 1 mg a.i./kg

- diet

LOAEC = 1250 mg a.i./kg

- diet (MRID 47944017 Acceptable) NA No The alpha

cypermethrin data

will be used.

850.2300 Avian reproduction Mallard duck and bobwhite quail NOAEC > 50 mg a.i./kg

- diet (MRID 00090072

and 00090074) Supplemental Bobwhite quail NOAEC < 48 mg a.i./kg

- diet LOAEC = 48 mg a.i./kg

- diet (MRID 47944018

Supplemental Qualitative) Mallard duck and bobwhite quail

NOAEC = 50

ppm LOAEC > 50

ppm (MRID 00090073

and 00090074

Acceptable) No The alpha

cypermethrin study

is not suitable for use in calculating RQs. Therefore,

the zeta

cypermethrin endpoint will be

used because it is a definitive endpoint.

850.3020 Honeybee

acute contact toxicity NA 24

- hr LD50 =

0.033 μ g a.i./bee (MRID 47944019

Supplemental Qualitative) 48

- hr LD50 =

0.023 μ g a.i./bee (Acc No. 260647

Acceptable) No The alpha

cypermethrin data

will be used.



### TABLE A

. 4 . Available ecological effects data for aquatic animals exposed to cypermethrins.

Guideline Description Racemic Cypermethrin Endpoint Alpha

Cypermethrin Endpoint Zeta

Cypermethrin Endpoint Data Gap? Comments

850.1075 Freshwater

fish

– Acute

toxicity Rainbow Trout LC50 = 0.39 μg

a.i./L (MRID

44546027 Acceptable) Rainbow trout

LC50 = 2.2 μg a.i/ L

NOAEC = 0.

96 μg a.i. /L

(MRID

47944207 Acceptable) NA No The alpha

- cypermethrin

data will be used.

850.1075 Saltwater

fish

– Acute

toxicity Sheepshead

minnow LC50 = 0.95 μg

a.i./L (MRID NA NA No The racemic cypermethrin endpoint will be used.- Page 98 of 126

- 00090075 Acceptable)

850.1010 Freshwater

invertebrates

– Acute toxicity Daphnid

48

- hr EC50 =

0.42 μg a.i./L (MRID

44546031 Acceptable) Daphnid

EC50 = 0. 067

μ g a.i. /L

NOAEC =

0. 028 μ g a.i. /L (MRID

47944208 Acceptable) Amphipod

96

- hr LC50 =

0.0036 μg

a.i./L (MRID

44423501 Acceptable) No Though alpha

- cypermethrin specific data is available, amphipods are known to be acutely more sensitive to pyrethroids than daphnids. Therefore, the zeta

cypermethrin endpoint will

be used.

850.1025

850.1035 Saltwater

invertebrates

– Acute toxicity Mysid shrimp

96

- hr LC50 =

0.00475 μg

a.i./L (MRID

42444601 Acceptable) NA NA No The racemic cypermethrin endpoint will be used.

850.1300 Freshwater

invertebrate

– life cycle

test NA NA NA Yes For the purposes of this risk

assessment a NOAEC value

based on acute:chronic ratio will be used ( 0.00059 μg a.i./L ).

850.1350 Saltwater

invertebrates

– life cycle

test Mysid shrimp

NOAEC =

0.000781 μg a.i./L

LOAEC =

0.00197 μg a.i./L (MRID

42725301 Acceptable) NA NA No The racemic cypermethrin endpoint will be used.

850.1400 Freshwater

fish

– early

life stage

test Fathead

minnow

NOAEC = 0.14 μg a.i./L

LOAEC = 0.33 μg a.i./L (MRID

00089039 Acceptable) NA NA No The racemic cypermethrin endpoint will be used.

850.1400 Saltwater

fish

– early

life stage

test NA NA NA Yes For the purposes of this risk

assessment a NOAEC value

based on acute:chronic ratio will be used (NOAEC =

0.06 μg a.i./L ).

850.1735 Whole

sediment

acute
freshwater

invertebrates Amphipod Experimental

sediment value

NOAE< 1.8 μg a.i./ kg sediment Derived pore

water value NA NA No *Derived value- Page 99 of 126

- NOAEC <

0.00182 μg a.i./ L pore

water* (MRID

44074406 Acceptable)

850.1740 Whole

sediment

acute marine

invertebrates NA NA NA Yes

Unpublished

guideline Whole

sediment:

chronic

freshwater

and marine

invertebrates NA NA NA No The chronic NOAEC value for the mysid shrimp will be used as a surrogate for

the chronic benthic

invertebrate NOAEC for

pore water (NOAEC =

0.000781 μg a.i./L pore water) because of similarities in life stages exposed during chronic toxicity tests for both species. In addition the LC50 value for the mysid shrimp and Hyalella azteca

in 96

- hour acute studies are very similar (LC50 = 0.00475 μg a.i./L for mysid

and LC50 = 0.0036 μg a.i./L , indicating that these species experience similar toxicity to cypermethrin.



### TABLE A

. 5 . Available ecological effects data for plants exposed to cypermethrins.

Guideline Description Racemic Cypermethrin Endpoint Alpha

Cypermethrin Endpoint Zeta

Cypermethrin Endpoint Data Gap? comments

850.4100 Terrestrial

Plant toxicity:

Tier I seedling

emergence NA NA NA No

850.4225 Terrestrial

Plant toxicity:

Tier II seedling

emergence NA NA NA No- Page 100 of 126

- 850.4150 Terrestrial

Plant toxicity:

Tier I vegetative

vigor NA NA NA No

850.4250 Terrestrial

Plant toxicity:

Tier II vegetative

vigor NA Monocot: EC50 >

0.0266 lbs a.i./A

NOEC < 0.00333

lbs a.i./A Dicot:

EC50 > 0.0266

lbs a.i/A NOEC =

0.0133 lbs a.i./A (MRID)

47944210 Supplemental Qualitative) NA No Available study is supplemental for use in characterization only.

850.5400 Aquatic

Plant

Growth:

algae NA Skeletonema

costatum EC50 >

33.5 μg a.i./L

NOAEC = 33.5 μg a.i/L (MRID 47944032 Acceptable) NA No *EFED typically requires aquatic plant toxicity studies for at least 4 types of algae.

850.4400 Aquatic

Plant

Growth:

vascular

plants NA EC50 > 1.39 μg

a.i./L NOAEC =

1.39 μg a.i./L (MRID 47944031

Supplemental Quantitative) NA No- Page 101 of 126

- 

### Appendix B. Sumary of Environmental Fate Data for Alpha

- cypermethrin

835.2130 Aqueous Photolysis (MRID 48425003)

Citation: Concha, M., V. Zhixing., and B. Claude. 2001. BAS 310 I (Alphacypermethrin): Aqueous Photolysis. Unpublished study performed by
PTRL West, Inc., Hercules, CA; sponsored and submitted by BASF Corporation, Research Triangle Park. NC. BASF Registration Document Number : AL

- 324

- 003. Study initiated August 4, 2000 and completed October 24, 2001.

The aqueous phototransformation of [ l4 

### C]alpha

- cypermet hrin (BAS 310 I); Two radiolabeled test substances, (benzyI and cyclopropane labels) were studied at 21.8 ± 0.5°C in sterile aqueous buffered pH 5 (alpha

- cypermethrin is hydrolytically stable at this pH) solutions (0.01M acetate) that were continuously irr adiated using a Xenon arc lamp for 15 days and 28 days, respectively. Recoveries were acceptable and ranged from 90

– 113% of the applied radiation. Two major degradates were observed, CL 206969 (3

- phenoxybenzaldehyde, max of 12.9% 4 DAT) and CL206128 (3

- phenoxybenzoic acid, 22.5% 4 DAT). The reviewer

- calculated phototransformation half

- life of BAS310 I (avg; both labels) was 1.7 days which is equivalent to 4.84 days for a latitude of 40°N during the spring season. This study is classified as acceptable.

835.2120 Hydrolysis (MRID 48425001)

Citation:

The hydrolysis of FASTAC  (WL85871; alpha

- cypermethrin) at pH's 5, 7 and 9 have been measured in buffer solutions containing 1M acetone. Single first

- order half

– lives ranged from 2.9 h at pH 9 to 162 days at pH 5 (22°C). Major degradated included cyclopropane carboxylic acid (WL42640) and meta

- phenoxybenzaldehyde. This study is clas sified as unacceptable for the following scientific reasons: No indication that the study was conducted in the dark; it was not specified that the buffer solutions were sterile; therefore, it could not be determined if degradation was due to hydrolysis of biotic process; the test material was not characterized; degradation curves and regression analysis were not provided; Limits of Detection (LOD) and Limits of Quantification (LOQ) were not reported; the study author indicated (p. 9) that there is a

An Arrh enius plot for each pH. No such plots were found in study.

MRID 48425002

Citation:

The abiotic hydrolysis of 14 

### C

- alpha

- cypermethrin at 0.0011 pg/ml was investigated in sterile aqueous buffered solutions at pH 4 , 7, and 9 at 25 and 50 ° C. For the 50 ° C s tudy, first

- order half

lives were calculated. Alpha

- cypermethrin was stable at pH 4, not determined at pH 7, and degraded with a half

- life of 3.0 days in pH 9 buffered solution. In the 25 ° C study, first

- order degradation half

- lives were calculated for pH 7, and 9 buffered solutions as 67 and 3.5 days, respectively (half

- lives were not determined for pH 4). In the aqueous solution at pH 4, only the parent compound was found until 10 days of incubation at 50 °C, indicating that alpha

-- Page 102 of 126

- 

### cypermethrin was stable to hydrolysis at acidic pH. This study is classified as acceptable.

835.1230 Batch Equilibrium, Adsorption/desorption

Citation: A.D. Hill . 1993. [Benzyl

- C] WL85875 (Fastac): Adsorption/Desorption In Three

Soils . Unpublished study performed and sponso red by BASF Corporation, Agricultural Products, Research Triangle Park ; BASF Number AL

- 620

- 011 . Experimental start date 18th

March 1993 , and experimental completion date 21st May 1993 . Study completion date October 12, 1993.

The adsorption and desorpti on characteristics of FASTAC  (14

- C alpha

- cypermethrin) in three

soils were studied in a batch equilibrium experiment (in a sand [pH 6.7, organic carbon 0.6%], a sandy loam soil [pH 7. 1, organic carbon 1.8%], and a silty clay soil [pH 6.8, organic carbon 3.1%]. The experiment was conducted in accordance with USEPA Subdivision N, Chemistry: Environmental Fate, Section 163

- 1: Leaching and Adsorption/Desorption Studies. Mean adsoption K d 

### ’s were 868, 1042, and 821, corresponding mean K

oc 

### ’s were 144,662, 57,88 9, and 26,492 for the sand, sandy loam and silty clay, respectively. This study is classified as supplemental and upgradeable upon the submission of additional information related to classification of soils used in this study, in accordance to FAO Soil Cla ssification (i.e. Soil Units) or equivalent U.S. Soil Taxonomy.

835.4300 Aerobic Aquatic Metabolism

CITATION: Mamouni, A. 1993. Fastac (Benzyl

14 

### C): Degradation and Metabolism in Aquatic Systems . Unpublished study performed by RCC Umweltchemie AG, Switzerland , and sponsored by BASF Corporation, Agricultural Products . North Carolina, USA. Report Series:

AL

- 630

- 011 . Experiment start date February 11, 1992 ; completion date February 22, 1993

. Final report issued October 18, 1993

.

The biotransfor mation of FASTAC  (Benzyl

14 

### C, labeled) i.e. l:l mixture of (S)

- alpha

- cyano

- 3

- phenoxybenzyl

- (lR,3R)

- 3

- (2,2

- dichloroviny1)

- 2,2

- d1methylcydopropanecarboxylate and (R)

- alpha

- cyano

- 3

- phenoxybenzyl

- (lS,3S)

- 3

- (2,2

- dich1orovinyl)

- 2,2

- dimethy1cyclopropanecarboxy late ( radiochemical purity ≥99.8%) was evaluated in two water/sediment systems.

System I : Rhine

- river water + Rhine loamy sand sediment ( water: pH 8.2, total carbon 9.3; sediment: pH 7.8, total organic carbon 0.9); and

System II : Pond water + Pond s andy clay sediment ( water: pH 7.2, total carbon 9.3; sediment: pH 7.1, total organic carbon 5.4).

Alpha

- cypermethrin degraded at different rates in two aquatic systems with first

- order half

- lives of 45 and 18.2 days in the Rhine river, and in the pond aq uatic system, respectively. The amount

of the non

- extractable radioactivity was greater in the pond system than in the Rhine system. After 30 days of incubation time, the non

- extractable component amounted to 37.3 and 20.5% of total applied radioactivity f or the pond and Rhine

- river sediment, respectively. Overall- Page 103 of 126

- 

### recoveries were acceptable. This study is classified supplemental . The drainage area contributing to the soucres of water used in the study were not appropriately characterized; the sediments

used in the study were not classified according to the FAO or WRB classification scheme.; and the experiments were conducted in systems with neutral to alkaline conditions that may favor more rapid hydrolysis therefore the results are of uncertain significance

.

Terrestrial Field Dissipation Studies

MRIDs 48425014, 48425015, 48425016 (UK)

Alpha

- cypermethrin residues in the field were studied in soils plots in the UK over a three year period from 1981

- 1983; applications of alpha

- cypermethrin were made a singl e time each year. Over the three years of the trial there was no indication of a build

- up of FASTAC residues in the surface soil layers, or any evidence to suggest that the compound is leached into sub

- surface soil layers. This study was not conducted in accordance with EPA

- Terrestrial Field Dissipation guideline 835

- 6100. The submitter of this study was neither the sponsor of this study nor conducted it, and does not know whether it has been conducted in accordance with 40 CFR Part 160. These are signifi cant limitations of the study, thus is classified as unacceptable.

MRIDs 48425017, 48425018, 48425019 (Hoath)

Residues in the field were studied in soils plots in the UK over a three year period from 1981

- 1983 to study the decay of FASTAC  (alpha

- cyperm ethrin) in a clay loam soil. A second application of pesticide was made to the same trial plots in 1982 and a. third application in 1983. In all cases the compound was applied to bare soil, as a diluted EC formulation, at a rate of 0.5 kg ai/ha. Samples of soil were then taken at various intervals up to 52 weeks after application and analyzed for residues of FASTAC. Over the three years of the trial there was no indication of

a build

- up of FASTAC residues in the surface soil layers, or any evidence to sugge st that the compound is leached into sub

- surface soil layers. This study was not conducted in accordance

with EPA

- Terrestrial Field Dissipation guideline 835

- 6100. The submitter of this study was neither the sponsor of this study nor conducted it, and doe s not know whether it has been conducted in accordance with 40 CFR Part 160. These are significant limitations of the study, thus is classified as unacceptable.

MRIDs 48425020, 48425021, 48425022 (Coates)

Residues in the field were studied in soils plot s in the UK over a three year period from 1981

- 1983 to study the decay of FASTAC  (alpha

- cypermethrin) in silty clay soil. Alpha

cypermethrin was applied annually at the same trial plots for three years, as a diluted EC formulation, at a dosage rate of U.5 kg ai/ha. Over the three years of the trial there was no

indication of a build

- up of FASTAC residues in the surface soil layers, or any evidence to suggest that significant leaching of the compound into sub

- surface soil layers was occurring. This study wa s not conducted in accordance with EPA

- Terrestrial Field Dissipation guideline

835

- 6100. The submitter of this study was neither the sponsor of this study nor conducted it, and

does not know whether it has been conducted in accordance with 40 CFR Part 160 . These are significant limitations of the study, thus is classified as unacceptable.- Page 104 of 126

- 

### Appendix C . Aquatic Model Input/Output Data.

Example Input/Output Data for Individual Simulations

PRZM/EXAMS Example Input/Output File.

stored as alphacyp_citrus.out Chemical: alpha

- cypermethrin

PRZM environment: FLcitrusSTD.txt modified Tueday, 29 May 2007 at 13:45:56 EXAMS environment: pond298.exv modified Tueday, 26 August 2008 at 06:14:08

Metfile: w12844.dvf modified Tueday, 26 August 2008 a t 06:14:22 Water segment concentrations (ppb)

Year Peak 96 hr 21 Day 60 Day 90 Day Yearly

1961 0.04266 0.01229 0.007847 0.005455 0.004836 0.001544

1962 0.07194 0.02487 0.0108 0.007519 0.007241 0.00232

1963 0.1423 0.04125 0.01212 0.00788 0.006535 0.002472

1964 0.1516 0.04229 0.01521 0.01086 0.008799 0.003551

1965 0.108 0.04521 0.0156 0.008026 0.006894 0.003201

1966 0.1102 0.04441 0.01426 0.01072 0.01026 0.003436

1967 0.07331 0.02622 0.01012 0.007551 0.006701 0.002663

1968 0.1677 0.04651 0.01368 0.01085 0.00 9087 0.003614

1969 0.07825 0.02448 0.0113 0.00851 0.007652 0.003152

1970 0.04281 0.01267 0.006276 0.00532 0.005084 0.001943

1971 0.04341 0.01714 0.008061 0.005764 0.005746 0.002109

1972 0.1413 0.0407 0.01765 0.01004 0.008651 0.002885

1973 0.05575 0.01609 0.009127 0.00763 0.006709 0.00231

1974 0.1088 0.03047 0.01109 0.007645 0.00669 0.002517

1975 0.1031 0.02988 0.0137 0.007285 0.006687 0.002354

1976 0.07483 0.02532 0.01244 0.008962 0.007301 0.002519

1977 0.1652 0.05703 0.02101 0.01036 0.00822 0.002838

1978 0.05004 0.01834 0.009283 0.007076 0.006267 0.002497

1979 0.1235 0.05793 0.02307 0.01131 0.00889 0.003203

1980 0.1381 0.03805 0.01275 0.007833 0.006515 0.002176

1981 0.1256 0.04125 0.01619 0.01067 0.00847 0.002888

1982 0.07641 0.0266 0.01126 0.007332 0.0068 34 0.00284

1983 0.07625 0.02516 0.009221 0.00695 0.006354 0.002616

1984 0.06929 0.02281 0.008414 0.007028 0.006439 0.002684

1985 0.04621 0.01758 0.01165 0.00822 0.007199 0.002352

1986 0.07898 0.02206 0.009262 0.007053 0.006489 0.002348

1987 0.07018 0.0206 0.01032 0.006785 0.005832 0.002631

1988 0.1902 0.05364 0.02023 0.01222 0.01006 0.003155

1989 0.04615 0.01614 0.006879 0.005485 0.00505 0.00161

1990 0.09643 0.02848 0.0126 0.009444 0.008954 0.002884

Sorted results

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

0.032258064516129 0.1902 0.05793 0.02307 0.01222 0.01026 0.003614

0.0645161290322581 0.1677 0.05703 0.02101 0.01131 0.01006 0.003551

0.0967741935483871 0.1652 0.05364 0.02023 0.01086 0.0090870.003436

0.129032258064516 0.1516 0.04651 0.01 765 0.01085 0.0089540.003203

0.161290322580645 0.1423 0.04521 0.01619 0.01072 0.00889 0.003201

0.193548387096774 0.1413 0.04441 0.0156 0.01067 0.0087990.003155

0.225806451612903 0.1381 0.04229 0.01521 0.01036 0.0086510.003152- Page 105 of 126

- 0.258064516129032 0.1256 0.04125 0.01426 0.01004 0.00847 0.002888

0.290322580645161 0.1235 0.04125 0.0137 0.0094440.00822 0.002885

0.32258064516129 0.1102 0.0407 0.01368 0.0089620.0076520.002884

0.354838709677419 0.1088 0.03805 0.01275 0.00851 0.0073010.00284

0.387096774193548 0.1 08 0.03047 0.0126 0.00822 0.0072410.002838

0.419354838709677 0.1031 0.02988 0.01244 0.0080260.0071990.002684

0.451612903225806 0.09643 0.02848 0.01212 0.00788 0.0068940.002663

0.483870967741936 0.07898 0.0266 0.01165 0.0078330.0068340.002631

0.516129032258 065 0.07825 0.02622 0.0113 0.0076450.0067090.002616

0.548387096774194 0.07641 0.02532 0.01126 0.00763 0.0067010.002519

0.580645161290323 0.07625 0.02516 0.01109 0.0075510.00669 0.002517

0.612903225806452 0.07483 0.02487 0.0108 0.0075190.0066870.002497

0.64 5161290322581 0.07331 0.02448 0.01032 0.0073320.0065350.002472

0.67741935483871 0.07194 0.02281 0.01012 0.0072850.0065150.002354

0.709677419354839 0.07018 0.02206 0.0092830.0070760.0064890.002352

0.741935483870968 0.06929 0.0206 0.0092620.0070530.0064390.0 02348

0.774193548387097 0.05575 0.01834 0.0092210.0070280.0063540.00232

0.806451612903226 0.05004 0.01758 0.0091270.00695 0.0062670.00231

0.838709677419355 0.04621 0.01714 0.0084140.0067850.0058320.002176

0.870967741935484 0.04615 0.01614 0.0080610.0057640 .0057460.002109

0.903225806451613 0.04341 0.01609 0.0078470.0054850.0050840.001943

0.935483870967742 0.04281 0.01267 0.0068790.0054550.00505 0.00161

0.967741935483871 0.04266 0.01229 0.0062760.00532 0.0048360.001544

0.1 0.16384 0.052927 0.019972 0.010859 0.0090737 0.0034127 Average of yearly averages: 0.00264373333333333

Inputs generated by pe5.pl

- Novemeber 2006

Data used for this run: Output File: alphacyp_citrus

Metfile: w12844.dvf

PRZM scenario: FLcitrusSTD.txt

EXAMS environment file: pond298.exv

Chemical Name: alpha

- cypermethrin Description Variable Name Value Units Comments Molecular weight mwt 416.3 g/mol Henry's Law Const. henry 3.4e

- 7 atm

- m^3/mol Vapor Pressure vapr 2.5e

- 9 torr Solubility sol 0.004 mg/L

Kd Kd mg/L

Koc Koc 141700 m g/L Photolysis half

- life kdp 36.2 days Half

- life Aerobic Aquatic Metabolism kbacw 10.7 days Halfife Anaerobic Aquatic Metabolism kbacs 18.1 days Halfife

Aerobic Soil Metabolism asm 61 days Halfife Hydrolysis: pH 7 0 days Half

- life

Method: CAM 2 integer See PRZM manual Incorporation Depth: DEPI 0 cm Application Rate: TAPP 0.028 kg/ha Application Efficiency: APPEFF 0.95 fraction Spray Drift DRFT 0.039 fraction of application rate applied to pond Application Date Date 01

- 06 dd/mm or dd/mmm or dd

- mm or dd

- mmm
I nterval 1 interval 14 days Set to 0 or delete line for single app. app. rate 1 apprate 0.028 kg/ha

Interval 2 interval 14 days Set to 0 or delete line for single app.- Page 106 of 126

- app. rate 2 apprate 0.028 kg/ha

Interval 3 interval 14 days Set to 0 or delete line for single app. app. rate 3 apprate 0.028 kg/ha

Interval 4 interval 14 days Set to 0 or delete line for single app. app. rate 4 apprate 0.028 kg/ha

Interval 5 interval 14 days Set to 0 or delete line for single app. app. rate 5 apprate 0.028 kg/ha

Interval 6 interval 14 days Set to 0 or delete line for single app. app. rate 6 apprate 0.028 kg/ha

Interval 7 interval 14 days Set to 0 or delete line for single app. app. rate 7 apprate 0.028 kg/ha

Record 17: FILTRA

IPSCND 1

UPTKF

Record 18: PLVKRT

PLDKRT

FEXTRC 0.5 Flag for Index Res. Run IR EPA Pond Flag for runoff calc. RUNOFF none none, monthly or total(average of entire run)- Page 107 of 126

- 

### Appendix D . Model Outputs

SIP Model Outputs

Table 1. Inputs

Parameter Value

Chemical name Alpha

- cypermethrin
Solubility (in water at 25 o C; mg/L) 4.00E

- 03

Mammalian LD 50 (mg/kg

- bw) 86 Mammalian test species laboratory rat Body weight (g) of "other" mammalian species

Mammalian NOAEL (mg/kg

- bw) 100
Mammalian test species laboratory rat Body weight (g) of "other" mammalian species

Avian LD 50 (mg/kg

- bw) 2025 Avian test species northern bobwhite quail Body weight (g) of "other" avian species Mineau scaling factor 1.15

Mallard NOAEC (mg/kg

- diet) 50 Bobwhite quail NOAEC (mg/kg

- diet) 50 NOAEC (mg/kg

- diet) for other bird species 0 Body weight (g) of other avian species NOAEC (mg/kg

- diet) for 2nd other bird species 0 Body weight (g) of 2nd other avian species

Table 2. Mammalian Results

Parameter Acute Chronic Upper bound exposure (mg/kg

- bw) 0.0007 0.0007 Adjusted toxicity value (mg/kg

- bw) 66.1478 76.9161 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 mammals

Table 3. Avian Results

Parameter Acute Chronic- Page 108 of 126

- Upper bound exposure (mg/kg

- bw) 0.0032 0.0032 Adjusted toxicity value (mg/kg

- bw) 1458.8698 2.4806 Ratio of exposure to acute toxicity 0.0000 0.0013

Conclusion* Drinking water exposure alone 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 Model Outputs



# Welcome to the EFED Screening Tool for Inhalation Risk

This tool is designed to provide the risk assessor with a rapid method for determining the potential significance of the inhalation exposure route to birds and mammals in a risk assessment.



# Input

Application and Chemical Information

Enter Chemical Name Alpha

cypermethrin

Enter Chemical Use Is the Application a Spray? (enter y or n) y If Spray What Type (enter ground or air) air Enter Chemical Molecular Weight (g/mole) 416.3 Enter Chemical Vapor Pressure (mmHg) 2.50E

- 09 Enter Application Rate (lb a.i./acre) 0.025

Toxicity Properties

**Bird**

Enter Lowest Bird Oral LD 50 (mg/kg bw) 2025 Enter Mineau Scaling Factor 1.15 Enter Tested Bird Weight (kg) 0.178

**Mammal**

Enter Lowest Rat Oral LD 50 (mg/kg bw) 86

Enter Lowest Rat Inhalation LC 50 (mg/L) 2.5 Duration of Rat Inhalation Study (hrs) 4 Enter Rat Weight (kg) 0.35



# Output- Page 109 of 126

- 

### Results Avian (0.020 kg )
Maximum Vapor Concentration in Air at Saturation (mg/m 3 ) 5.60E

- 05

Maximum 1

- hour Vapor Inhalation Dose (mg/kg) 7.04E

- 06

Adjusted Inhalation LD 50 3.28E+02

Ratio of Vapor Dose to Adjusted Inhalation LD 50 2.15E

- 08 Exposure not Likely Significant

Maximum Post

- treatment Spray Inhalation Dose (mg/kg) 2.40E

- 03 Ratio of Droplet Inhalation Dose to Adjusted Inhalation

LD 50 7.32E

- 06 Exposure not Likely Significant



### Results Mammalian (0.015 kg )
Maximum Vapor Concentration in Air at Saturation (mg/m 3 ) 5.60E

- 05

Maximum 1

- hour Vapor Inhalation Dose (mg/kg) 8.85E

- 06

Adjusted Inhalation LD 50 1.49E+02

Ratio of Vapor Dose to Adjusted Inhalation LD 50 5.95E

- 08 Exposure not Likely Significant

Maximum Post

- treatment Spray Inhalation Dose (mg/kg) 3.02E

- 03 Ratio of Droplet Inhalation Dose to Adjusted Inhalation

LD 50 2.03E

- 05 Exposure not Likely Significant



### KABAM Model Outputs

*Predicted concentrations of alp ha

- cypermethrin in fish assume measured uptake (K1= 208) and elimination (K2 = 0.58) rate constants from the submitted bluegill sunfish BCF study (MRID 42868203).

Table 11. Estimated concentrations of Alpha

- cypermethrin in ecosystem c omponents.

Ecosystem Component Total
concentration

(μg/kg

- ww) Lipid
normalized

concentration

(μg/kg

- lipid) Contribution

due to diet (μg/kg

- ww) Contribution

due to respiration (μg/kg

- ww)
Water (total)* 0 N/A N/A N/A Water (freely dissolved)* 0 N/A N/A N/A Sediment (pore water)* 0 N/A N/A N/A Sediment (in solid)** 28 N/A N/A N/A
Phytoplankton 2,067 103357 N/A 2,067.14
Zooplankton 3,154 105132 828.34 2,325.61

Benthic Invertebrates 4,553 151770 2,520.62 2,032.49

Filter Feeders 2,983 149138 1,635.96 1,346.80

Small Fish 268 6711 258.24 10.22

Medium Fish 125 3120 114.55 10.24 Large Fish 15 373 4.21 10.70
* Units: μg/L; **Units: μg/kg

- dw- Page 110 of 126

- Table 12. Total BCFand BAF values of Alpha

- cypermethrin in aquatic trophic levels.

Trophic Level Total BCF (μg/kg

ww)/(μg/L) Total BAF (μg/kg

ww)/(μg/L)
Phytoplankton 120571 68905 Zooplankton 85907 105132

Benthic Invertebrates 89911 151770

Filter Feeders 59098 99425

Small Fish 344 8949

Medium Fish 344 4160 Large Fish 359 497

Table 13. Lipid

- normalized BCF, BAF, BMF and BSAF values of Alpha

- cypermethrin in aquatic trophic levels. 0 500 1000 1500 2000 2500 3000 3500 4000 4500 5000

Zooplankton Benthic
Invertebrates Filter Feeders Small Fish Medium Fish Large FishConcentration (μg/kg)

Trophic Level

Figure 1. Total pesticide concentration per trophic level Contribution due to respiration (μg/kg

- ww)

Contribution due to diet (μg/kg

- ww)- Page 111 of 126

- Trophic Level BCF (μg/kg

lipid)/(μg/L) BAF (μg/kg

lipid)/(μg/L) BMF (μg/kg

lipid)/(μg/kg

lipid) BSAF (μg/kg

lipid)/(μg/kg

OC)
Phytoplankton 6028572 3445235 N/A 146
Zooplankton 2863579 3504387 1.02 148

Benthic Invertebrates 2997019 5059010 2.21 214

Filter Feeders 2954909 4971271 2.17 210

Small Fish 8592 223716 0.05 9

Medium Fish 8592 103989 0.04 4 Large Fish 8966 12422 0.12 1

Table 14. Calculation of EECs for mammals and birds consuming fish contaminated by Alpha

cypermethrin.

Wildlife Species Biological Parameters EECs (pesticide intake) Body Weight

(kg) Dry Food Ingestion Rate (kg

- dry

food/kg

bw/day) Wet Food Ingestion Rate (kg

- wet

food/kg

bw/day) Drinking

Water

Intake (L/d) Dose Based (mg/kg

bw/d) Dietary

Based (ppm)

Mammalian

fog/water shrew 0.02 0.140 0.585 0.003 2.665 4.55

rice rat/star

- nosed

mole 0.1 0.107 0.484 0.011 1.268 2.62

small mink 0.5 0.079 0.293 0.048 0.037 0.12

large mink 1.8 0.062 0.229 0.168 0.029 0.12

small river otter 5.0 0.052 0.191 0.421 0.024 0.12

large river otter 15.0 0.042 0.157 1.133 0.002 0.01

Avian
sandpipers 0.0 0.228 1.034 0.004 2.6654 2.58

cranes 6.7 0.030 0.136 0.211 0.3437 2.53

rails 0.1 0.147 0.577 0.010 1.3919 2.41

herons 2.9 0.040 0.157 0.120 0.3682 2.34

small osprey 1.3 0.054 0.199 0.069 0.0249 0.12

white pelican 7.5 0.029 0.107 0.228 0.0016 0.01- Page 112 of 126

- Table 15. Calculation of toxicity values for mammals and birds consuming fish contaminated by Alpha

- cypermethrin.

Wildlife Species Toxicity Values

Acute Chronic

Dose

Based (mg/kg

bw) Dietary

Based (mg/kg

- diet) Dose Based (mg/kg

- bw) Dietary

Based (mg/kg

- diet)

Mammalian fog/water shrew 180.59 N/A 10.50 100

rice rat/star

- nosed

mole 122.51 N/A 7.12 100

small mink 80.76 N/A 4.70 100

large mink 57.11 N/A 3.32 100

small river otter 44.24 N/A 2.57 100

large river otter 33.61 N/A 1.95 100

Avian
sandpipers 1458.87 4690.00 N/A 50

cranes 3489.58 4690.00 N/A 50

rails 1760.46 4690.00 N/A 50

herons 3077.67 4690.00 N/A 50

small osprey 2712.68 4690.00 N/A 50

white pelican 3549.12 4690.00 N/A 50

Table 16. Calculation of RQ values for mammals and birds consuming fish contaminated by Alpha

- cypermethrin.

Wildlife Species Acute Chronic

Dose

Based Dietary

Based Dose Based Dietary

Based

Mammalian fog/water shrew 0.015 N/A 0.254 0.046

rice rat/star

- nosed

mole 0.010 N/A 0.178 0.026

small mink 0.000 N/A 0.008 0.001

large mink 0.001 N/A 0.009 0.001- Page 113 of 126

- small river otter 0.001 N/A 0.009 0.001

large river otter 0.000 N/A 0.001 0.000

Avian
sandpipers 0.002 0.001 N/A 0.052

cranes 0.000 0.001 N/A 0.051

rails 0.001 0.001 N/A 0.048

herons 0.000 0.000 N/A 0.047

small osprey 0.000 0.000 N/A 0.002

white pelican 0.000 0.000 N/A 0.000



### T

- REX Model Outputs

Summary of Risk Quotient Calculations Based on Upper Bound Kenaga EECs

Table X. Upper Bound Kenaga, Acute Avian Dose

- Based Risk Quotients

Size

Class (grams) Adjuste

d

LD50 EECs and RQs

Short Grass Tall Grass Broadleaf Plants/

Small Insects Fruits/Pods/

Seeds/ Large Insects Granivore

EEC RQ EEC RQ EEC RQ EEC RQ EE

C RQ

20 1440.86 17.96 0.01 8.23 0.01 10.10 0.01 1.12 0.00 0.25 0.0

0

100 1834.29 10.24 0.01 4.69 0.00 5.76 0.00 0.64 0.00 0.14 0.0

0

1000 2591.00 4.59 0.00 2.10 0.00 2.58 0.00 0.29 0.00 0.06 0.0

0

Table X. Upper Bound Kenaga, Subacute Avian Dietary Based Risk Quotients

LC50 EECs and RQs

Short Grass Tall Grass Broadleaf

Plants/

Small Insects Fruits/Pods/

Seeds/ Large Insects- Page 114 of 126

- EEC RQ EE

C RQ EE

C RQ EEC RQ

2634 15.77 0.01 7.23 0.00 8.87 0.00 0.99 0.00

Size class not used for dietary risk quotients

Table X. Upper Bound Kenaga, Chronic Avian Dietary Based Risk Quotients

NOAE

C (ppm) EECs and RQs

Short Grass Tall Grass Broadleaf

Plants/

Small Insects Fruits/Pods/

Seeds/ Large Insects

EEC RQ EE

C RQ EE

C RQ EEC RQ

50 15.77 0.32 7.23 0.14 8.87 0.18 0.99 0.02

Size class not used for dietary risk quotients

Table X. Upper Bound Kenaga, Acute Mammalian Dose

- Based Risk Quotients

Size

Class (grams) Adjuste

d

LD50 EECs and RQs

Short Grass Tall Grass Broadleaf Plants/

Small Insects Fruits/Pods/

Seeds/ Large Insects Granivore

EEC RQ EEC RQ EEC RQ EEC RQ EE

C RQ

15 189.01 15.04 0.08 6.89 0.04 8.46 0.04 0.94 0.00 0.21 0.0

0

35 152.93 10.39 0.07 4.76 0.03 5.85 0.04 0.65 0.00 0.14 0.0

0

1000 66.15 2.41 0.04 1.10 0.02 1.36 0.02 0.15 0.00 0.03 0.0

0

Table X. Upper Bound Kenaga, Acute Mammalian Dietary Based Risk Quotients

LC50 (ppm) EECs and RQs

Short Grass Tall Grass Broadleaf

Plants/

Small Insects Fruits/Pods/

Seeds/ Large Insects

EEC RQ EE

C RQ EE

C RQ EEC RQ

0 15.77 ####

# 7.23 ####

# 8.87 #DIV/0

! 0.99 ####

#

Size class not used for dietary risk quotients- Page 115 of 126

- Table X. Upper Bound Kenaga, Chronic Mammalian Dietary Based Risk Quotients

NOAE

C (ppm) EECs and RQs

Short Grass Tall Grass Broadleaf

Plants/

Small Insects Fruits/Pods/

Seeds/ Large Insects

EEC RQ EE

C RQ EE

C RQ EEC RQ

100 15.77 0.16 7.23 0.07 8.87 0.09 0.99 0.01
Size class not used for dietary risk quotients

Table X. Upper Bound Kenaga, Chronic Mammalian Dose

- Based Risk Quotients

Size

Class (grams) Adjuste

d

NOAEL EECs and RQs

Short Grass Tall Grass Broadleaf Plants/

Small Insects Fruits/Pods/

Seeds/ Large Insects Granivore

EEC RQ EEC RQ EEC RQ EEC RQ EE

C RQ

15 10.99 15.04 1.37 6.89 0.63 8.46 0.77 0.94 0.09 0.21 0.0

2

35 8.89 10.39 1.17 4.76 0.54 5.85 0.66 0.65 0.07 0.14 0.0

2

1000 3.85 2.41 0.63 1.10 0.29 1.36 0.35 0.15 0.04 0.03 0.0

1- Page 116 of 126

- 

### Appendix E. Reported Ecological Incidents for Racemic and Zeta

- Cypermethrin in EIIS.

Table E

- 1. Cypermethrin and Zeta

- Cypermethrin Incident Report Summaries

Incident # Organism(s)

Affected Certainty of

Involvement Legality of

Use Description

I008737

- 001 Lobster (Decapoda) Probable Registered

Use In a 5000 gal. saltwater tank in Cocoa Beach, FL 32931, an

owner, Rancher/Breeder/Farmer found

800 lobsters dead and another

25 lobsters still alive in the tank. He used a product (EPA Reg. No. 4822

- 452): RAID

Concentrate

- Deep Reach Fogger in a room adjacent to

the tank room t hen closed the tank room door for the night, but did not place a towel under

the door. An air conditioner

was turned off. He does not

have UV/ozone sterilization.

He has added another 200

- 300

lobsters to this same tank and they seem fine. He has tested water, ammonia nitrites, nitrate, pH and all are within

normal limits. He could not locate the EPA Reg. No. on the

container.

I009966

- 002 Bass ( Micropterus

spp. ) Bluegill ( Lepmis

macrochirus ) Carp ( Cyprinus carpio ) Catfish (Ictaluridae) Crappie (Centrarchidae)

Minnow (Cyprinidae) Shad (Clupeidae) Probable Misuse A fish kill was reported on February 9, 1998 in Chattanooga, the result of a termiticide containing cypermethrin entering Rogers

Branch and its un

- named

tributaries. The Tennessee

Wildli fe Resources

Association assessed the cost of the dead fish at $609.33. Civil penalties and damages were assessed, suggesting misuse of the pesticide.

Further information was provided by a 6(a)(2) report from Zenaca Ag Products- Page 117 of 126

- 

### Table E

- 1. Cypermethrin and Zeta

- Cypermethrin Incident Report Summaries

Incident # Organism(s)

Affected Certainty of

Involvement Legality of

Use Description

(I006971

- 001). They claim that their investigation indicate that the kill was not likely the result of any labeled use of

Demon TC or of the minor spill reported on the property

in November

- December 1997. They claim the exposure characteristics suggest "introduction of

relativel y massive amounts of chemical directly into the

water course.
I011346

- 001 Crayfish (Decapoda) Highly probable Misuse According to a report from the Environment Agency

- UK, thousands of crayfish had been

killed in the Sherston Avon at Pinkney, upstream of Malmesbury, Wiltshire.

Within 24 hours of the first report, the Environment Agency's Exeter laboratory pinpointed cypermethrin as the cause. An investigation led to the Badminton sewage treatment works and, ultimately, to a kennel where a sheep dip called Crovert (containing cypermethrin) had

been used to treat hounds for mange. After treatment, the

Crovert was washed off and entered the river through the effluent of the sewage treatment plant.

I001031

- 001 Bluegill ( Lepmi s macrochirus ) Carp ( Cyprinus carpio ) Catfish (Ictaluridae)

Largemouth bass

( Micropterus

salmoides ) Highly probable Undetermined This fish kill resulted from the application of Demon TC as a

termite barrier around a home in Henderson, Kentucky. Undergroun d drainage tile had

been installed around the home to divert water to a pond 50 feet away, and the night- Page 118 of 126

- 

### Table E

- 1. Cypermethrin and Zeta

- Cypermethrin Incident Report Summaries

Incident # Organism(s)

Affected Certainty of

Involvement Legality of

Use Description

following the application of Demon there was a heavy

rainfall which resulted in dumping some of the Demon into the pond. Approximately

44 fish we re k illed.

I018158

- 017 Koi ( Cyprinus carpio ) Probable Undetermined Koi allegedly died from a drift exposure caused by an Eagle

Pest Control technician performing a routine quarterly perimeter treatment using the

labeled rate of Probuild TC (a.i. cypermethrin). Koi fish pond was located at the backyard of the treatment

location.

I017029

- 001 Unknown fish Highly probable Misuse (Accidental) This is an update of a previous

incident that occurred in Takoma Park, MD, in which a cypermethrin

- based pesticide called "Prevail" spilled from one of the company's pesticide application trucks onto a driveway while an employee was attempting to repair or replace a pump. The employee

used a hose to wash off the driveway, causing the pesticide

to drain into a creek and, subsequently, into Chesapeake Bay. A large number of fish

were killed as the result of this incident.The pest control company was fined $7,300 and its license was suspended for 4 years as a part of the consent agreement with the Maryland Department of Agriculture.

I006971

- 001 Unknown fish Highly probable Undetermined Zeneca reported that Tennessee Dept. of Agriculture

was contacted about fish kill in several small ponds fed by a

small stream. State- Page 119 of 126

- 

### Table E

- 1. Cypermethrin and Zeta

- Cypermethrin Incident Report Summaries

Incident # Organism(s)

Affected Certainty of

Involvement Legality of

Use Description

investigators estimated 2,200

dead fish (i.e., bass, bluegill, shad) were impacted along with various other unspecified aquatic organisms. Soil and water samples were obtained. Analysis showed trace levels of chlorpyrifos and permethrin, and exceptionally high levels of cypermethrin.

Initial investigation focused on a local pest control applicator.

A multi

- agency investigation

team later focused its attention to alternative explanations.

I007107

- 003 Minnow (Cyprinidae) Highly probable Undetermined This incident is one of the

incidents stated on a consolidated report submitted by the Pesticide Investigation Unit, California Dept. of Fish and Game for the year 1997.

One thousand Gambusia (minnows) reported dead in Placer County on 2

- 7

- 1997.

The PIU confirmed that Cypermethrin was the cause of

this fish kill.

I010444

- 004 N/R Probable Misuse (Accidental) To comply with 6(a)2 regulations, FMC reported an

incident that occurred in Silver Spring, MD (the location was not given in the report but was known to this writer). A treatment tank was being cleaned out by an applicator and the washings entered Rock Creek, causing a fish kill extending from an area near Walter Reed Hospital to the

Potomac River. Initial

estimates that there were between 1000 and 150,000 dead fish but later, the estimate- Page 120 of 126

- 

### Table E

- 1. Cypermethrin and Zeta

- Cypermethrin Incident Report Summaries

Incident # Organism(s)

Affected Certainty of

Involvement Legality of

Use Description

was revised to 10,000. The Maryland Dept. of Agricuoture found 50 ppb cypermethrin in

the water.

I013857

- 011 Unknown fish Probable Misuse (Intentional) To comply with 6(a)2 requirements, Syngenta reported that the February 25, 2003, issue of the Independent (London) carried an account of a large fish kill in the river Slea, in Lincolnshire. According to this newspaper, someone had dumped Cypermethrin into surface

water drai ns at an industrial site, infecting 13 miles of the river and causing the death of 100,000 fish.

I004876

- 011 Crayfish (Decapoda) Stonefly (Plecoptera) Highly probable Misuse (Accidental) This information was sent in response to a letter from Gerard Desir, EPA. It

concerns a fish kill in the

Salmon River as the result of cypermethrin poisoning.

I000011

- 001 N/R Possible Registered

Use Pond fishkill via alleged underground stream under home, after termite control.

I015094

- 001 Unknown fish Possible Registered

Use FMC 6(a)(2) incident report stated that a contractor applied Prevail (cypermethrin) on a

horizontal soil surface where a concert slab was to be poured.

Dead fish were found in a

stream 1/2 to 1 mile from the construction site. No analyses

we re given.

I017984

- 001 Crayfish (Decapoda) Possible Misuse (Accidental) A web site from the UK reports that the joint mater of the Duke of Beaufort appeared at Avon magistrates on 10/20/1998. He pleaded guilty to allowing hounds treated with cypermethrin, which is- Page 121 of 126

- 

### Table E

- 1. Cypermethrin and Zeta

- Cypermethrin Incident Report Summaries

Incident # Organism(s)

Affected Certainty of

Involvement Legality of

Use Description

used to treat mange, to enter the River Avon. The pesticide killed around 10,000 endangered white clawed crayfish in the river.

I011348

- 001 Sparrow (Fringillidae) Unlikely Undetermined A report on the Internet (Third World Network) described a massive killing of sparrows in a small village in Bangladesh

as the result of a massive use of cypermethrin. In eggplant and pointed gourd fields there was a spraying of Ustad the night before. T he sparrows ate

insects that had died from the spraying and they, in turn, died by the thousands. An original

estimate was that 5000 had

died but later indications were

that the number was much higher. Residents were shocked by the massive kill of

these birds and protests were made against the use of pesticides.

I021456

- 001 Bluegill ( Lepomis

macrochirus ) Largemouth bass

( Micropterus

salmoides ) Possible Undetermined Iowa Departmewnt of Natural Resources reported an incident

on dozens of fish kill in a pri vate pond surrounded by soybean field on three sides and live pasture field to the

south in Iowa. There was aerial spraying of pesticides onto the soybean field.

I000340

- 009 Goat (Bovidae) Possible Undetermined The report implied that an unspecified numbe r of goats may have suffered illness due to nearby application of cypermethrin.

I000103

- 010 Barred owl ( Strix

varia ) Mockingbird ( Mimus polyglottos ) Unlikely Undetermined According to the investigative report 11 dead birds were found near a private dwelling (9 sparrows, a mockingbird,- Page 122 of 126

- 

### Table E

- 1. Cypermethrin and Zeta

- Cypermethrin Incident Report Summaries

Incident # Organism(s)

Affected Certainty of

Involvement Legality of

Use Description

White

- throated

sparrow ( Zonotrichea

albicollis ) and a barred owl). It was suspected that the mortality

was due to toxicosis. Four

birds were selected for necropsy (1 mockingbird and 3

spa rrows). The premises had been periodically sprayed for termites for 8 years, the most recent being 2 month prior to the event with cypermethrin.

Earlier treatments had been done with lindane. Analysis of brain ChE activity gave normal

results. Residue a nalysis of gizzard/crop contents revealed the presence of Heptachlor Epoxide and a significant

amount of Dieldrin. there was

an insufficient amount of brain

tissue left to make a residue analysis of the brain for Dieldrin. According to the report brain tissue residue of 1ppm is considered significant but body residues are usually many times greater than brain

residue. The birds were observed to undergo convulsions just before dying. Crop/gizzard content residue analysis revealed Dieldrin at 7480 ppb an d Hrptachlor Epoxide at 710 ppb. There

was no evidence of organophosphate, carbamate, lindane, or cypermethrin pesticides.

I000340

- 006 Dog ( Canis familiaris ) Possible Undetermined According to the investigative report, a dog was dipped and also exposed t o pyrethroid products. The dog's illness was suspected to be due to one of these exposures.- Page 123 of 126

- 

### Table E

- 1. Cypermethrin and Zeta

- Cypermethrin Incident Report Summaries

Incident # Organism(s)

Affected Certainty of

Involvement Legality of

Use Description

I000340

- 002 Cat ( Felix

domesticus ) Probable Registered

Use According to the report A cat was exposed to toxic fumes of cypermethrin by following applicator around as he

worked.

I014202

- 007 Honey Bee ( Apis millifera ) Possible Registered

Use On Aug 9, 2002, a bee keeper reported that queenless hives was observed on Aug 8, 2002. Yard was inspected where there use to be 32 hives, but

has declined to 26 hives. All 26 hives were open and inspected. 8 of the hives were queenless or failing. No diseases were found, but Varroa mite was positive for one hive. An erratic or spotty brood pattern was common. Pesticide exposure was suspected. One hybrid poplar

field was identified 3.5 miles from the yard, and this field

had not been treated in 2002.

An alfalfa field 2.75 miles from the yard was identified and it was sprayed with zeta

cypermethrin 23 days prior to the observation in the bee yard. Samples of pollen w ere taken and analyzed with no detection

of zeta

- cypermethrin, carbaryl,

1

- naphthol and carbofuran. The insecticide coumaphos

was detected. It is used in Check Mite Strips used to

control Varroa mites.

Note: The insecticide used on

the alfalfa field was identified by the name Mustang and the EPA Reg. # 279

- 3126 was also given. Mustang is a pyrethin pesticide cancelled in 1983. The Reg. # identified the- Page 124 of 126

- 

### Table E

- 1. Cypermethrin and Zeta

- Cypermethrin Incident Report Summaries

Incident # Organism(s)

Affected Certainty of

Involvement Legality of

Use Description

product Fury and its active ingredient is zeta

cypermethrin.

I014202

- 008 Honey Bee ( Apis millifera ) Unlikely Registered

Use A bee keeper reported on Sept 4, 2002 that there were dead bees in his bee yard. It was also stated that on Aug. 27, 2002, the bee keeper removed honey and that the hives were fine. The inspector opened

and examined 20 of the twen ty hives. Colonies appeared to be disease free, except for two

hives with normal chalkbrood. Two hybrid poplar fields, 3,25 and 8 miles from the bee yard,

were identified. There were no

insecticide treatments to these

fields in 2002. An alfalfa field

h ad been treated with zeta

cypermethrin about 50 days before symptoms were reported. Bee tissue and pollen samples were obtained. Analyses of the samples did not detect any carbaryl, 1

- naphthol or carborfuran. Coumaphos was detected in

both the bee tissu e and pollen samples. Level were not given. Test for Varroa mites was negative.- Page 125 of 126

- 

### A ppendix F . Federally Listed Species Potentially at Risk from the Proposed Uses of Alpha Cypermethrin
Taxon Count by State for Selected Crops

No species exclusions.

Minimum of 1 Acre All Medium Types Included

alfalfa hay, broccoli, brussels sprouts, cabbage

- chinese, cabbage

- head, cabbage

- mustard, cauliflower, collards, kale, mustard greens, spinach, turnip greens,

citrus fruit

- all, corn

- popcorn & sweet cor n, corn

- sweet for seed, cotton

- all, squash

- summer, squash

- winter, muskmelons and pepinos, celery, escarole and
endive, lettuce

- head, lettuce

- leaf, parsley, rhubarb, beans

- dry edible excluding limas, beans

- dry lima, beans

- green lima, beans

- snap (green), bea ns

- yard

- long,

peas

- green (excluding southern), peas

- green southern (cowpeas)

- blackeyed, crowder, etc., peas

- pigeon, rice

- wild, artichokes

- excluding jerusalem, carrots, chicory, dasheens, ginger root, ginseng, potatoes, radishes, sweet potatoes, turnips, yam (lesser), yams, sorghum for grain, soybeans, sugarbeets for seed, sugarbeets for sugar, wheat

- all

AL, AZ, AR, CA, CO, CT, DE, DC, FL, GA, ID, IL, IN, IA, KS, KY, LA, ME, MD, MA, MI, MN, MS, MO, MT, NE, NV, NH, NJ, NM, NY, N C, ND, OH, OK, OR, PA, RI, SC , SD, TN, TX, UT, VT, VA, WA, WV, WI, WY, an, OA, an, OP

Amphibian, Arachnid, Bird, Bivalve, Conf/cycds, Coral, Crustacean, Dicot, Ferns, Fish, Gastropod, Insect, Lichen, Mammal, Mon ocot, Reptile

All Crops

Mammal Bird Amphibian Reptil Fish Crustacean Bival Gastropod Arachnid Insect Dico Monocot Ferns Conf/cycd Coral Liche

Alabama 5 4 2 4 15 1 38 12 2 13 4 3

Arizona 8 6 2 2 19 3 16 2

Arkansas 5 4 1 7 2 10 1 1 6 1 California 30 15 6 7 21 8 3 23 161 18 2

Colorado 3 5 6 2 15 1

Connecticut 1 2 1 1 1 2 1

Delaware 1 1 1 1 1

Florida 11 12 2 6 4 1 7 4 47 3 1 2 1
Georgia 5 6 2 2 8 17 2 15 6 2 1 1

Idaho 4 5 4 4 1

Illinois 2 2 2 1 8 1 2 7 2

Indiana 2 1 1 9 2 4 1

Iowa 1 2 3 4 1 3 2

Kansas 2 3 5 1 1 1 1 Kentucky 4 6 6 1 23 1 9

Thursday, May 31, 2012 Page 1 of 22- Page 126 of 126

- Louisiana 3 3 2 3 3 2 1

Maine 2 2 2 1 2 Maryland 2 1 1 1 1 2 5 2

Massachusetts 1 2 2 1 1 3 1 2 Michigan 3 2 1 4 4 4 3 1

Minnesota 1 1 1 4 1 2 2
Mississippi 5 4 1 5 4 10 2 1

Missouri 3 1 1 6 9 1 1 7 1

Montana 3 3 4 2 1

Nebraska 2 3 3 2 2 2

Nevada 1 2 1 22 2 9 1 New Hampshire 1 1 1 1 1 2
New Jersey 1 2 1 1 1 3 3

New Mexico 5 5 1 1 13 2 5 13

New York 1 2 1 1 3 1 1 5 2 1

North Carolina 7 4 2 5 8 1 1 1 21 5 1

North Dakota 2 3 2 1

Ohio 1 1 1 1 8 3 4 2

Oklahoma 3 6 1 4 3 1 2
Oregon 3 4 15 1 2 15 2 Pennsylvania 1 1 1 6 2

Rhode Island 1 2 1 1 1 1

South Carolina 1 6 1 1 1 1 13 6 1 1

South Dakota 1 4 3 2 1 1

Tennessee 3 3 20 1 41 3 1 15 2 1 1

Texas 6 12 4 9 1 1 10 9 26 3

Utah 3 3 1 8 1 24 2

Vermont 2 1 1 2
Virginia 6 3 1 1 8 2 23 1 1 2 13 4 Washington 8 4 6 1 9 1

West Virginia 2 1 1 6 1 4 2

Wisconsin 2 2 5 2 5 2
Wyoming 3 3 1 7 3 2

Thursday, May 31, 2012 Page 2 of 22