### 1 **OFFICE OF CHEMICAL SAFETY AND**  **POLLUTION PREVENTION UNITED ST**  **AT ES ENVIRONMENT** **AL PROTECTION A** **GENCY**

**WA SHINGTON D.C., 20460** 



### PC Code: 129112 Chemical: Trifloxys trobin DP Barcode: D 413110 August 18 , 2014 **MEMORANDUM SUBJECT:**  Ecological Ri sk A ssessment for N ew U se s of T rifloxystrobin on C hickpeas, D ry

P eas, and L entils **TO:** Tony

Kish, Product Manager Fungicide Branch Registration Division (7505P) **FROM:** Nic holas Mastrota, Wildlife Biologist

Melanie Biscoe , Physical Scientist Environmental Risk Branch 3 Environmental Fate and Effects Division (7507P ) **REVIEWED** Melissa Panger, Ph.D., Senior Biologist **BY:** Environmental Risk Branch

Environmental Fate and Effects Division (7507P) **T HROUGH**  **:** Dana Spatz, Branch Chief

Environmental Risk Branch 3 Environmental Fate and Effects Division (7507P) This memorandum summarizes the potential ecological risks associate d with the proposed new use s of the fungicide trifloxys trobin (PC code: 129112) on chickpeas, dry peas, and lentils . The proposed single application rate for use on chickpeas, dry peas, and lentils is 0.1 19 lb a.i./acre. Up to two applications may be made. The maximum annual rate is 0 . 24 lb a.i./A. The rate for the proposed use s is within the range of existing registere d uses on food crops and less than the existing rate for use on turf. The ecological risks associated with these new uses are no greater than those of existing uses.

### 2



## Risk	Summary EFED’s Tier I risk assessment indicates that potential ecological risks from trifloxystrobin parent and its isomers resulting from the proposed new uses do not exceed the EPA’s level of concern (LOC) for non - endangered species. However, all proposed uses exceed the endangered species level of concern for acute risk to saltwater invertebrates and terrestrial plants, and uses with aerial application exceed the endangered species LOC for acute risk to freshwater fish. These risks are similar to those identified in previous risk assessments for other uses of trifloxys trobin. 

## P **revious	Risk	Conclusions** Triflox ys trobin has been previously evaluated b y EFED for use on numerous commodities including pome fruits, grapes, cucurbits, peanuts, and turf (New Chemical Review, D244219, D245281, D254206, D254285, D254286); almonds, fruiting vegetables, hops, potatoes, sugar beets, and wheat (D254215, D254220, D254222); root vegetable subgroup 1B (except beet and radish) and leaf petiole subgroup 4B (D286427); barley , oats, sweet corn, and soy beans (D315580, D314187, D318621, D318623, D3 63130); grass grown for seed (D332979, D332982); asparagus, tropical crops, radish, root vegetables , strawberries (D331915, D339548, D348876) , and artichoke (D378918) . Detailed summaries of these assessments can be found in the following previous risk asse ssments: D309489, D331915 , D378918 . Based on previous reviews, EFED concluded that some uses are expected to present risk on an acute basis to freshwater and/or estuarine/marine aquatic organisms (fish and invertebrates); including Federally- listed endan gered and threatened species. Those uses include turf, cucurbits, grasses grown for seed, tropical crops, root vegetables, leaf petiole, almonds, fruiting vegetables, hops, and potatoes. Ecological risks are not expected for any of the other registered use s based on previous assessments. 

## Overview	of	Pesticide **Usage** The active ingredient in US F 0728 325 SC Fungicide is the E,E isomer of trifloxystrobin, which referred to generally

as trifloxystrobin for the purposes of this risk assessment. New use sites that are proposed for the registration of trifloxystrobin are chickpea, dry pea, and lentil. For all of these proposed new uses, the maximum single - application rate is 0.1 2 lb a.i./A 1 

### , and no more than 0.24 lb a.i./A of triflox ys trobin may be applied per year. Up to two applications may be made per ye ar, with a 10 - to 14 day interval between applications. The product is sprayed onto the foliage of plants. Spray applications may

be made with ground or aerial spray equipment, or through irrigati on systems (chemigation).

1 The label direction actually states the maximum single application rate as 12.0 fl oz/acre, which is equivalent to 0.119 lb a.i./acre. For simplicity, this rate has been rounded up to 0.12 lb a.i./A in this assessment.

### 3



## Environmental	Fate	and	Transport Trifloxys trobin isomers E,E (parent); E,Z; Z,E; and Z,Z, are expected to be in equilibrium in the environment. For the purposes of this assessment, all four isomers are considered in the exposure estimates using a Total Toxic Residues (TTR) approach . This approach was used to determine the environmental fate data parameters for modeling in conjunction with the Guidance for Selecting Input Parameters in Modeling the Environmental Fate and Transport of Pesticides , Version 2.1, October 22, 2009 and the draft Guidance for Modeling Pesticides Total Toxic Residues (TTR) May

20, 2009. Although trifloxys trobin’s major degradation product (CGA - 321113) comprises >50% of applied trifloxys trobin in some diss ipation studies, the available data suggest that CGA - 321113 is considerabl y less toxic to aquatic organisms on an acute and chronic basis than triflox ys trobin (see Appendix 1). Therefore, it is ' 

### anticipated that risk quotients based on chronic studies usin g trifloxys trobin and its isomers would be protective of aquatic organisms exposed to CGA 321113 on a chronic basis. Since the mode of action of trifloxys trobin (inhibition of cellular respiration) is the same in terrestrial and in aquatic organisms, CGA - 3 21113 is assumed to be also less toxic to terrestrial organisms than the parent . Therefore, the risk assessment will be based on exposure to the parent compound and the three aforementioned isomers and not CGA 321113. The c hemical names and structure s fo r the trifloxystrobin isomers considered in this assessment are summarized in Table 1 . **Table 1**  **. Chemical identification inform ation for trifloxystrobin**  **isomers**

**Chemical Structure**  CGA279202, Trifloxystrobin, (Parent) (EEisomer) (E,E) - Methoxyimino - {2 - [1 - (3 - trifluoro methyl -phenyl) - ethylideneaminooxymethyl] - phenyl} - acetic acid methyl ester Chemical Abstracts #: 141517 - 21 - 7 CGA357262 (ZZ - isomer) (Z,Z) - Methoxyimino - {2 - [1 - (3 - trifluoro methyl -phenyl) - ethylideneamino - oxymethyl] - phenyl} - acetic acid methyl ester

### 4

CGA357261 (ZE - isomer) (Z,E) - Methoxyimino - {2 - [1 - (3 - trifluoro methyl -phenyl) - ethylideneaminooxymethyl] - phenyl} - acetic acid methyl ester CGA331409 (EZ - isomer) (E,Z) - Methoxyimino - {2 - [1 - (3 - trifluoro methyl -phenyl) - ethylideneamino - oxymethyl] - phenyl} - acetic acid methyl ester 

### Parent: Trifloxystrobin E,E Isomer Available data suggest that trifloxys trobin is not persistent and has low mobility in the environment . The major routes of degradation and dissipation for triflox ys trobin are associated with alkaline - catalyzed hydrolysis, microbial - mediated metabolism, photodegradation, and soil binding. Hydrol ys is of tri floxys trobin is most important under alkaline conditions. D ispersion of trifloxys trobin will also occur in the environment by spray drift, in runoff water and eroded soil. The major degradate in hydrolys is, metabolism and photodegradation on soil is CGA - 32 1113, the free acid degradation product of trifloxys trobin ; h owever , as previousl y mentioned, CGA 321113 is not considered to be a degradate of concern in this risk assessment. Trifloxys trobin has a low solubility (0.61 mg/L @ pH 7) in water. The vapor pressure is 2.55 x 10 - 8 

### torr at 25 °C, and the calculated Henry’s Law Constant is 2.25 x 10 - 8 

### atm - m 3 

### mol - 1 

### . These values suggest that trifloxys trobin is non - volatile under field conditions from water and moist soil surfaces. Volatilization is not a likely route of dissipation. Trifloxys trobin is non -persistent in soil. Laboratory studies indicate that biotransformation is an important route of trifloxystrobin transformation in aerobic soil. Triflox ys trobin degraded rapidly in aerobic soils with half

- lives ranging between 0.41 and 0.91 days. The photo - induced isomerization half

- life (t 1/2 

### ) was 2.1 days on soils. Based upon the soil organic carbon coefficient, KF OC 

### (median KFOC 

### =2709 mL/g oc 

### ), trifloxystrobin would fall into the slightly mobile class 2 

### . There is no correlation between soil organic matter and K F 

### (r2 

### =0.04, p - value=0.72) and the coefficient of variation for the K F 

### ’ s is lower than that for the K FOC 

### ’s. This indicates that sorption is controlled by

factors other than soil organic carbon content. La boratory studies indicate that trifloxystrobin is also not persistent in water. The aerobic and anaerobic metabolism half - lives for trifloxys trobin are each less than one day. Hydrol ys is of 2 USEPA Office of Pesticide Programs, Environmental Fate and Effects Division. Standardized Soil Mobility Classification Guidance. April 21, 2006.

### 5

trifloxystrobin is dependent on pH; while trifloxystrobin is stabl e to hydrolysis under acidic conditions (pH 4), it readily hydrol yz es in alkaline conditions (t 1/2 

### = 55.2 days at pH 7 and 0.83 days at pH 9). In the aquatic environment, the photo - induced isomerization half - life (t 1/2 

### ) was 14.8 days. Triflox ys trobin demonstrated a biphasic degradation pattern in field dissipation studies conducted in California, New York, and Georgia. For the first degradation phase, trifloxys trobin half - life values ranged from 1.9 to 24 days. In the second degradation phase, half - life values ranged from 6.5 days to 4 months. The log Kow 

### of 4.5 suggests that trifloxystrobin may bioaccumulate. Trifloxystrobin has bioconcentration factors in bluegill sunfish edible tissues of 130 - 166X, 1172 - 114 4X for nonedible tissues, and 542 - 547X in whole fish. The bioaccumulation plateau was rapid (3 days post exposure). However, depuration was rapid, with 96.7 - 98.1% of the total [ 14 

### C]residues accumulated b y exposure day 28 eliminated from all tissues by 7 days in the 0.16 μg/L s ys tem, and 98.3 - 98.5% eliminated from all tissues by 14 days in the 1.6 μg/L s ys tem. Due to the relativel y low fish bioconcentration factors in fish tissue, rapid aquatic biotransformation to CGA - 321 1 13 (acid) and the rapid depurati on of trifloxystrobin observed in the fish study , bioaccumulation is unlikely . **Trifloxystrobin T**

**otal T**  **oxic R**  **esidues (TTR) : Parent and**  **Isomers of Concern in Aquatic Environments**  The triflox ys trobin isomers considered in the TTR approach are expected to h ave the same physical and chemical properties as the parent isomer. The proposed degradation pathways of triflox ys trobin in aquatic systems indicate that the E,Z; Z,E ; and Z, Z isomers are in equilibrium with the parent ( E,E ) isomer in aquatic environments (DP405629). The Z,E isomer is the major transformation product resulting from photo - induced isomerization of the parent in aqueous environments. The Z,E isomer formed up to 63.8% and 1% of the appli ed radioactivity

in the aqueous photol ys is and aerobic soil metabolism studies, respectivel y . The Z,E isomer was not detected in the other fate laboratory studies, and was not detected below 18 inches in the terrestrial field dissipation studies. The Z,E isomer is expected to be more mobile than the parent, with KFOC 

### ’s ranging from 389 to 567 mL/g oc 

### . Sorption is highl y dependent on soil organic carbon content, as the KF 

### ’ s are highly correlated with percent organic carbon (r2 

### =0.99, p - value=7e - 4 

### ) and the coefficient of variation for the KF OC 

### ’ s is lower than that for the KF 

### ’s. Because the Z,E isomer is more mobile than the parent isomer, the KFOC 

### for the Z,E isomer is used in modeling estimated exposure concentrations. The Z,Z isomer is a minor transformation product in the aqueous photolysis , soil photolysis , and aerobic soil metabolism studies , forming up to 9.1% , 4.1%, and 0.5% of applied radioactivity , respectivel y . The Z,Z isomer was not detected in the other fate laboratory studies. Inthe

### 6

terrestrial field dissipation studies, it was detected once in th e 12 - 18 inch segment s , and not detected below 18 inches. An adsorption/desorption study is not available for this isomer. The E,Z isomer is a minor transformation product in the aerobic soil metabolism, soil photolysis, and aerobic aquatic metabolism studies , forming up to 4.2%, 4.1%, and 0.4% of applied radioactivity , respectively . The E,Z isomer was not detected in the other fate laboratory studies or in the terrestrial field dissipation studies. An adsorption/desorption study is not available for this i somer. The aqueous photol ys is half - life for trifloxystrobin TTR is 54.7 days and the aerobic aquatic metabolism half

- life for trifloxystrobin TTR is 0.492 days. Aerobic soil metabolism half - lives could not be calculated for trifloxys trobin TTR because the submitted studies did not measure the non -parent isomers of concern until mid - way through each study. Although an uncertainty , this is not expected to substantially change the estimated exposure concentrations, as the non parent isomers were observed at < 5% applied radioactivity in these studies. The soil photolysis half - life for trifloxystrobin TTR was not calculated, as it is not currently used in aquatic exposure modeling. The half

- lives for trifloxystrobin TTR in the other laboratory studies are the same as those for the parent. Environmental fate data for trifloxys trobin and trifloxystrobin TTR are summarized in Table 2 . **Table 2**  **. Physical/Chemical Properties and Environmental Fate Data for Trifloxystrobin and Trifloxystrobin**  **TTR Param**  **eter Trifloxystrobin**  **1 Trifloxystrobin TTR** **2 Source**  Molecular Weight 408.4 MRID 44052801 Solubility ( 20 ◦ C ) 0.61 mg/L at pH7 MRID 44052801 Vapor Pressure ( 20 ◦ C ) 2.55e - 08 mm Hg DP Barcode D254920 Henry’s Law Constant 2.2e - 08 atm m 3 mo l - 1 DP Barcode 405629 Hydroly sis Half

- life Stable at pH 4

55.2 days at pH 7 0.83 days at pH 9 MRID 44496727 Aquatic Photolysis Half - life 14.8 days at pH 5 54.7 days at pH 5 MRID 44496727 TTR half - life calculated using NAFTA Degradation Kinetics Guidance (2012) and includes isomers identified in the study and expected to be in equilibrium with the parent in aquatic environments: CGA - 357261 and CGA - 357262 Photolysis on soil Half - life 2.1 days Not calculated 3 MRID 44496729

### 7

**Param eter**  **Trifloxystrobin 1**  **Trifloxystrobin TTR 2**  **Source** Aerobic Soil Metabolism Half

life 0.74, 0.41, and 0.91 days M ean = 0.69 d, S td = 0.25 d Not calculated4 MRID 44496732 MRID 44496730 MRID 44496731 Anaerobic Aquatic Metabolism Half

life 0.72 days MRID 44496733 No isomers identified in this study are expected to be in equilibrium with the parent in aquatic environments. Aerobic Aquatic Metabolism Half

life 0.60 days 0.492 days (tR IORE ) MRID 44496734

TTR half - life calculated using NAFTA Degradation Kinetics Guidance (2012) and includes an isomer identified in the study that is expected to be in equilibrium with the parent in aquatic environments: CGA - 331409 . Organic Carbon Partition Coefficient (KFOC ) (mL/g - oc ) Data for the parent (E,E) isomer: 2354, 951, 3064, 3927, 9871, 951 KF vs. organic matter coefficient of determination (r2 ) = 0.03 p - value = 0.72 Data for the Z, E isomer: 476, 526, 479, 389, 567 KF vs. organic matter coefficient of determination (r2 ) = 0.99, p - value = 0.001 MRID 44496802 (Parent) MRID 44496805 (Z,E isomer) For trifloxystrobin parent and the three isomers expected to be present in aquatic environments, only two adsorption desorption studies are available and considered

– one for the parent and one for CGA - 357261. CGA - 357261 is more mo bile and is therefore u sed as the

mo del input. Soil Partition Coefficient (KF ) (mL/g) Data for the parent (E,E) isomer: 6.8 Loamy Sand 7.7 Sandy Loam 16.0 Low Organic Matter Sand 59.4 High Organic Matter Sand 91.8 Clay Loam 33.2 Silt Loam Mean = 35.8; Std = 33.8 Data for the Z, E

isomer: 14.9 Loam 12.8 Clay Loam 2.8 Hanford Sandy Loam 3.2 Saw- Wake Sandy Loam 4.6 Sand Mean = 7.7 Std = 5.7 1 Trifloxystrobin Parent is the E,E isomer 2 Trifloxystrobin TTR includes the parent E,E, isomer and the E,Z; Z,E; and Z,Z, isomers. 3 Value currently not used in modeling, and was therefore not calculated for trifloxystrobin TTR.

### 8 4 Although the Z,E; Z,Z; and E,Z isomers were detected in the aerobic soil metabolism studies at levels below 5% of applied radioactivity, the studies did not report data for these isomers during the initial stages of each study. As a result, reliable half

- lives for trifloxystrobin TTR could not be calculated. 

## Estimation	of	Exposure **Aquatic	Exposure** The aquatic estimated environmental concentrations (EECs) in surface water were estimated with the Surface Water Concentration Calculator (SWCC version 1.106). The SWCC generates daily expos ures and 1 - in - 10 - ye ar EECs of trifloxystrobin that may occur in surface water bodies adjacent to application sites receiving trifloxystrobin through runoff and spray drift. A detailed description, documentation, and direct links for running the SWCC can be found at http://www.epa.gov/oppefed1/models/water/index .htm . EECs for trifloxystrobin TTR were estimated for the Michigan Beans, Washington Beans, and California Row Crop scenarios , using the maximum application rates on the proposed label and assuming an annual application for thirty years. Details on the pesticide application assumptions used for the modeling are summarized in Table 3 , and the environmental fate properties used for modeling are summari zed in Table 4 . The maximum peak, 21 - day , 60 - day means for the trifloxystrobin new uses are summarized in Table 5 . A sample SWCC output file from the Michigan Beans (aerial) modeling is in Appendix 3 . **Table 3**  **. Summary of application input param eters used in aquatic m**  **odeling for total toxic residues.**  **Model Input Param eter**  **Input Value and Unit Source/**  **Comment** SWCC Scenarios MI Beans WA Beans (NMC) 1 CA Row Crop (RLF v2) 2 Proposed End - Use Label (EPA Reg. # 264 - 1055) Maximum Single Application Rate 0.1344 kg ai/ha Maximum Num

ber of Applications per Year 2 Method of Application Ground Aerial Proposed End - Use Label (EPA Reg. # 264 - 1055) allows chemigation as well as ground and aerial applications; ground application is assessed instead of chemigation and is assumed to be protective of potential exposures from chemigation. Application Efficiency 0.99 0.95 December 2013 EFED Spray Drift Guidance

### 9

**Model Input Param eter**  **Input Value and Unit Source/**  **Comment** Spray Drift Fraction 0.062 0.125 Ty pe of Application Foliar Proposed End - Use Label (EPA Reg. # 264 - 1055). Initial Date of Application (month/day) MI Beans : June 1 WA Beans (NMC) : June 16 CA Row Crop (RLF v2) : January

1 Initial application dates are assumed to occur on

the crop emergence dates listed in scenario metadata. Minimum Interval between Applications 10 days Proposed End - Use Label (EPA Reg. # 264 - 1055) 1 Scenario developed for the N - Methyl Carbamate Cumulative Risk Assessment 2 Scenario developed for the Red - Legged Frog Endangered Species Risk Assessment **Table 4**  **. Summary of environmental fate input param**  **eters used in aquatic m odeling for total toxic residues.**  **Model Input Param eter**  **Input Value and Unit Source/Comments**  Foliar Half

- life Stable Assumption based on Input Parameter Guidance Molecular Weight 408.37 g/mol Calculated molecular weight of trifloxystrobin ( C 20 H 19 F 3 N 2 O 4 ) Vapor pressure (25°C) 2.55 x 10 - 8 torr USEPA Fact Sheet reports 3.4 x 10 - 6 torr (@25 °C) , PMRA Reg2004 - 03 and Trifloxystrobin (213) report 3.4 x 10 - 6 Pa @ 25 °C Solubility in water (20  C , pH 7 ) 0.61 mg/L MRID 44502801 Hydroly sis half

- life (25±1  C , pH 4 ) Stable MRID 44496727 Aqueous photolysis half

life (25±1  C , pH 5 ) 54.7 days MRID 44496727 Aerobic soil metabolism half - life (25±1°C) 0.96 days MRID s 44496732 , 44496730 , 44496731 The 90th percentile upper bound of mean (0.74, 0.41, and 0.91 days). Ana erobic soil metabolism half - life S table No Data Submitted Aerobic aquatic metabolism half

- life (25 °C) 1.48 days MRID 44496734 3 x the aerobic aquatic metabolism half - life for a single test system ( 0.492 days) , per input parameter guidance . Anaerobic aquatic metabolism half

- life (20 - 29  C) 2.16 days (assume 25 deg C) MRID 44496733

3 x the anaerobic aquatic metabolism half - life for a single test system (0.72 days). Freundlich s oil - water partition coefficient for isomer CGA - 357261 (Koc ) ( 25±1°C ) 487.4 mL/g - oc MRID 44496802 Mean Koc for isomer CGA - 357261 .

### 10

**Table 5**  **. SWCC**  **Trifloxystrobin TTR Estimated Environmental Concentrations (EECs) for the Proposed New**  **Uses Crop**  **Application**

**Method Maximum** 

**Application Rate**  **( lb**  **a.i./ acre**  **) #**  **of**

**App l**  **ications Minimum** 

**Appl ication**  **Interval (days)**  **Scenario**

**(State crop)**  **1 st** 

**Appl .**  **date (day**  **** **m o**  **) EECs**  ***** **(μg/L) Peak**  **21**

**day 60 day** 

Chickpea, Dry Peas, Lentil Aerial

Spray 0. 12 2 10 MI Beans 1 - Jun **1.08** 0.341 0.123 WA Beans (NMC) 16 -

Jun 0.902 0.289 0.103 CA Row Crops (RLF) 1 - Jan 1.04 **0.479 0.190** 

Ground Spray 0. 12 2 10 MI Beans 1 - Jun **0.667** 0.205 0.0736 WA Beans (NMC) 16 -

Jun 0.448 0.143 0.0511 CA Row Crops (RLF) 1 - Jan 0.540 **0.258 0.101**  *Values in **bold** are the most conservative values. 

### Terrestrial	Exposures The T - REX Model (version 1.5.2) was used to calculate EEC s for wildlife food items. To calculate maximum EECs, the model assumed two applications at the maximum application rate of 0.1 2 lb a.i./A, separated by a 10 - day interval. EEC s represent predicted peak residue levels which are expected to occur immediatel y after the second application. The model’s default foliar half - life of 35 - day is used , which is expecte d to account for persistence of trifloxystrobin and its isomers . **Table** 

### 6 provides predicted dietary-based EECs for the proposed new use on chickpeas, dry peas, and lentils . **Table 6**  **. Terrestrial**  **Dietary -**  **Base EECs for Proposed New Uses of Trifloxystrobin** 

**Crop Food Item**  **EEC (ppm)** Chickpea, Dry Peas, Lentil Short Grass 52.4 Tall Grass 24.0 Broadleaf Plants 29.5 Fruits/Pods/Seeds 3.28 Arthropods 20.5 

### The EECs were converted to an oral dose and compared with the oral toxicity data. These “dose based” EECs were calculated for small, medium, and large birds and mammals. Body weights of 20 g, 100 g, and 1000 g were assumed for small, medium, and large birds, respectivel y, and body weights of 15 g, 35 g, and 1000 g were assumed for small, medium, and large mammals, respectivel y. P redicted dose -based EECs are presented in

### 11

**Table** 

### 7 . **Table 7**  **. Terrestrial**  **Dose -**  **Based EECs Proposed New Uses of Trifloxystrobin**  **Crop Food Item**  **EEC ( mg/kg**  **- bw** **) Sm**  **all Medium**  **Large** Avian EECs Chickpea, Dry Peas, Lentil Short Grass 59.7 34.1 15.2

Tall Grass 27.4 15.6 6.99 Broadleaf Plants 33.6 19.2 8.57 Fruits/Pods/Seeds 3.73 2.13 0.95 Arthropods 23.4 13.3 5.97 Seeds 0.83 0.47 0.21

Mammalian EECs Chickpea, Dry Peas, Lentil Short Grass 50.0 34.6 8.01

Tall Grass 22.9 15.8 3.67 Broadleaf Plants 28.1 19.4 4.51 Fruits/Pods/Seeds 3.12 2.16 0.50 Arthropods 19.6 13.5 3.14 Seeds 0.69 0.48 0.11 

### TerrPlant (Version 1.1.2) was used to calculate EECs for non - target plant species inhabiting dry and semi - aquatic (wetland) areas. Parameter values for application rate, drift assumption and incorporation depth are based upon the use and related application method. A runoff value of 0.01 is utilized based on trifloxys trobin’s solubility , which is classified by TerrPlant as <10 mg/L. Predicted terrestrial plant EECs are provided in Table 8 . **Table 8**  **. Terrestrial Plant EECs for the New Uses of Trifloxystrobin** 

**Exposure Scenario EEC**  **Ground Applications Aerial Applications**  Runoff to dry areas 0.0012 0.0012 Runoff to semi - aquatic areas 0.012 0.012 Spray Drift 0.0012 0.006 Total for dry areas 0.0024 0.0072 Total for semi - aquatic areas 0.0132 0.018 

## Ecological **Effects Characterization**  **Effects	to Aquatic	Organisms** 

### 12

**Table** 

### 9 provides aquatic toxicity data that was used to assess the risk of trifloxystrobin to aquatic plants and animals. The toxicity data indicate that trifloxystrobin is very highl y toxic to fish and aquatic invertebrates on an acute exposure basis. Data for green algae ( Pseudokirchneriella subcapitata ) indicate toxicity to algae occurs at relatively low exposure levels, with toxicity endpoints comparable to the acute toxicity endpoints for fish and aquatic invertebrates. On a chronic basis, the most sensitive test species was the waterflea ( Daphnia magna ) , in which significant growth and reproduction was observed at 5.98 μg ai/L. The waterflea NOAEC was established at 2.76 μg ai/L. **Table 9**  **. Summ**  **ary of the Most Sensitive Endpoints from Aquatic Toxicity Studies for Trifloxystrobin**  **Taxonomic Group**  **Study**

**Type Surrogate Species**  **Toxicity Value (all units in terms of**  **measured active ingredient** **) Acute** 

**Toxicity Classification**  **Source**

Freshwater fish 1 Ac ute Rainbow Trout ( Oncorhynchus mykiss ) 96 - hr LC 50 = 14.3

μg/L Very highly toxic MRID

44502803 Chronic (Early Life Stage) Rainbow Trout NO AEC = 4.3 μg/L LO AEC = 7.7 μg/L Endpoint: Post - hatch survival -- MRID 44502804

Freshwater invertebrates Ac ute Water Flea ( Daphnia magna ) 48 - hr EC 50 = 25.3

μg/L Very highly toxic MRID

44496611 Chronic Water Flea NO AEC = 2.76 μg/L LO AEC = 5.98 μg/L Endpoint: Dry

weight and fecundity -- 44496615 Estuarine/marine fish Ac ute Sheepshead Minnow ( Cyprinodon variegatus ) 96 - hr LC 50 = 78 .0

μg/L Very highly toxic MRID

44496612 Estuarine/marine invertebrates Ac ute My sid ( Americamysis bahia ) 96 - hr EC 50 = 8.62

μg/L Very highly toxic 44496614 Aquatic plants and algae Vascular Duckweed ( Lemna gibba ) NO AEC = 410 μg/L 2

14 - d EC 50 >1930 μg/L 2 -- MRID 44496725 Non vascular Green Algae

(Pseudokirchneriella subcapitata ) NOAEC = 10 .5 μg/L

5 - d EC 50 = 37 .1 μg/L -- MRID 44496724 1 Freshwater fish may be surrogates for aquatic - phase amphibians. 2 These results are uncertain because the test material was unstable and renewals were not done, resulting in dramatic declines of the test material during the duration of the exposure period. The study was classified as Supplemental . 

### Available toxicity

data for CGA - 321113 , the major degradation product of trifloxystrobin, are given in **Table** 

### 1 0 . The data indicate that this compound is much less toxic to fish, aquatic invertebrates, and al gae than the parent compound. CGA - 321113 is classified as practicall y nontoxic to fish and aquatic invertebrates on an acute basis. A supplemental life - cycle study with CGA - 32 1 113 established an NOAEC for chronic effects at 3.2 mg/L. The chronic toxicity endpoints derived from this study were greater than 3 orders of magnitude higher than that

### 13

obtained for this species when tested with the parent compound. Although the lack of evaluation of growth endpoints (dry

weight or length) may

m ake this study

less sensitive than a study that adhered to the test guideline, the study provides sufficient evidence to conclude that this degradation product has much less chronic toxicity than the parent compound. **Table 1**  **0 .**  **Summary of the Most Sensitiv e Endpoints from Aquatic Toxicity Studies for CGA**  **- 321113**  **Taxonomic Group**  **Study**

**Type Surrogate Species**  **Toxicity Value (all units in terms**  **of me**  **asured active ingredient** **) Acute** 

**Toxicity Classification**  **Source**

**(M RID No.)**  Freshwater fish 1 Ac ute Rainbow trout 96 - hr EC 50 > 106 mg/L Practically

nontoxic 44527502

Freshwater invertebrates Ac ute Water Flea ( Daphnia magna ) 48 - hr EC 50 > 95.3

mg/L Practically

nontoxic 44527503 Chronic Water Flea NOAEC= 3.2 mg/L 2 LOAEC= 10.0 mg/L 2 Endpoint: Survival -- 44869701 Aquatic plants and algae Non vascular Green Algae

(Pseudokirchneriella subcapitata ) NOAEC = 15.7 mg/L 5 - d EC 50 = 7 7 .1 mg/L -- 44496724 1 Freshwater fish may be surrogates for aquatic - phase amphibians. 2 This study was classified as Supplemental because it did not follow the experimental design prescribed by the test guideline. The study did not evaluate growth parameters (dry weight or length) and thus the results may not be as sensitive as a fully acceptable study.

### 14

**Effects	to	Terrestrial	Organi sms**  **Table** 

### 1 1 provides toxicity data that was used to assess the risk of trifloxystrobin to terrestrial plants and animals. All available acute oral and subacute dietary studies in dic ate that trifloxystrobin is practically nontoxic to birds, mammals, and bees on an acute basis. Acute testing with the rat (Rattus norvegicus ) show that acute toxicity to mammals from the dermal and inhalation routes of exposure is also low. With chronic exposure, trifloxystrobin did not cause any observable toxic effect to birds at dietary concentrations up to 320 mg a.i./kg - diet. Chronic toxicity to birds at exposures greater than 320 mg ai/kg - diet is not known; however, maximum residues on terrestrial food items from the proposed uses are not expected to reach this concentration. Chronic toxicity studies with the laboratory rat showed body

weight effects to adult and young with chronic exposures of 750 mg a.i./kg - diet and above, with an NOAEL established at 500 mg a.i./kg - diet. No reproductive impairment was noted in rats exposed to up to 1500 mg a.i./kg - diet. Testing with the honey bee found that trifloxystrobin is practicall y nontoxic to bees. Tier I phy

totoxicity studies found that exposure of triflox ys trobin to terrestrial plants at approximately

0.25 lb a.i./A caused some inhibition of growth (no more than 13% inhibition). These studies are adequate for demonstrating that the proposed uses of trifloxystrobin would have little toxicity

to target plants that are sprayed directly at the maximum label application rate. **Table 1**  **1 .**  **Summary of the Most Sensitive Endpoints from Terrestrial Toxicity Studies for Trifloxystrobin Taxonomic**  **Group Study Type**  **Surrogate Species**  **Toxicity Value**

**(all units in terms of active ingredient)**  **Acute Toxicity Classification**  **Source**

**(M RID No.)** 

Birds 1 Ac ute Bobwhite ( Colinus virginianus ) LD 50 > 2000 mg/kg -bw

(No mortality) Practically nontoxic 44496606 Sub - acute dietary Bobwhite and

Mallard ( Anas platyrhynchos ) LC 50 > 5050 mg/kg - diet

(No treatment - related mo rtality) Practically nontoxic 444966 - 07

444966 - 08 Chronic Bobwhite quail NO AEC = 320 mg/kg diet LO AEC > 320 mg/kg - diet -- 44496609

Mammals Ac ute Oral Laboratory rat (Rattus norvegicus ) LD 50 > 5000 mg/kg -bw

(No mortality, minor sublethal effects 2 ) P ractically nontoxic 44496622 Ac ute Dermal L aboratory rat LD 50 > 2000 mg/kg -bw Toxicity Category III - IV 44496627 Ac ute Inhalation Laboratory rat LC 50 > 4.65 mg/L Toxicity Category I V 44496630

### 15

**Taxonomic Group**  **Study Type Surrogate**  **Species Toxicity Value** 

**(all units in terms of active ingredient)**  **Acute Toxicity Classification**  **Source**

**(M RID No.)** 

Chronic (2 - Gen. Repro.) Laboratory rat

(Rattus norvegicus ) Parental:

NO AEL : 50 ppm LO AE L: 750 ppm Endpoint: Reduced body weight, body weight gain, and food consumption Offspring: NO AEL : 50 ppm LO AE L: 750 ppm Endpoint: Reduced body weight Reproduction: NO AEL : 1500 ppm LO AE L: >1500 ppm -- 44496710

Insects Ac ute

contact Honey bee

( Apis mellifera L. ) LD 50 > 200 μg/bee Practically nontoxic 44496726

Terrestrial plants Seedling

Emergence Dicot

– cabbage 13% inhibition in dry weight at 0.249 lb a.i./A

-- 44496723 Monocot

– ryegrass 7% inhibition in dry

weight at 0.249 lb a.i./A Vegetative vigor Dicot

– tomato 10% inhibition in dry weight at 0.249 lb a.i./A 44496723 Monocot

– ryegrass 9% inhibition in dry

weight at 0.249 lb a.i./A 1 Birds represent surrogates for terrestrial - phase amphibians and reptiles. 2 Observed sublethal effects included hypersensitivity to touch, red stained face, excessive salivation, soft or watery stool, and dark stained or wet urogenital area, and decreased body weight (3 - 4%) in three of five females during the 7 to 14 day interval. 

### No in vivo studies are available on the toxicity of CGA - 32111 3 to terrestrial organisms. However, an in vitro study of this compound using rat hepatocy te cultures has been submitted to the EPA (MRID 44496720). This study found that CGA - 321113 does not express the toxic mechanism of action of the parent compound, i.e ., inhibition of mitochondrial respiration, and is much less toxic to hepatocy te cells than is the parent. The NOAEL was 600 μM for CGA 321113 compared to <30 μM for trifloxys trobin. These results agree with the findings of aquatic toxicity studies which also showed that CGA - 321113 is much less toxic to animals and plants than triflox ys trobin.

### 16



## Ecological **Risk	Estimation** Risk characterization compares EECs to toxicity endpoints to determine whether the proposed uses pose ecological risks that exceed EPA’s levels of concern (LOC). In a deterministic approach, a single point estimate of toxicity is divided by

an exposure estimate to calculate a risk quotient (RQ). The RQ is then compared to Agency LOCs, which serve as criteria for categorizing potential risk to non - target organisms (see Appendix 2). In this assessment, RQs were calculated with EECs that represent total concentrations of all racemic isomers of trifloxystrobin. **Risk	to	Aquatic	Organisms** Acute aquatic RQs range from <0.01 to 0.13 ( Table 1 2 ). Because acute RQs are less than the acute LOC for non - listed species (0.5), the proposed uses are not expected to pose high acute risk to fish and aquatic invertebrates. However, RQs for saltwater invertebrates are above the endangered species LOC . The RQ for freshwater fish also exceeded the listed species LOC for aerial applications. Chronic RQs ranged from < 0.0 1 to 0.0 6 ( Table 1 3 ) . Because all of the chronic RQs were less than the chronic LOC (1), the proposed uses are expected to pose minimal chronic risk to fish and aquatic invertebrates. **Table 1 2**  **. Acute RQs for Fish and Aquatic Invertebrates**  **Use Scenario Habitat Type**  **Peak EEC ( μg/L)**  **EC 50**  **(μg a.i./L) RQ**  **2 (EEC/EC**  **50 )** 

**Fish Inverts.**  **Fish Inverts.**  Aerial Applications 2 applications at 0. 119 lb a.i./A, separated by 10 - day interval Freshwater 1.08 14.3 25.3 0.076* 0.043 Saltwater 1.08 78.0 8.62 0.014 0.13* Ground Applications 2 applications at 0. 119 lb a.i./A, separated by 10 - day interval Freshwater 0.667 14.3 25.3 0.047 0.026 Saltwater 0.667 78.0 8.62 <0.01 0.077* * Exceeds the LOC for Acute endangered species (RQ ≥ 0.05) **Table 1 3**  **. Chronic RQs for Fish and Aquatic Invertebrates Use Scenario**  **Habitat Type Average**  **EEC (μg/L)**  **1 NOAEC (μg**  **a.i./L) RQ**  **1 (EEC/** **NOAEC )** 

**Fish Inverts.**  **Fish Inverts.**  Aerial Applications 2 applications at 0.119 lb a.i./A, separated by 10 - day interval Freshwater 21 - d: 0.479 60 - d: 0.190 4.3 2.76 0.044 0.17 Saltwater2 21 - d: 0.479

60 - d: 0.190 23.5 0.94 <0.01 0.51 Ground Applications 2 applications at 0.119 lb a.i./A, separated by 10 - day interval Freshwater 21 - d: 0.258 60 - d: 0.101 4.3 2.76 0.023 0.060 Saltwater2 21 - d: 0.258

60 - d: 0.101 23.5 0.94 <0.01 0.27

### 17 1 The 60 - d average EEC is used for fish RQs, whereas the 21 - d EEC is used for invertebrate RQs. 2 Chronic endpoints for saltwater species were estimated from acute toxicity endpoints on acute - to - chronic ratios (ACRs) derived from freshwater species. The ACR was 3.33 for fish and 9.17 for crustaceans. 

### For aquatic vascular and non - vascular plants, RQs range from < 0.01 to 0.029 for non - listed species, and < 0.0 1 to 0.10 for listed species ( Table 1 4 ). Because all of the RQs are less than the LOC for aquatic vascular and non - vascular plants (1), the proposed new uses are expected to pose minimal risk to listed and non - listed species of aquatic vascular and non - vascular plants. **Table 1 4**  **. RQs for Vascular**  **and Non -**  **vascular Aquatic Plants**  **Use Scenario Peak**  **EEC (**  **μg/L )**  **Vascular Plant**  **RQ 1**  **Non -**  **Vascular Plant**  **RQ 2** 

**Non -**  **listed Species**  **(EEC/EC 50**  **) Listed Species** 

**(EEC/NOEC) Non**  **- listed** 

**Species (EEC/EC**  **50 )**  **Listed Species**

**(EEC/NOEC)** Aerial Applications 2 applications at 0.119 lb a.i./A, separated by 10 - day interval 1.08 < 0.01 <0.01 0.029 0.10 Ground Applications 2 applications at 0.119 lb a.i./A, separated by 10 - day interval 0.667 <0.01 <0.01 0.018 0.063 1 B ased on the green algae EC50 of 0.024 ppm 2 B a sed on the duckweed EC50 of >1.93 ppm 

### In conclusion, the risk assessment for aquatic organisms indicates that the new use of trifloxystrobin on chickpeas, dry peas, and lentils will not pose a risk to any aquatic organism that exceeds the EPA LOC for non - listed species, but the LOC for listed saltwater invertebrates is exceeded , as is the LOC for listed freshwater fish when trifloxystrobin is applied by air. **Risk	to	Terrestrial	Organisms** The T - REX model was used to calculate acute and chronic risk quotients (RQs) fo r the proposed new uses on chickpea, dry peas, and lentils. For acute risk, the non - definitive “greater than” value generated b y the acute toxicity values were entered into the model as if they were definitive values. Thus, while the actual acute RQs are unknown, we know that they are less than the RQs generated b y this approach. This approach is , therefore , appropriate for conducting a conservative screen of acute risk. Endpoints from chronic studies were definitive, and thus the chronic RQs are the actual values. For birds, acute dose -based RQs ranged from <0.01 to 0.0 6 ( Table 1 5 ) , and acute dietary-based RQs were all less than or equal to 0.01 (Table 1 7 ) . All acute RQs were less than the LOC for risk to non - endangered species (0.5) , as well as the LOC fo r risk to threatened and endangered species (0. 1 ). As mentioned above , these RQs are conservative since they were calculated using the limit dose of 2000 mg a.i/kg and no mortality was observed at this limit dose . For chronic risk, RQs ranged from 0.01 to 0. 16 (Table 17) . All chronic RQs were less than the EPA’s LOC for chronic risk (1.0). In conclusion, the risk assessment indicates that the proposed new uses will pose minimal risk to birds, and are not expected to directl y harm any threatened or

### 18

endangere d (listed) species of birds . These conclusions also apply to reptiles and terrestrial phased amphibians, for which birds serve as a surrogate. For mammals , acute dose -based acute RQs were all less than 0.01 ( Table 1 5 ) . All acute RQs were therefore less than the LOC for risk to listed species (0. 1 ) as well as the LOC for non - listed species (0.5). Chronic dose -based RQs ranged from <0.01 to 0. 30 (Table 1 6 ) and chronic dietarybased RQs ranged from < 0.01 to 0. 03 (Table 1 7 ) . All chronic RQs were less than th e EPA’s LOC for chronic risk (1.0). In conclusion, the risk assessment indicates that the proposed new uses will pose minimal risk to mammals, and are not expected to directly harm any listed species of mammals.

### 19

**Table 1 5**  **. Acute**  **Terrestrial Dose -**  **Based RQs for**  **Proposed New Uses of Trifloxystrobin Crop**  **Food Item Risk Quotient**  **Sm all**  **Medium Large**  Birds 1 Chickpea, Dry Peas, Lentil Short Grass 0.06 0.03 0.01

Tall Grass 0.03 0.01 <0.01 Broadleaf Plants 0.03 0.01 <0.01 Fruits/Pods/Seeds <0.01 <0.01 < 0.01 Arthropods 0.02 0.01 <0.01 Seeds <0.01 <0.01 <0.01 Mammals 2 Chickpea, Dry Peas, Lentil Short Grass <0.01 <0.01 <0.01

Tall Grass <0.01 <0.01 <0.01 Broadleaf Plants <0.01 <0.01 <0.01 Fruits/Pods/Seeds <0.01 <0.01 <0.01 Arthropods <0.01 < 0.01 <0.01 Seeds <0.01 <0.01 <0.01 1 Assumed bodyweights for small, medium, and large birds are 20 g, 100 g, and 1000 g, respectively. Avian toxicity is based on the LD 50 for the bobwhite (>2000 mg a.i./kg -bw , MRID 44496606). The weight - adjusted LD 50 estimates are 1038, 1322, and 1867 mg a.i./kg -bw for small, medium, and large birds, respectively. 2 Assumed bodyweights for small, medium, and large mammals are 15 g, 35 g, and 1000 g, respectively. Mammalian toxicity is based on the LD 50 for the laboratory rat (>5000 mg a.i./kg -bw , MRID 44496622). The weight - adjusted LD 50 estimates are 10,890, and 8891, and 3846 mg a.i./kg -bw for small, medium, and large birds, respectively. **Table 1 6**  **. Chronic Mammali**  **a n**  **Dose -**  **Based RQs for Proposed New Us es of Trifloxystrobin**  **Crop Food Item**  **Risk Quotient Sm**  **all Medium**  **Large** Chickpea, Dry Peas, Lentil Short Grass 0.30 0.26 0.14

Tall Grass 0.14 0.12 0.06 Broadleaf Plants 0.17 0.15 0.08 Fruits/Pods/Seeds 0.02 0.02 0.01 Arthropods 0.12 0.10 0.05 Seeds <0.01 <0.01 <0.01 1 Assumed bodyweights for small, medium, and large birds are 20 g, 100 g, and 1000 g, respectively. Avian toxicity is based on the LD 50 for the bobwhite (>2000 mg a.i./kg -bw , MRID 44496606). The weight - adjusted LD 50 estimates are 1038, 1322, and 1867 mg a.i./kg -bw for small, medium, and large birds, respectively. 2 Assumed bodyweights for small, medium, and large mammals are 15 g, 35 g, and 1000 g, respectively. Mammalian toxicity is based on the LD 50 for the laboratory rat (>5000 mg a.i./kg -bw , MRID 44496622). The weight - adjusted LD 50 estimates are 10,890, and 8891, and 3846 mg a.i./kg -bw for small, medium, and large birds, respectively.

### 2 0

**Table 1 7**  **. Terrestrial Dietary**  **- Base**  **Acute and Chronic RQs for Proposed New Uses**  **of Trifloxystrobin**

**Crop Food Item**  **RQs Acute**  **Chronic** Birds 1 Chickpea, Dry Peas, Lentil Short Grass 0.01 0.16

Tall Grass <0.01 0.08 Broadleaf Plants 0.01 0.09 Fruits/Pods/Seeds <0.01 0.01 Arthropods <0.01 0.06

Mammals 2 Chickpea, Dry Peas, Lentil Short Grass N/A 3 0.03

Tall Grass N/A 0.02 Broadleaf Plants N/A 0.02 Fruits/Pods/Seeds N/A <0.01 Arthropods N/A 0.01 1 Avian acute RQs are based on the dietary LC 50 for the bobwhite and mallard (> 5050 mg a.i./kg - diet, MRID 44496607 and 44496608). Avian chronic RQs are based on the avian reproductive NOAEC for the bobwhite (320 mg/kg - diet, MRID 44496609). 2 Mammalian acute RQs are were not calculated because no acute dietary LC 50 was available. Mammalian chronic RQs are based on the two - generation reproduction NOAEC for the laboratory rat (50 mg a.i./kg - diet, MRID 44496710). 3 RQ could not be calculated because acute dietary toxicity data are not available for mammals. 

### The acute contact toxicity v alue for honey

bees is >200 ug/bee, which is practicall y non - toxic. Risk estimations for terrestrial invertebrates are not routinely conducted. Based on the low acute contact toxicity

study to honey bees, acute risk to adult terrestrial insects is expected to be l ow . However, additional data are needed for the EPA to conduct a complete risk assessment for potential adverse effects to honey bees and other insect pollinators. Because bees are attracted to the blooms of legume crops, bees may be exposed to nectar and pollen of the crops of this new use. Therefore, a honey

bee acute oral toxicity

study is needed to assess risk from oral exposure. Also, chronic toxicity

studies with adult and larval bees are needed to assess the risk of lethal and sublethal effects from chronic exposure to trifloxystrobin. Table 18 provides RQs for non - target plants for the proposed new uses on chickpeas, dry peas, and lentils. For both aerial and ground applications, all RQs calculated for non - listed terrestrial plants were less than 0.1. These RQs were less than one - tenth the LOC for listed terrestrial plants, and thus indicate minimal risk to all non - target plants. RQs for listed species of terrestrial plants could not be calculated because phytotox icity tests failed to obtain either a NOAEL or an EC 05 

### for terrestrial plants. In the T ier I phy totoxicity test with trifloxystrobin, exposure to plants at 0.25 lb a.i./A did not have any more than a 13% inhibitory effect on any

plant tested. The maximum s easonal application rate for the proposed new uses is approximately equal to the exposure rate used in this limit test . Therefore, while the risk to terrestrial plants appears to be low, possible adverse effects to listed species of terrestrial plants cann ot be discounted.

### 21

**Table 1 8**  **. RQ**  **s for**  **Plants in**  **D ry and**  **S em** **i -**  **aquatic A**  **reas E**  **xposed to Trifloxystrobin TTR**  **through R** **unoff and/or**  **S pray**  **D rift.**  **Use Scenario Plant Type**  **Listed Status Dry**  **Semi -** **Aquatic Spray Drift**  Aerial Application on Chickpea, Dry Peas, or Lentil Monocot Non - listed <0.1 <0.1 <0.1 Listed N/A 1 N/A N/A Dicot Non - listed <0.1 <0.1 <0.1

Listed N/A N/A N/A Ground Application on Chickpea, Dry Peas, or Lentil Monocot Non - listed <0.1 <0.1 <0.1 Listed N/A N/A N/A Dicot Non - listed <0.1 <0.1 <0.1

Listed N/A N/A N/A 1 RQs are not available for listed species because phytotoxicity studies with trifloxystrobin failed to establish an NOAEC . 

### Incident Reports On 4 August 2014, the Ecological Incident Information System (EIIS, v. 2.1) , Incident Data System (IDS), and Avian Incident Monitoring S ys tem (AIMS) w ere queried for ecological incidents involving exposure to trifloxystrobin. The EIIS database contains 28 incidents that were associated with trifloxystrobin (Table 19). All of these incidents involved damage to plants that were directl y treated with trifloxys trobin. All of the incidents had a certainty index of either “possible” or “probable.” None of the incidents were associated with known misuse of trifloxystrobin. Except for incidents on ornamental plants, most of the incidents involved exposure to one or more pesticide other than trifloxystrobin, and thus the causal agent is uncertain. For ornamental plants, however, all but one of these involved exposure to only trifloxystrobin, providing stronger evidence that trifloxystrobin caused the plant damage. All of the ornamental plant incidents occurred in nurseries in Florida. **Table 19. Ecological Incidents Associated with the Use of Trifloxystrobin.**

Crop Number of Incidents Involving

Trifloxystrobin and other Pesticides Number of Incidents Involving T rifloxystrobin Cereal 1 0 Corn 4 0 Grape 1 1 Ornamental Plants 1 10 Soy bean 2 1 Wheat, spring 5 0 Wheat, winter 1 0 Tomato 0 1 Total 15 13 

### The Incident Data S ys tem (IDS) was also queried for aggregated incident reports that listed ecological incidents for products containing trifloxystrobin. Ten a ggregate d incident report were reported for minor plant damage incidents associated with products containing trifloxystrobin. The products involved in these incident reports included Stratego YLD (5) , Stratego (3), and

### 22

Gem 25WG (2). No aggregated incidents were reported for adverse effects to animals. Also, n o avian incidents have been reported for trifloxys trobin in the AIMS database of the American Bird Conservancy . Altogether, ecological incidents suggest that trifloxys trobin may cause adverse effects to plants that are sprayed directl y. They do not provide evidence of risk to plants exposed by spray drift or runoff, or risk to non - target organisms other than plants. **Risk Description Non**  **- target Aquatic Animals and Plants**  Aquatic Animals Although trifloxystrobin is highly toxic to aquatic animals , the low application rate, low persistence, and low mobility in soils together work to limit aquatic exposure. Based on water modeling conducted with three different scenarios (Michigan beans, Washington beans, and California row crops), the combined aquatic residues of trifloxystrobin and its racemic isomers are not expected to reach lev els where the risk would exceed the EPA’s level of concern (LOC) for non - listed species. However, peak EECs for ground and aerial applications were high enough to result in RQs that exceed the li sted species LOC for saltwater invertebrates, and peak EECs f or aerial applications also exceeded the listed species LOC for freshwater fish. These acute aquatic risks are similar to those previously predicted for other registered uses of trifloxystrobin. Concentrations of trifloxystrobin and its racemic isomers did not reach toxic levels on a chronic basis. Triflox ys trobin was found to be less toxic to aquatic plants than to aquatic animals. None of the RQs for aquatic plants exceeded the LOC for either non - listed or listed species. Therefore, risk to aquatic plant s is not a concern. **Non -**  **target Terrestrial Animals and Plants** Toxicity studies indicate that trifloxystrobin has low acute toxicity to all terrestrial animals tested. Because of this low toxicity, combined with the relativel y low application rate, the acute risk to terrestrial animals are predicted to be below the LOC for both listed and non - listed species . Because p eak EECs did not exceed the NOAEC for chronic effects to birds or mammals, chronic RQs are less than one, indicating that chronic risk to terre strial animals is not a concern . The proposed new use of trifloxys trobin are expected to result in both contact and oral exposure to bees and other insect pollinators. Because the acute contact toxicity of trifloxystrobin to the honey bee is very

l ow ( LD 50 

### > 200 μg a.i. /bee) and the application rate s of trifloxystrobin are low, acute risk to bees and other insect pollinators from contact exposure is assumed to be low. However, additional tier- 1 honey bee toxicity

studies are needed for EFED to conduct a

### 23

complete tier- 1 risk assessment for insect pollinators. The additional honey bee studies that are needed are listed below in the section on uncertainties. Both the T ier I phy

totoxicity tests and the incident data indicate that trifloxystrobin can cau se some phy totoxicity to plants that receive full direct spray at the application rate. Tier I seedling emergence and vegetative vigor studies found that exposure of some plants at or near the maximal seasonal rate of 0.25 lb a.i./A resulted in inhibition of growth ranging from 7% to 13%. In cidents have also been reported that allege that crops have been damaged by direct application of triflox ys trobin. However, the risk assessment indicates that off - site exposure from spray drift and runoff is not expected to reach levels that are toxic to plants. RQs calculated for non - listed terrestrial plants were all below 0.1, well below the LOC of 1. Therefore, risk to non - listed terrestrial plants is not a concern. However, because some growth effects were observed in the Tier I phy totoxicity studies, and some incidents of plant damage have been reported, the possibility

of adverse effects to listed plants cannot be excluded at this time. 

## Uncertainties The Registration Review Preliminary Problem Formulation completed for triflo xystrobin in 2013 requests the following ecotoxicity studies (DP405629):

 Guideline 850.4500, Aquatic Algae Growth and Reproduction, Tier II (The guidelin e is satisfied for freshwater green algae, but additional testing is needed with a freshwater diatom and a saltwater diatom.)  Guideline 850.4450, Cyanobacteria Toxicity with Anabaena flos - aquae (bluegreen algae)  Guideline 850.4100, Terrestrial Plant Toxic ity, Seedling Emergence Test  Guideline 850.4150, Terrestrial Plant Toxicity, Vegetative Vigor Test Tier 1 honey

bee toxicity

studies are now also requested for assessing all new pesticide uses with potential exposure to insect pollinators. In addition to the honey bee acute contact toxicity study , which has already been submitte d, the following studies are now needed to complete the tier- 1 bee risk assessment:

 A honey

bee acute oral study

(OECD 213)  A honey

bee chronic oral toxicity

study with adult bees  A honey

bee chronic oral toxicity

study with bee larvae. Depending on the results of these studies, additional higher- tiered honey bee testing may

be required. For terrestrial plants, the EC 25 

### is > 0.25 lb a.i./A. Using that value, the LOC for non - listed terrestrial plants would not be exceeded; however, neither a NOAEC nor an EC 05 

### has been

### 24

established for terrestrial plants. Therefore, there is uncertainty in whether there is or is not a hazard to threatened and endangered terrestrial plants. Since the data from the Tier I study are not sufficient for calculation of an EC 05 

### nor determining a NOAEC, risk to endangered plant species cannot be assessed . Tier 2 phytotoxicity studies have been recommended in the recent Registration Review problem formulation for trifloxystrobin (D405269) to reduce this uncertainty and to support uses with application rates above 0.25 lb a.i./A. However , considering that the single application rate of the current new use is half of the application rate used in the terrestrial p lant study

mentioned above (MRID 44496723) , significant adverse effects to listed terrestrial plants appear to be unlikely .

### 25

**REFERENCES** Burns, L. A. 2002. EXAMS ( Exposure Analysis M odeling S ys tem) Version 2.98.04.06. Environmental Research Laboratory . U. S. Environmental Protection Agency . Athens, GA. Carsel et al. 1997. PRZM (Pesticide Root Zone Model) Version 3.12.2 Environmental Research Laboratory . U. S. Environmental Protection Agency . Athens, GA. FAO 2000. Appendix 2. Parameters of pestic ides that influence processes in the soil. In FAO In formation Division Editorial Group (Ed.), Pesticide Disposal Series 8. Assessing Soil Contamination. A Reference Manual. Rome: Food & Agriculture Organization of the United Nations (FAO). http://www.fao.org/docrep/003/x2570e/x2570e00.htm Fletcher, J.S., J.E. Nellessen, and T.G. Pfleeger. 1994. Literature review and evaluation of the EPA food - chain (Kenaga) nomogram, an instrument for estimating pesticide residues on plants. Environ. Tox. Chem. 13:1383 - 1391. Hoerger, F. and E. E. Kenaga. 1972. Pesticide Residues on Plants: Correlation of Representative Data as a Basis for Estimation of their Magnitude in the Environment. In F. Coulston and F. Korte, eds., Environmental Quality and Safety: Chemistry, Toxicology, and Technology, Georg Thieme Publ., Stuttgart, West Germany , pp. 9 - 28. USEPA. 1998. Guidelines for Ecological Risk Assessment. Risk Assessment Forum, Office of Research and Development, Washington, D.C. EPA/630/R - 95/002F. April 1998. http://cfpub.epa.gov/ncea/cfm/recordisplay .cfm?deid=30759 USEPA. 2004. Overview of the Ecological Risk Assessment Process in the Office of Pesticide Programs. U.S. Environmental Protection Agency, Office of Prevention, Pesticides and Toxic Substances, Office of Pesticide Programs, Washington DC. January 23, 2004. USEPA. 2006. User’s Guide TerrPlant version 1.2.2 . December 2006. United States Environmental Protection Agency . Environmental Fate and Effects Division. Office of Pesticide Programs. USEPA 2009a. Guidance for Selecting Input Parameters in Modeling the Environmental Fate and Transport of Pesticides. Version 2.1 October 22, 2009. http://www.epa.gov/oppefed1/models/water/input_guidance2_28_02.htm . U.S. Environmental Protection Agency , Office of Pesti cide Programs, Environmental Fate and Effects Division. Arlington, VA. USEPA 2009b. DRAFT Guidance for Modeling Pesticides Total Toxic Residues (TTR) May 20, 2009. U.S. Environmental Protection Agency, Office of Pesticide Programs, Environmental Fate and Effects Division. Arlington, VA.

### 26

USEPA 2012a. Guidance for Residues of Concern in Ecological Risk Assessment. December 20, 2012. U.S. Environmental Protection Agency, Office of Pesticide Programs, Environmental Fate and Effects Division. Arlington , VA. USEPA 2012 b . NAFTA Guidance for Evaluating and Calculating Degradation Kinetics in Environmental Media. December 17, 2012. U.S. Environmental Protection Agency , Office of Pesticide Programs, Environmental Fate and Effects Division. Arlington, VA. USEPA 2012 c . Standard Operating Procedure for Using the NAFTA Guidance to Calculate Representative Half

- life Values and Characterizing Pesticide Degradation. November 30, 2012. U.S. Environmental Protection Agency , Office of Pesticide Programs, Environmental Fate and Effects Division. Arlington, VA. **APPENDIX 1**  **. SWCC**  **O utput**  **F ile**  **: Michigan Beans, Aerial Application** Variable Volume Water Model, SWCC Compatible Version ******************************************* Performed on: 7/22/2014 at 11: 2 Peak 1 - in - 10 = 1.08 ppb Chronic 1 - in - 10 = 0.202E - 01 ppb Simulation Avg = 0.184E - 01 ppb 4 - day avg 1 - in - 10 = 0.668 ppb 21 - day avg 1 - in - 10 = 0.341 ppb 60 - day avg 1 - in - 10 = 0.123 ppb 90 - day avg 1 - in - 10 = 0.820E - 01 ppb Benthic Pore Water Peak 1 - in - 10 = 0.609E - 01 ppb Benthic Pore Water 21 - day avg 1 - in - 10 = 0.433E - 01 ppb Benthic Conversion Factor = 19.9 - Pore water (ug/L) to (total mass, ug)/(dry sed mass,kg) Benthic Mass Fraction in Pore Water = 0.186E - 01 YEAR Peak 4 - day 21 - day 60 - day 90 - day

Yearly Avg Benthic Pk Benthic 21 - day 1 9.27E - 01 6.04E - 01 3.40E - 01 1.23E - 01 8.20E - 02 2.02E - 02 5.01E - 02 3.11E - 02 2 1.39E+00 7.84E - 01 3.37E - 01 1.21E - 01 8.05E - 02 1.98E - 02 1.30E - 01 4.73E - 02 3 9.19E - 01 5.71E - 01 3.16E - 01 1.13E - 01 7.56E - 02 1.86E - 02 3.55E - 02 2.58E - 02 4 9.03E - 01 5.55E - 01 3.08E - 01 1.11E - 01 7.40E - 02 1.83E - 02 5.37E - 02 2.78E - 02 5 8.99E - 01 5.44E - 01 2.94E - 01 1.05E - 01 7.03E - 02 1.73E - 02 3.20E - 02 2.44E - 02 6 9.43E - 01 5.99E - 01 3.41E - 01 1.22E - 01 8.17E - 02 2.01E - 02 4.01E - 02 2.93E - 02 7 9.40E - 01 5.89E - 01 3.31E - 01 1.18E - 01 7.87E - 02 1.94E - 02 3.82E - 02 2.75E - 02 8 9.29E - 01 5.77E - 01 3.26E - 01 1.20E - 01 7.97E - 02 1.96E - 02 3.70E - 02 2.72E - 02 9 1.00E+00 6.73E - 01 3.83E - 01 1.40E - 01 9.36E - 02 2.31E - 02 5.30E - 02 4.43E - 02 10 9.01E - 01 5.38E - 01 2.88E - 01 1.03E - 01 6.85E - 02 1.69E - 02 3.09E - 02 2.21E - 02 11 9.19E - 01 5.79E - 01 3.17E - 01 1.14E - 01 7.60E - 02 1.87E - 02 3.79E - 02 2.63E - 02 12 8.96E - 01 5.39E - 01 2.89E - 01 1.04E - 01 6.92E - 02 1.71E - 02 3.50E - 02 2.28E - 02 13 9.37E - 01 5.89E - 01 3.32E - 01 1.18E - 01 7.89E - 02 1.95E - 02 3.93E - 02 2.90E - 02 14 9.17E - 01 5.66E - 01 3.11E - 01 1.11E - 01 7.42E - 02 1.83E - 02 3.39E - 02 2.48E - 02 15 8.93E - 01 5.23E - 01 2.75E - 01 9.89E - 0 2 6.60E - 02 1.63E - 02 2.97E - 02 2.17E - 02 16 9.15E - 01 5.57E - 01 3.03E - 01 1.08E - 01 7.21E - 02 1.78E - 02 3.32E - 02 2.38E - 02 17 8.85E - 01 5.17E - 01 2.69E - 01 9.68E - 02 6.45E - 02 1.59E - 02 2.80E - 02 1.99E - 02

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18 8.92E - 01 5.30E - 01 2.79E - 01 9.94E - 02 6.63E - 02 1.64E - 02 3.09E - 02 2.11E - 02 19 9.05E - 01 5.59E - 01 3.00E - 01 1.09E - 01 7.23E - 02 1.78E - 02 3.32E - 02 2.36E - 02 20 9.12E - 01 5.73E - 01 3.10E - 01 1.13E - 01 7.55E - 02 1.86E - 02 3.49E - 02 2.51E - 02 21 9.20E - 01 5.75E - 01 3.17E - 01 1.13E - 01 7.55E - 02 1.86E - 02 4.65E - 02 2.73E - 02 22 1.09E+00 6.22E - 01 2.97E - 01 1.06E - 01 7.08E - 02 1.75E - 02 6.17E - 02 3.39E - 02 23 9.35E - 01 6.04E - 01 3.36E - 01 1.22E - 01 8.12E - 02 2.00E - 02 3.98E - 02 2.86E - 02 24 9.31E - 01 5.77E - 01 3.23E - 01 1.15E - 01 7.68E - 02 1.89E - 02 3.68E - 02 2.64E - 02 25 9.10E - 01 5.63E - 01 2.97E - 01 1.07E - 01 7.14E - 02 1.76E - 02 3.37E - 02 2.36E - 02 26 1.43E+00 8.72E - 01 3.80E - 01 1.37E - 01 9.12E - 02 2.25E - 02 9.93E - 02 4.69E - 02 27 8.75E - 01 4.88E - 01 2.44E - 01 8.64E - 02 5.76E - 02 1.42E - 02 2.43E - 02 1.62E - 02 28 8.90E - 01 5.26E - 01 2.73E - 01 9.75E - 02 6.50E - 02 1.60E - 02 2.90E - 02 1.99E - 02 29 9.05E - 01 5.40E - 0 1 2.92E - 01 1.05E - 01 6.97E - 02 1.72E - 02 3.11E - 02 2.28E - 02 30 9.22E - 01 5.84E - 01 3.21E - 01 1.15E - 01 7.65E - 02 1.89E - 02 4.04E - 02 2.72E - 02 ********************************************************************************************* ** ***** Effective compartment halflives averaged over simulation duration: zero washout 0 water col metab halflife (days) = 3.74860934970674 zero hydrolysis 0 photolysis halflife (days) = 7704.75777615493 volatile halflife (days) = 13967.9605636501 total water col halflife (days) = 3.74578164510793 zero burial 0 benthic metab halflife (days) = 5.47094337524768 zero benthic hydrolysis 0 total benthic halflife (days) = 5.47094337524768 *********************************************************************** Fractional Contribution of Transport Processes to Waterbody & Total Mass (kg): Due to Runoff = 0.0370 0.3917E - 01 Due to Erosion = 0.0112 0.1187E - 01 Due to Drift = 0.9518 1.008 *********************************************************************** Flow in/out Characteristics of Waterbody: Average Daily Runoff Into Waterbody (m3/s) = 4.882614124166565E - 004 Baseflow Into Waterbody (m3/s) = 0.000000000000000E+000 Average Daily Flow Out of Waterbody (m3/s) = 4.882614124166484E - 004 ********************************* ************************************** Inputs: 487.4 = oc partitioning coefficient 1.480 = water column half Life 25.00 = reference temp for water column degradation 2.160 = benthic Half Life 25.00 = Reference temp for b enthic degradation 2.000 = Q ten value 54.70 = photolysis half life 40.00 = reference latitude for photolysis study 0.000 = hydrolysis half life 408.4 = molecular wt 0.2550E - 07 = vapor pressure 0.6100 = solubility 0.1000E+06 = field area 0.1000E+05 = water body area

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2.000 = initial depth 2.000 = maximum depth 2 1=vvwm, 2=usepa pond, 3 = usepa reservoir, 4 = const vol no flow , 5 = const vol w/flow F T = burial, else no burial 0.1000 E - 07 = mass transfer coefficient 0.5000 = PRBEN 0.5000E - 01 = benthic compartment depth 0.5000 = benthic porosity 1.350 = benthic bulk density 0.4000E - 01 = OC frcation in benthic sediment 5.000 = DOC in benthic compartment 0.6000E - 02 = benthic biomass 1.190 = DFAC 30.00 = SS 0.5000E - 02 = chlorophyll 0.4000E - 01 = OC frcation in water column SS 5.000 = DOC in water column 0.4000 = biomass in water column FRACTION AREA CROPPED = 1.000000000000 00

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**APPENDIX 2**  **. Output from T**  **- REX Model for Trifloxystrobin**  

## Upper Bound Kenaga Residues For RQ Calculation **Chemical Name: Trifloxystrobin** 

**Use Dry Peas, chickpeas, and** 

**lentils Formulation**  **Al l products**  **Ap plication Rate**  **0.12 lbs**  **a.i./acre**

**Half -**  **life 35**  **days Ap**  **plication Interval 10**  **days Ma**  **ximum # A pps./Year**  **2 Length of Simulation**  **1 year**  **Variable application rates? no**  

## Endpoints



# Avi **an Ma**  **llard duck LD50 (mg/kg**  **- bw)**  **2000.00 Bobwhite quail**  **LC50 (mg/kg -**  **diet) 5050.00**  **Bobwhite quail NOA**  **EL(mg/kg -**  **bw) 0.00** 

**Bobwhite quail NOA**  **EC (mg/kg -**  **diet) 320.00**  

# Mammals **LD50 (mg/kg -**  **bw) 5000.00**  **LC50 (mg/kg -**  **diet) 0.00**  **NOA EL (mg/kg**  **- bw)**  **75.00 NOA**  **EC (mg/kg -**  **diet) 1500.00**  

# Dietar**y -**  **based EECs (ppm)**  **Kenaga Values**  **Short Grass 52.43**  **Tall Grass 24.03**  **Broadleaf plants 29.49**  **Fruits/pods/seeds 3.28**  **Arthropods 20.53** 

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# Avi **an Results Av**  **ian Body**  **Ingestion (Fdry)**  **Ingestion**

**(Fwet) % body wgt**  **FI Class**  **Weight (g) (g bw/day)**  **(g/day) consumed**  **(kg -**  **diet/day) Small**  **20 5**  **23 114**  **2.28E -**  **02 Mi**  **d 100**  **13 65**  **65 6.49E**  **- 02**  **Large 1000**  **58 291**  **29 2.91E**  **- 01**  **20 5**  **5 25**  **5.06E -**  **03 Granivores**  **100 13**  **14 14**  **1.44E -**  **02 1000**  **58 65**  **6 6.46E**  **- 02**  **Av ian Body**  **Ad justed LD50**  **Weight (g) (mg/kg**  **- bw)**  **20 1038.45**  **100 1322.00**  **1000 1867.37**  

# Dose **- based EECs**  **(mg/kg -**  **bw) Av**  **ian Classes and Body Weights (grams) small**  **mid large**  **20 100**  **1000 Short Grass**  **59.71 34.05**  **15.24 Tall Grass**  **27.37 15.61**  **6.99 Broadleaf plants**  **33.59 19.15**  **8.57 Fruits/pods**  **3.73 2.13**  **0.95 Arthropods**  **23.39 13.34**  **5.97 Seeds**  **0.83 0.47**  **0.21** 

# Dose **- based RQs**  **(Dose -**  **based EEC/adjusted LD50) Avian**  **Ac ute RQs**  **Size Class (grams) 20**  **100 1000**  **Short Grass 0.06**  **0.03 0.01**  **Tall Grass 0.03**  **0.01 0.00**  **Broadleaf plants 0.03**  **0.01 0.00**  **Fruits/pods 0.00**  **0.00 0.00**  **Arthropods 0.02**  **0.01 0.00**  **Seeds 0.00**  **0.00 0.00** 

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# Dietary **- based RQs**  **(Dietary -**  **based EEC/LC50 or NOA EC)**  **RQs Acute**  **Chronic Short Grass**  **0.01 0.16**  **Tall Grass 0.00**  **0.08 Broadleaf plants**  **0.01 0.09**  **Fruits/pods/seeds 0.00**  **0.01 Arthropods**  **0.00 0.06**  Note: To provide risk management with the maximum possible information, it is recommended that both the dose - based and concentration - based RQs be calculated when data are available 

# Mammalian Results **Ma mmalian**  **Body Ingestion**  **(Fdry) Ingestion** 

**(Fwet) %**  **body wgt FI**  **Class Weight**  **(g bwt/day) (g/day)**  **consumed (kg**  **- diet/day)**  **15 3**  **14 95**  **1.43E -**  **02 Herbivores/**  **35 5**  **23 66**  **2.31E -**  **02 insectivores**  **1000 31**  **153 15**  **1.53E -**  **01 15**  **3 3**  **21 3.18E**  **- 03**  **Grainvores 35**  **5 5**  **15 5.13E**  **- 03**  **1000 31**  **34 3**  **3.40E -**  **02 Ma**  **mmalian Body**  **Ad justed**  **Ad justed**  **Class Weight**  **LD50 NOA**  **EL 15**  **10989.15 164.84**  **Herbivores/ 35**  **8891.40 133.37**  **insectivores 1000**  **3845.80 57.69**  **15 10989.15**  **164.84 Granivores**  **35 8891.40**  **133.37 1000**  **3845.80 57.69** 

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# Dose **- Based EECs**  **(mg/kg -**  **bw) Ma**  **mmalian Classes and Body weight**  **(grams) 15**  **35 1000**  **Short Grass 49.98**  **34.55 8.01**  **Tall Grass 22.91**  **15.83 3.67**  **Broadleaf plants 28.12**  **19.43 4.51**  **Fruits/pods 3.12**  **2.16 0.50**  **Arthropods 19.58**  **13.53 3.14**  **Seeds 0.69**  **0.48 0.11**  

# Dose **- based**  **RQs (Dose**  **- based**  **EEC/LD50 or NOA EL)**  **Small mammal Me**  **dium mammal Large mammal**  **15 grams**  **35 grams**  **1000 grams**  **Acute Chronic**  **Acute Chronic**  **Acute Chronic**  **Short Grass 0.00**  **0.30 0.00**  **0.26 0.00**  **0.14 Tall Grass**  **0.00 0.14**  **0.00 0.12**  **0.00 0.06**  **Broadleaf plants 0.00**  **0.17 0.00**  **0.15 0.00**  **0.08 Fruits/pods**  **0.00 0.02**  **0.00 0.02**  **0.00 0.01**  **Arthropods 0.00**  **0.12 0.00**  **0.10 0.00**  **0.05 Seeds**  **0.00 0.00**  **0.00 0.00**  **0.00 0.00**  

# Dietary **- based RQs**  **(Dietary -**  **based EEC/LC50 or NOA EC)**  **Ma mmal RQs**  **Acute Chronic**  **Short Grass #DIV/0!**  **0.03 Tall Grass**  **#DIV/0! 0.02**  **Broadleaf plants #DIV/0!**  **0.02 Fruits/pods/seeds**  **#DIV/0! 0.00**  **Arthropods #DIV/0!**  **0.01** Note: To provide risk management with the maximum possible information, it is recommended that both the dose - based and concentration - based RQs be calculated when data are available

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**APPENDIX 3**  **. Output from TERRPLANT Model**  **for Trifloxystrobin TerrPlant v. 1.2.2**  **Table 1. Chemical Identity. Chemical Name**  **Trifloxystrobin PC code**  **129112 Use**  **Chickpeas, lentils, and dry peas Ap**  **plication Method Aerial**  **Ap plication Form**  **Spray Solubility in Water**  **(ppm) 0.61**  **Table 2. Input parameters used to derive EECs. Input Parameter**  **Symbol Value**  **Units** Application Rate A **0.12 lb ai/A**  Incorporation I **1** none Runoff Fraction R **0.01** none Drift Fraction D **0.05** none **Table 3. EECs for Trifloxystrobin. Units in lb ai/A**  **.**

**Description Equation**  **EEC** Runoff to dry areas (A/I)*R 0.0012 Runoff to semi - aquatic areas (A/I)*R*10 0.012 **Spray drift** **A*D** **0.006 Total for dry areas**  **((A** **/I)*R)+(** **A*D)** **0.0072 Total for semi**  **- aquatic**  **areas ((A**  **/I)*R*10)+(** **A*D)** **0.018 Table 4. Plant survival and growth data used for RQ derivation. Units are in lb ai/A**  **. Seedling Emergence**  **Vegetative Vigor Plant type**  **EC 25**  **NOA EC**  **EC 25**  **NOA EC**  Monocot **0.25 x**  **0.25 x**  Dicot **0.25 x**  **0.25 x**  **Table 5. RQ values for plants in dry and semi -**  **aquatic areas exposed to Trifloxystrobin through runoff and/or spray drift.** * **Plant Type Listed Status**  **Dry Semi**  **- Aq**  **uatic Spray Drift**  Monocot non - listed <0.1 <0.1 <0.1 Monocot listed #VALUE! #VALUE! #DIV/0! Dicot non - listed <0.1 <0.1 <0.1 Dicot listed #VALUE! #VALUE! #DIV/0! *If RQ > 1.0, the LOC is exceeded, resulting in potential for risk to that plant group.