I. EXECUTIVE SUMMARY

EFED has completed a risk assessment for picoxystrobin on March 8, 2012. Initially, a maximum annual rate of 0.78 lb a.i./A was proposed for picoxystrobin use on sweet corn with maximum annual rates of 0.585, 0.39, and 0.195 lb a.i./A proposed for all other uses. Fixed application rates and reapplication intervals were assumed for all proposed uses. It was initially concluded that the use of picoxystrobin would cause potential adverse effects to fish, aquatic- phase amphibians, invertebrates, mammals and aquatic non-vascular plants (algae/diatoms) based on the proposed uses for picoxystrobin. Results of the risk estimation indicate terrestrial monocots and dicots and aquatic vascular plants (duckweed) were not affected and uncertain for birds, terrestrial-phase amphibians and reptiles.

However, the registrant of pixcoxystrobin (Du Pont de Nemours & Co.) has submitted a revised label (EPA Reg. No. 352-IUN) with variable rates and intervals for corn and cereal grain uses. The initial maximum annual rate of 0.78 lb a.i./A for sweet corn was reduced to 0.585 lb a.i./A in the revised labels, clarifying the corn early season application to be a single 3-4 oz applied between the V4 and V7 growth stages; any subsequent application at the 6-12 oz rate to be made between VT and R3 growth stages. Similarly for cereal grains; an early single application (between tillering through jointing) in addition to any subsequent application (at 6-12 oz rate to be made at Feeke’s 9 and no later than the beginning of flowering (Feeke’s 10.5)). This revised risk assessment is addressing these changes in label directions.

The revised risk conclusions were basically unchanged even though the revised RQs were slightly lower than in the original risk assessment. The only change was that the LOC for acute risk to non-listed freshwater invertebrates is no longer exceeded yet the potential risk to freshwater invertebrates still exists.

I.1. Nature of Chemical Stressor

DuPont™ is seeking registration for the new chemical fungicide picoxystrobin (trade name: APROACH fungicide); Methyl (2E)-3-methoxy-2-{2-[6-(trifluoromethyl)-2- pyridyloxymethyl]phenyl}acrylate; CAS#: 117428-22-5; PC code: 129200). Picoxystrobin is a broad spectrum fungicide from the strobilurin group. Picoxystrobin is proposed for use on a variety of food crops, including cereal grains (except rice), sorghum, soybean, field corn, corn seed, popcorn, sweet corn, canola, legume vegetables, dried shelled beans, and peas. It has systemic, and translaminar properties. Picoxystrobin and other strobilurin analogues inhibit fungal respiration. The picoxystrobin molecule contains a ß-methoxyacrylate moiety, which is common to the naturally occurring strobilurins and is responsible for the binding of picoxystrobin to the bc1 segment of the electron transport chain. This binding causes interference with electron flow at the cytochrome bc1 complex. Picoxystrobin is currently registered in some 28 countries, including: Argentina, Austria, Belgium, Brazil, Colombia, Czech Republic, Denmark, Estonia, Finland, France, Germany, Hungary, Ireland, Kenya, Latvia, Lithuania, the Netherlands, New Zealand, Norway, Poland, Romania, Slovakia, South Africa, Sweden and the UK. Registration is in progress in the US, Italy and Portugal1.

1 I.2. Potential Risks to Non-target Animals, Organisms, and Plants

Picoxystrobin is proposed for use on a variety of food crops, including cereal grains (except rice), sorghum, soybean, field corn, corn seed, popcorn, sweet corn, canola, legume vegetables, dried shelled beans, and peas. Thus, the ecosystems at risk may be extensive in scope. In general terms, terrestrial ecosystems potentially at risk due to the use of picoxystrobin, could include the treated field and areas immediately adjacent to the treated field that 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. Aquatic ecosystems potentially at risk due to the use of picoxystrobin include water bodies adjacent to, or downstream from, the treated field and might include impounded bodies such as ponds, lakes and reservoirs, or flowing waterways such as streams or rivers. For uses in coastal areas, aquatic habitat also includes marine ecosystems, including estuaries.

The proposed fungicide uses of picoxystrobin have the potential to cause adverse effects to survival of freshwater fish and aquatic-phase amphibians, freshwater and estuarine/marine invertebrates, algae and diatoms after acute exposures. There is potential for reproductive effects in freshwater and estuarine/marine invertebrates and mammals (including non-listed and listed species) when exposed to picoxystrobin on a chronic basis. Risks to seedlings and young plants inhabiting semi-aquatic and terrestrial habitats are not expected, including aquatic vascular plants inhabiting waterbodies. No precautionary label language is needed for bees. There is also a potential for indirect effects to species that depend upon taxonomic groups directly at risk when exposed to picoxystrobin.

There is an uncertainty in the risk assessment for potential acute risk to birds. Ecological toxicity tests with Northern bobwhite quail via the oral and dietary routes and with mallard duck via the dietary route indicate no mortality, sub-lethal effects, or clinical signs of toxicity occurred at the maximum concentration tested; acute risk to bobwhite quail and mallard duck from picoxystrobin uses can be expected to be minimal. However, there was 15% mortality and more than 50% frank sub-lethal effects of lethargy, ruffled appearance, prostrate posture and loss of righting reflex observed with zebra finch (a passerine species). Regurgitation in the passerines was observed at several of the oral doses tested where mortality and sub-lethal effects occurred, confounding the results of the study since the actual dose received by the bird that has regurgitated the test substance cannot be determined. In addition, the use of a screening-level endpoint of 486 mg a.i/kg-bw for passerines where no effects (e.g., regurgitation, mortality, and sub-lethal effects) were observed combined with predicted terrestrial EECs using the T-REX model results in an RQ that exceeds the level of concern (LOC) for acute risk to listed species. In the absence of a definitive LD50 value due to regurgitation, the frank sub-lethal effects in >50% of the tested birds, and the screening-level endpoint used that results in a LOC exceedance; the potential effects to passerines is uncertain since acceptable data with the bobwhite quail and mallard indicate minimal effects. A new study with passerines is requested to address the uncertainty. Therefore, until a definitive endpoint for acute oral exposure is available, it is uncertain whether the risks to birds from the use of picoxystrobin are expected or not. Also, because birds are surrogates for terrestrial-phase amphibians and reptiles, the risk to these taxonomic groups is assumed. Submission of the data will help determine whether there is or is not a potential for adverse effects on the survival of the passerines. The data requested is as

2 follows:

• OSCPP Guideline 850.2100: Avian Acute Oral Toxicity Test (with a passerine bird if regurgitation does not occur up to or greater than 1400 mg a.i./kg bw) or • OSCPP Guideline 850.2200: Avian Subacute Dietary Toxicity Test (a modified protocol with a passerine bird to closely document food consumption and calculation of an oral LD50 value)

While the assessment suggest that picoxystrobin does not bioaccumulate in benthic invertebrates; picoxystrobin has chemical characteristics consistent with other chemicals that have a propensity to sorb onto particles (e.g., log Kow = 3.6) plus supplemental data indicate picoxystrobin has the potential to binds to sediment, there is an exposure concern for benthic invertebrates. Thus, until data are available to address the uncertainty, risks to sediment-dwelling invertebrates from the use of picoxystrobin will be assumed. The data requested are as follow:

• Test Method 100.4: Hyalella azteca 42-d Test for Measuring the Effects of Sediment-associated Contaminants on Survival, Growth, and Reproduction in USEPA 2000 Methods for Measuring the Toxicity and Bioaccumulation of Sediment-associated contaminants with Freshwater Invertebrates EPA 600/R- 99/064 (OSCPP 850.1770, in prep.); • Test Method 100.5: Life-cycle Test for Measuring the Effects of Sediment- associated Contaminants on Chironomus dilates (formerly known as C. tentans) in USEPA 2000 Methods for Measuring the Toxicity and bioaccumulation of Sediment-associated Contaminants with Freshwater Invertebrates EPA 600/R- 99/064 (OSCPP 850.1760, in prep.); and • Leptocheirus plumulosus in USEPA 2001 Method for Assessing the Chronic toxicity of Marine and Estuarine Sediment-associated Contaminants with the Amphipod Leptocheirus plumulosus EPA 600/R-01/020 (OCSPP 850.1780, in prep.)

Tables I.1 and I.2 provides summaries for the environmental risk conclusions for aquatic and terrestrial animals and plants.

3 Table I.1. Summary of Environmental Risk Conclusions for Aquatic Organisms and Plants.

Assessment Endpoint Use Patterns with LOC Summarized Risk Characterization Exceedances

Acute Risk to Freshwater Use on sorghum and soybean, Acute LOCs Exceeded: Restricted Use and Listed Species. Fish and Aquatic-phase sweet corn, field corn, popcorn Using the peak EECs from the MS soybean and MS corn scenarios, Amphibians and seed there are exceedances of the acute restricted use and acute listed species LOCs for listed freshwater fish and aquatic-phase amphibians following the proposed labeled use of picoxystrobin on sorghum, soybean, sweet corn, field corn, popcorn and seed. The highest RQ of 0.1 for freshwater fish including aquatic-phase amphibians is 2x higher than and borders the acute listed species and the restricted use LOC thresholds of 0.05 and 0.1, respectively.

Acute LOC Exceeded: Listed Species. Using the peak EECs Use on cereal grain, excluding from the MI bean and ND wheat scenarios, there is an exceedance rice, canola, legume vegetables, of the acute listed species LOC for listed freshwater fish and dried shelled beans, and pea aquatic-phase amphibians following the proposed labeled use of (aerial application only) picoxystrobin via aerial application on canola, legume vegetables, dried shelled beans, and peas. The highest RQ of 0.06 for freshwater fish including aquatic-phase amphibians is marginally higher than the acute listed species LOC threshold of 0.05. However, there are no LOC exceedances as a result of ground applications; the RQ is 0.04, which is slightly below the LOC of 0.05 for potential acute exposures to listed freshwater fish and aquatic-phase amphibians.

Acute Risk to None No acute LOC exceedances for non-listed and listed Estuarine/marine Fish estuarine/marine fish following picoxystrobin applications. Highest acute RQ = 0.03. A comparison of the peak EECs from scenarios modeled to the toxicity value for sheepshead minnow to assess acute risk to estuarine/marine fish indicates that the toxicity value [330 µg/L] average 37x to 116x higher than the highest EECs for all proposed uses.

Chronic Risk to None No chronic LOC exceedance for non-listed and listed fish and Freshwater Fish, aquatic-phase amphibians following picoxystrobin applications. Aquatic-phase Highest RQ = 0.27. A comparison of the 60-day EECs in surface Amphibians and water to the chronic toxicity value using the lowest fish NOAEC to Marine/Estuarine Fish assess chronic risk to fish indicates that the highest EECs from the scenarios modeled are 4x to 12x lower than the lowest toxicity value for fish (sheepshead minnow NOAEC of 21 µg/L).

Acute Risk to Freshwater All Proposed Uses Acute LOCs Exceeded: Restricted Use and Listed Species. Invertebrates Using the peak EECs from the exposure scenarios modeled, the RQs of 0.1 – 0.4 all exceed the acute restricted use and acute listed species LOCs for listed freshwater invertebrates following picoxystrobin uses. The lowest and highest RQ of 0.1 and 0.4, respectively, for freshwater invertebrates is 2x and 8x higher than, respectively, the acute listed species LOC threshold of 0.05.

4 Table I.1. Summary of Environmental Risk Conclusions for Aquatic Organisms and Plants.

Assessment Endpoint Use Patterns with LOC Summarized Risk Characterization Exceedances

Acute Risk to All Proposed Uses Acute LOCs Exceeded: Acute Risk, Restricted Use and Listed Estuarine/Marine Species. Using the peak EECs from the exposure scenarios Invertebrates modeled, the RQs of 0.5 – 1.6 all exceed the acute risk, acute restricted use and acute listed species LOCs for non-listed and listed freshwater invertebrates following picoxystrobin uses. The lowest and highest RQ of 0.5 and 1.6 for freshwater invertebrates is 10x and 32x higher than, respectively, the acute listed species LOC threshold of 0.05.

Chronic Risk to All Proposed Uses Chronic LOC Exceeded: Chronic and Listed Species. Using 21- Freshwater Invertebrates day EECs from the exposure scenarios modeled, the RQs of 2.3-7.3 all exceed the chronic risk LOC for non-listed and listed freshwater invertebrates following picoxystrobin uses. The RQs all exceed the chronic risk LOC threshold of 1.0 for potential chronic exposure to listed and non-listed freshwater invertebrates.

Chronic Risk to Use on sorghum, soybean, Chronic LOC Exceeded: Chronic and Listed Species. Using 21- Estuarine/Marine sweet corn, field corn, seed, day EECs from the exposure scenarios modeled for soybean and Invertebrates popcorn corn, the RQs of 1.9-2.0 exceed the chronic risk LOC of 1 for non- listed and listed estuarine/marine invertebrates following

picoxystrobin uses on sorghum, soybean, sweet corn, field corn,

seed, and popcorn.

For picoxystrobin uses on canola, legume vegetables, dried shelled bean, cereal grains (excluding rice) and pea, the estuarine/marine invertebrates RQs of 0.6 – 0.9 do not exceed the chronic risk LOC of 1.0.

Acute Risk to Benthic All Proposed Uses Acute LOCs Exceeded: Acute Risk, Restricted Use and Listed Invertebrates Species. Using the peak sediment porewater EEC, there is an exceedance of the acute non-listed and listed species LOC for benthic invertebrates. In order to assess the potential risk to soil- dwelling invertebrates, the most sensitive endpoint derived from the available EPA-guideline studies for invertebrate species (Eastern oyster and daphnid) were compared to PRZM sediment porewater EECs. In this exercise, the most sensitive acute endpoints (5.7 µg a.i./L, Eastern oyster; 24 µg a.i./L, daphnid) were compared to peak sediment porewater EEC (3.70 µg a.i./L). Given that the peak EEC result in an acute RQ of 0.65 (oyster) and 0.15 (daphnid), the acute listed species LOC of 0.05 is exceeded for both species and the acute non-listed species LOC of 0.5 is exceeded for the most sensitive acute endpoint (oyster), there is a risk concern for acute exposure to listed and non-listed soil- dwelling invertebrates.

5 Table I.1. Summary of Environmental Risk Conclusions for Aquatic Organisms and Plants.

Assessment Endpoint Use Patterns with LOC Summarized Risk Characterization Exceedances

Chronic Risk to Benthic Assumed for all proposed uses Laboratory data and the chemical characteristics indicate that Invertebrates benthic invertebrates may be exposed to picoxystrobin uses. Based on calculations in this assessment where estimated sediment concentrations were calculated, the 21-day sediment porewater EEC predicted for picoxystrobin was compared to daphnid and mysid chronic toxicity endpoints. This 21-day sediment EEC and toxicity comparison result in a chronic RQ of 3.7 (daphnid) and 1.02 (mysid), which exceeds the chronic LOC of 1.0, which satisfies one of the criteria for requiring whole sediment toxicity testing under 40 CFR Part 158. Submitted soil metabolism and aquatic metabolism studies indicate picoxystrobin is moderately persistence (aerobic soil t1/2: 29.4 – 73.7 days; aerobic aquatic metabolism t1/2: 39.2 – 47.5 days; anaerobic aquatic metabolism t1/2: 83.5 days). These half-life values are greater than 40 CFR Part 158 criterion of 10 days. The third set of trigger criteria for requiring chronic testing (Kd >50 or log Kow >3 or Koc >1000) is also met for picoxystrobin (log Kow is 3.6 and Koc values range from 741 to 1089). The physicochemical property triggers (log Kow and Koc) reflect the propensity of the chemical to partition onto the particulate or organic matter phases of sediment. Exceeding any one of the physicochemical property triggers listed above is sufficient for indicating the pesticide has reasonable potential for partitioning to the sediment compartment. The absence of these studies introduces uncertainty as to the effects of picoxystrobin on sediment-dwelling invertebrates. In addition, picoxystrobin has the potential to enter estuarine/marine water bodies based on current usage patterns (sweet and field corn, wheat, barley, sorghum, and soybeans) that include coastal counties. Until data on both freshwater and estuarine/marine soil-dwelling species are available to address the uncertainty, the chronic risks to benthic invertebrates are assumed. Risk to Aquatic Vascular None At the peak surface water EECs, there is no exceedance of the non- Plants listed or listed plant LOCs for aquatic vascular plants following picoxystrobin applied aerially or with ground equipments. A comparison of the peak EECs in surface water to the toxicity values for duckweed to assess risk to non-listed and listed vascular plants indicates that the toxicity values [ranging from 20 to 210 µg/L] average 2x to 24x higher than the highest EECs modeled.

6 Table I.1. Summary of Environmental Risk Conclusions for Aquatic Organisms and Plants.

Assessment Endpoint Use Patterns with LOC Summarized Risk Characterization Exceedances

Risk to Aquatic Non- Use on sorghum, soybean, Plant LOC Exceeded: Non-listed and Listed. There are vascular Plants sweet corn, field corn, seed, exceedances of the non-listed and listed plant LOCs for non- popcorn vascular aquatic plants following the proposed labeled use of picoxystrobin on soybean, sorghum, sweet corn, field corn, seed, popcorn. The highest RQs of 2.2 and 3.9 exceeded the LOC of 1 for potential risk to non-listed and listed non-vascular aquatic plants, respectively, from both aerial and ground applications.

Use on canola, legume Plant LOC Exceeded: Listed. There is an exceedance of the listed vegetables, dried shelled bean, plant LOC for non-vascular aquatic plants. The RQs of 1.2-1.6 cereal grains (excluding rice) exceed the LOC of 1 for potential risk to listed non-vascular and pea aquatic plants adjacent to canola, legume vegetables, bean, cereal grain, and pea sites treated with picoxystrobin from aerial and ground applications. No exceedances for non-listed plants, the highest RQs were 0.7 and 0.9 for ground and aerial applications, respectively.

7

Table I.2. Summary of Environmental Risk Conclusions for Terrestrial Animals and Plants Risk Conclusion Use Patterns with LOC Summarized Risk Characterization Exceedances

Acute Risk to all Birds Assumed for all proposed uses In assessing the potential acute risk to birds, the lowest avian and smaller Passerines toxicity value of 486 mg a.i./kg-bw was compared to the highest

Species (including EEC of 140 mg a.i./kg (maximum dose-based residue on short terrestrial-phase grass following applications on soybean and sorghum). In this amphibians and reptiles) exercise, the endpoint was greater than 0.1 of the acute ratio (acute listed species LOC = 0.1) for potential risk to 20 g and 100 g birds consuming short grass and 20 g birds consuming tall grass, broadleaf plants and arthropods. Since the lowest screening-level endpoint resulted in LOC exceedances, >50% frank sub-lethal effects occurred, and one incident report of probable azoxystrobin (a strobilurin) effects on a bald eagle (Incident No. I018723-002) indicate that there is a potential risk for adverse effects on survival in addition to sub-lethal effects of ecological significance to passerines from the use of this pesticide. Therefore, the risk to all federally listed birds including the smaller, passerine, species and terrestrial-phase amphibians and reptiles from the use of picoxystrobin cannot be precluded until the uncertainty is addressed. In order to fully evaluate the potential risk to all birds including passerines, additional data are needed on either an avian acute oral study with a passerine species if regurgitation does not occur up to or greater than 1400 mg a.i./kg or 0.1 of the highest EEC (140 mg a.i./kg) or an avian subacute dietary study with a modified protocol for passerines where food consumption is monitored closely to generate an LD50, in addition to an LC50. In the absence of such data, risks to all listed birds including passerines and terrestrial-phase amphibians and reptiles will be assumed.

Chronic Risk to Birds None Using the dietary-based NOAEC and Kenaga EECs, the chronic (including terrestrial- risk LOC is not exceeded for potential chronic exposure to birds phase amphibians and consuming any of the selected feed items modeled at the maximum reptiles) application rate and maximum predicted residues following picoxystrobin applications applied aerially or with ground equipments. Highest RQ = 0.78 for a 20 gram bird consuming short grass. Given that the 20 g bird is considered the most vulnerable, the potential for risk to birds from acute exposure appears to be minimal. Acute Risk to Mammals None Acute RQs were not calculated because effects were not observed at the maximum level tested. A comparison of the EEC for a 15 gram mammal consuming short grass and the non-definitive endpoint (>5000 mg a.i./kg bw) as an acute screening-level endpoint indicates the RQ of 0.01 is a quarter of the acute listed species LOC threshold of 0.1. Given that the 15 g mammal is considered the most vulnerable, the potential for risk to mammals from acute exposure appears to be minimal.

8 Table I.2. Summary of Environmental Risk Conclusions for Terrestrial Animals and Plants Risk Conclusion Use Patterns with LOC Summarized Risk Characterization Exceedances

Chronic Risk to Mammals All proposed uses Following picoxystrobin applications on the proposed uses and maximum predicted residue levels, the dose-based RQs exceeded

the chronic risk LOC of 1.0 for all weight classes of mammals (15, 35, 1000 g) consuming short grasses, tall grasses, broadleaf forage and arthropods; the dose-based RQs ranged from 1.3 to 10. Using the maximum EECs and the proposed uses except canola, dried shelled bean and peas, the dietary-based RQs of 1.03 to 2.5 also exceeded the chronic risk LOC for mammals consuming the selected feed items except for fruits/pods/seeds and arthropods. No chronic LOC exceedance for mammals consuming fruit, pods, seeds, highest dose-based and dietary-based RQs were 0.6 and 0.2, respectively; and no dietary-based exceedance for mammals consuming arthropods, the highest RQ was 0.96.

Risk to Bees None likely Low toxicity to bees. Qualitative assessment indicates probable low risk.

Risk to Terrestrial Plants None Using the TERRPLANT dry and semi-aquatic EECs, there no LOC exceedances for non-listed and listed monocots and dicots located in adjacent areas and in semi-aquatic areas. Highest RQs all <0.1 for aerial and ground applications following two, three, and four applications of picoxystrobin.

Acute and Chronic Risks None Using the estimated soil EEC and the toxicity values for earthworm to Soil-dwelling to assess potential acute and chronic exposures to soil-dwelling Invertebrates invertebrates following a single application at the maximum application rate indicate no LOC exceedances. The RQs of 0.02 and 0.04 were below the acute listed species and chronic risk LOC thresholds of 0.05 and 1.0, respectively.

Based on estimated maximum application rates, exposure levels and available effects data, picoxystrobin used as a fungicide for control of foliar and soil-borne plant diseases (including brown rust, tan spot, powdery mildew and net blotch) indicates direct effects LOC exceedances those taxa idenitified above from the proposed uses. Such findings suggest a potential concern for indirect effects to listed animal and plant species with both narrow (i.e., species that are obligates or have very specific habitat or feeding requirements) and general dependencies (i.e., cover type requirements) as a resource or important habitat component. Therefore, there is a potential for indirect effects to all animal and plant taxonomic groups (i.e., mammal, bird, amphibian, reptile, fish, crustacean, mollusks, and gastropods) that depend on those freshwater fish, aquatic-phase amphibians, freshwater, estuarine/marine, and benthic invertebrates, algae and diatoms, and mammals as food resources to survive, grow, and reproduce and are presented in Table I.3.

9 Table I.3. Listed Taxonomic Groups Potentially at Risks Due to Direct or Indirect Effects as a Result of the Proposed Uses of Picoxystrobin. Listed Taxon Direct Effects from Direct Effects from Indirect Effects a Acute Exposures Chronic Exposures

Aquatic Aquatic non-vascular plants Yes N/A Yes Aquatic vascular plants No N/A Yes Freshwater invertebrates Yes Yes Yes Marine/estuarine invertebrates Yes Yes Yes Benthic invertebrates Yes Cannot be precluded1 Yes Freshwater fish Yes No Yes Marine/estuarine fish No No Yes Aquatic-phase amphibians Yes No Yes Terrestrial Semi-aquatic plants - monocots No N/A Yes Semi-aquatic plants - dicots No N/A Yes Terrestrial plants – monocots No N/A Yes Terrestrial plants - dicots No N/A Yes Bees No N/A Yes Soil-dwelling invertebrates No No Yes Birds Cannot be precluded2 No Yes Terrestrial-phase amphibians Cannot be precluded3 No Yes Reptiles Cannot be precluded3 No Yes Mammals No Yes Yes N/A - indicates that this exposure route is not assessed. a Until an endangered species assessment is complete, indirect effects to all species cannot be precluded 1 Screening-level risk assessment indicates concern for potential risk to benthic invertebrates from chronic exposure; until additional data are available to address the uncertainty, the risk is assumed. 2 Screening-level risk assessment indicates concern for potential risk to passerines from acute exposure; until additional data are available to address the uncertainty, the risk is assumed. 3 Birds are surrogates for terrestrial-phase amphibians and reptiles. Since the risk to bird from picoxystrobin use is assumed, the risk is assumed for terrestrial-phase amphibians and reptiles until additional data discount the risk.

I.3. Conclusions - Exposure Characterization

Picoxystrobin is moderately persistent in aerobic and anaerobic conditions, and is moderately mobile. Picoxystrobin is moderately persistent in soil with half-lives ranging from 29 to 73 days in aerobic soil. Picoxystrobin degraded under the conditions of aerobic aquatic metabolism with half-lives ranging from 39 to 41 days; and under anaerobic aquatic systems with a half-life of 83 days. There is no evidence of degradation via hydrolysis, which was studied across environmental pHs. Picoxystrobin is moderately mobile to mobile with reported organic carbon partitioning coefficients (Koc) ranging from 741 to 1089 L/kg-oc. The primary route of

10 degradation is via aqueous photolysis (half-life of 16 days); however photolysis may only play a significant role in shallow clear waters. Under other conditions, aerobic biometabolism is expected to be the primary route of degradation. Major degradates of picoxystrobin (constituting greater than 10% of the applied radiation from environmental fate studies, or of toxicological concern) include: Compound 2 (IN-QDY62 R403092), Compound 3 (IN-QDK50 R403814), Compound 4, Compound 7 (IN-QFA35), Compound 12, Compound 8 (IN-QDY63), and CO2

I.4. Conclusions - Effects Characterization

Aquatic Organisms

Results of acute toxicity studies in freshwater and estuarine/marine fish indicate that picoxystrobin is highly to very highly toxic to fish on an acute exposure basis. Reduced fish embryo hatchling, larval survival and growth were observed in the F1 generation of the available early life-stage (ELS) study with freshwater fish. Acute toxicity studies indicate that picoxystrobin is very highly toxic to freshwater and estuarine/marine invertebrates on an acute exposure basis. Dose-dependent sublethal effects observed in fish and aquatic invertebrate studies included loss of equilibrium, lethargy, quiescence, sounding, dark discoloration, and lying on bottom at doses equal to or less toxic than the dose observed for mortality and immobilization. Picoxystrobin has effects on aquatic vascular and nonvascular plants, with biomass and cell density being adversely affected.

Degradate toxicity data on fish, aquatic invertebrates and green algae indicate that picoxystrobin degradates are less toxic than the parent and effects are not expected at environmentally relevant concentrations.

Terrestrial Organisms

Picoxystrobin is practically non-toxic to laboratory rat (Sprague-Dawley) on an acute exposure basis. Two-generation studies on reproduction and fertility in the rat showed picoxystrobin to cause chronic toxicity effects in the parents and F1 and F2 generations that would impact adult body weights, body weight gains, pup body weights/litter, organ weights and food consumptions.

Studies of acute oral (dose-based) toxicity in bobwhite quail (Colinus virginianus) indicated that picoxystrobin is practically nontoxic to upland game birds while the toxicity to zebra finch (Poephila guttata), a passerine, is uncertain due to regurgitation and frank sub-lethal effects observed that a definitive LD50 could not be obtained when administered as a single oral dose. Two subacute dietary toxicity studies indicate that picoxystrobin TGAI is practically nontoxic to mallard duck and bobwhite quail on a subacute dietary exposure basis. For chronic effects, there were treatment-related effects on the % egg set of egg laid in the reproduction toxicity study of picoxystrobin TGAI in mallard duck; no effects were observed in bobwhite quail. No studies of the formulations or the degradates were submitted for birds; all measurement endpoints for avian species are based on technical grade picoxystrobin.

Results of available toxicity studies indicate that picoxystrobin TGAI is practically nontoxic to honey bees (Apis mellifera) on an acute exposure basis.

11

OECD guideline studies with the formulated product, picoxystrobin 250 g/L SC, indicate a direct effect on the mortality and fecundity of parasitoid species (parasitoid wasp A. rhopalosiphi, predatory green lacewing C. carnea, and predatory mite T. pyri) immediately following application; however, when introduced to aged residues over a period of twelve days, there were no direct effect on the population. Based on this information, the parasitoid species may be affected when exposed to picoxystrobin directly but less likely when they move back to the sites treated with picoxystrobin.

There were no significant effects to earthworm’s survivability when exposed to the TGAI; however, a reduction in the number of juveniles was observed. In addition, studies suggest different moisture levels of soil may impact earthworms on the surface.

Degradate toxicity data on earthworm indicate that picoxystrobin degradates are less toxic than the parent and effects are not expected at environmentally relevant concentrations.

Tier I limit studies of the effect of the picoxystrobin formulation Picoxystrobin 250 g/L SC on seed emergence and vegetative vigor in terrestrial plants were submitted, indicating that terrestrial plants are relatively insensitive to picoxystrobin at application rates 2x higher than the maximum per acre application rate for the proposed registration uses. Significant effects of dry weight and phytotoxicity were observed at the limit dose for listed dicots; however, the effects are not expected at environmentally relevant concentrations.

12 Contents I. EXECUTIVE SUMMARY ...... 1 I.1. Nature of Chemical Stressor ...... 1 I.2. Potential Risks to Non-target Animals, Organisms, and Plants ...... 2 I.3. Conclusions - Exposure Characterization ...... 10 I.4. Conclusions - Effects Characterization ...... 11 II. PROBLEM FORMULATION ...... 14 II.1. Nature of Regulatory Action...... 14 II.2. Stressor Source and Distribution ...... 14 II.2.1. Nature of Chemical Stressor ...... 14 II.2.2. Overview of Pesticide Usage ...... 15 II.3. Receptors ...... 15 II.3.1. Aquatic and Terrestrial Effects ...... 15 II.3.2. Ecosystems Potentially at Risk ...... 16 II.4. Assessment Endpoints ...... 17 II.5. Conceptual Model ...... 17 II.5.1. Risk Hypotheses ...... 17 II.5.2. Conceptual Diagram ...... 17 II.6. Analysis Plan ...... 20 II.6.1 Preliminary Identification of Data Gaps ...... 21 II.6.2. Measures of Exposure and Effects ...... 23 III. ANALYSIS ...... 25 III.1. Use Characterization ...... 25 III.2. Exposure Characterization ...... 26 III.2.1. Environmental Fate and Transport Characterization ...... 26 III.2.2. Measures of Aquatic Exposure ...... 31 III.3. Measures of Terrestrial Exposure ...... 35 III.3.1. Terrestrial Wildlife ...... 35 III.3.2. Terrestrial Plants...... 39 III.4. Ecological Effects Characterization ...... 40 III.4.1. Aquatic Effects Characterization ...... 40 III.4.2. Aquatic Plants ...... 48 III.4.3. Terrestrial Effects Characterization ...... 51 III.4.4. Terrestrial Plants ...... 57 IV. RISK CHARACTERIZATION ...... 62 IV.1. Risk Estimation - Integration of Exposure and Effects Data ...... 62 IV.1.1. Non-target Aquatic Animals and Plants ...... 63 IV.1.2. Risk Quotient Calculations for Aquatic Plants ...... 69 IV.1.3. Non-target Terrestrial Animals ...... 71 IV.1.4. Non-target Terrestrial Plants in Terrestrial and Semi-aquatic Environments ...... 77 IV.2. Risk Description ...... 78 IV.2.1. Risks to Aquatic Organisms and Plants ...... 79 IV.2.2. Risks to Terrestrial Animals and Plants ...... 89 V. FEDERALLY THREATENED AND ENDANGERED (LISTED) SPECIES CONCERNS ...... 97 V.1. Action Area ...... 97 V.2. Taxonomic Groups Potentially at Risk ...... 98 V.2.1. Probit Dose-Response Analysis ...... 99 V.2.2. Listed Species Occurrence Associated with Picoxystrobin Use ...... 101

13 II. PROBLEM FORMULATION

The purpose of this problem formulation is to provide the foundation for the environmental fate and ecological risk assessment for the registration of the new chemical picoxystrobin, (DuPont APROACH™ fungicide; Methyl(E)-2-{2-[6-(trifluoromethyl)pyridin-2-yloxymethyl]phenyl}-3- methoxyacrylate; CAS#: 117428-22-5; PC code: 129200). 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 picoxystrobin (USEPA, 1998).

II.1. Nature of Regulatory Action

The U.S. Environmental Protection Agency (EPA or the Agency) is required under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) to ensure that the proposed use of picoxystrobin as a new fungicide does not have the potential to cause unreasonable adverse 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 picoxystrobin is not likely to jeopardize the continued existence of such listed species or adversely modify their critical habitat. In order to meet the requirements of FIFRA 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 (USEPA, 2004).

The end result of the EPA pesticide registration process (i.e., the FIFRA regulatory action) is an approved 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 the new chemical registration of picoxystrobin.

II.2. Stressor Source and Distribution

II.2.1. Nature of Chemical Stressor

DuPont™ is seeking registration for the use of the new chemical fungicide picoxystrobin (APROACH™ fungicide; Methyl(E)-2-{2-[6-(trifluoromethyl)pyridin-2-yloxymethyl]phenyl}- 3-methoxyacrylate).

Picoxystrobin is a broad spectrum fungicide from the strobilurin group. It has systemic, and translaminar properties. Picoxystrobin and other strobilurin analogues inhibit fungal respiration. The picoxystrobin molecule contains a ß-methoxyacrylate moiety, which is common to the naturally occurring strobilurins and is responsible for the binding of picoxystrobin to the bc1 segment of the electron transport chain. This binding causes interference with electron flow at

14 the cytochrome bc1 complex2.

Major degradates of picoxystrobin (constituting greater than 10% of the applied radiation from environmental fate studies, or of toxicological concern) include: Compound 2 (IN-QDY62 R403092), Compound 3 (IN-QDK50 R403814), Compound 4, Compound 7 (IN-QFA35), Compound 12, Compound 8 (IN-QDY63), and CO2 (chemical names, chemical structures, and data on the formation of these degradates are provided in Appendix A). None of these degradates are of toxicological concern.

II.2.2. Overview of Pesticide Usage

DuPont is seeking the registration of picoxystrobin as a new fungicide to control foliar and soil- borne plant diseases (including brown rust, tan spot, powdery mildew and net blotch) on the following proposed uses: Cereal grains (except rice), sorghum, soybean, field corn, corn seed, popcorn, sweet corn, canola, legume vegetables, dried shelled beans, and peas. Picoxystrobin is formulated as a suspension concentrate (picoxystrobin 250 g/L SC) for broadcast foliar application to crops through ground and aircraft spray equipment. Picoxystrobin 250 g/L SC is labeled as APROACHTM for agricultural use. This assessment is based on proposed maximum application rates for all uses. Further characterization of the use is provided in Section III-1.

II.3. Receptors

II.3.1. Aquatic and Terrestrial Effects

The receptor is the biological entity that is exposed to the stressor (USEPA, 1998). Consistent with the process described in the Overview Document (USEPA, 2004), this risk assessment uses a surrogate species approach in its evaluation of picoxystrobin. Toxicity data generated using surrogate test species, which are intended to be representative of broad taxonomic groups, are used to extrapolate to potential effects on a variety of species (receptors) included under these broader taxonomic groupings. Within each of these very broad taxonomic groups, a measure of effect is selected from the available test data.

Table II.1 provides a summary of the taxonomic groups and the surrogate species tested to provide potential acute ecological effects data to non-target animals and plants. In addition, the table provides a preliminary overview of the potential acute toxicity of picoxystrobin by providing the acute toxicity classifications.

15 Table II.1. Test Species Evaluated for Assessing Potential Ecological Effects of Picoxystrobin and the Associated Acute Toxicity Classification Taxonomic Group Example(s) of Surrogate Species Acute Toxicity Classification [Oral] Bobwhite quail (Colinus virginianus) Practically non-toxic [Oral] Zebra finch (Poephila guttata) Uncertain Birds1 [Dietary] Mallard duck (Anas platyrhynchos) All practically non-toxic [Dietary] Bobwhite quail (Colinus virginianus) Mammals Laboratory rat (Rattus norvegicus) Practically non-toxic Beneficial insects Honey bee (Apis mellifera L.) Practically non-toxic Soil-dwelling Earthworm (Eisenia fetida) Not classified invertebrates Bluegill sunfish (Lepomis macrochirus) Rainbow trout (Oncorhynchus mykiss) Very highly toxic to Freshwater fish2 Fathead minnow (Pimephales promelas) highly toxic Mirror Carp (Cyprinus carpio) Three-spined stickleback (Gasterosteus aculeatus) Freshwater Water flea (Daphnia magna) Very highly toxic invertebrates Estuarine/marine fish Sheepshead minnow (Cyprinodon variegatus) Highly toxic Estuarine/marine Eastern Oyster (Crassostrea virginica) All very highly toxic invertebrates Mysid (Americamysis bahia) Chironomids (Chironomus dilutes) Benthic Invertebrates Not classified Amphipods (Hyalella azteca) [Seedling Emergence and Vegetative Vigor] Monocot – Corn, Onion, Ryegrass, Oat Terrestrial plants Not classified [Seedling Emergence and Vegetative Vigor] Dicot – Cucumber, Oilseed rape, Pea, Soybean, Sugar beet, Tomato Vascular – Duckweed (Lemna gibba) Non-Vascular - Green algae (Pseudokirchneriella Aquatic plants and subcapitata), Blue-green algae (Anabaena flos-aquae), Not classified algae Freshwater diatom (Navicula pelliculosa), Marine diatom (Skeletonema costatum) 1Birds represent surrogates for amphibians (terrestrial phase) and reptiles. 2 Freshwater fish may be surrogates for amphibians (aquatic phase).

II.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 that 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.

Aquatic ecosystems potentially at risk include water bodies adjacent to, or downstream from, the use site and might include impounded bodies 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 includes marine ecosystems, including estuaries, embayment’s, and near shore environments.

16 II.4. Assessment Endpoints

Assessment endpoints represent the actual environmental value that is to be protected, defined by an ecological entity (species, community, or other entity) and its attribute or characteristics (USEPA, 1998). For picoxystrobin, the ecological entities include the following: birds, amphibians, reptiles, mammals, freshwater fish and invertebrates, estuarine/marine fish and invertebrates, non-target terrestrial plants, insects, and aquatic vascular and non-vascular plants. The attributes for each of these entities may include growth, survival, and reproduction (Table II.3 in Section II.6.2.2).

II.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 ecological pathway to be complete, it must have a source, a release mechanism, an environmental transport medium, and a feasible route of exposure.

The conceptual model is intended to provide a written description and visual representation of the predicted relationships between picoxystrobin, potential routes of exposure, and the predicted effects for the assessment endpoints. The conceptual model consists of two major components: risk hypotheses and a conceptual diagram (USEPA, 1998).

II.5.1. Risk Hypotheses

Risk hypotheses are specific assumptions about potential adverse effects (i.e., changes in assessment endpoints) and may be based on theory and logic, empirical data, mathematical models, or probability models (EPA, 1998). For this assessment, the risk is stressor-linked, where the stressor is the release of picoxystrobin to the environment. For picoxystrobin, the following generic ecological risk hypothesis s being employed for this baseline risk assessment:

Given the proposed uses of picoxystrobin and its environmental fate properties, there is a likelihood of exposure to non-target terrestrial and aquatic organisms.

When used in accordance with the label, picoxystrobin results in potential adverse effects upon the survival, growth, and reproduction of non-target terrestrial and aquatic organisms.

II.5.2. Conceptual Diagram

The conceptual model is a graphic representation of the predicted relationships between the ecological entities, both listed (threatened and endangered) and non-listed species, and the stressors to which they may be exposed. The conceptual model specifies the potential routes of exposure, biological receptor types, and effects endpoints of potential concern. Picoxystrobin is applied to cereal crops using aerial as well as ground application methods. Spray drift is

17 expected from the proposed label applications. Figure II.1 depicts the stressors, exposure pathways, and potential effects to terrestrial animals from proposed uses of picoxystrobin on crops. Figure II.2 depicts the stressors, exposure pathways, and potential effects to aquatic organisms from proposed uses of picoxystrobin. Figure II.3 depicts the drinking water and inhalation pathways and effects to terrestrial animals. For all figures, dotted lines indicate exposure pathways that have a low likelihood of contributing to ecological risk.

Figure II.1. Conceptual diagram for effects of picoxystrobin uses on non-target terrestrial animals.

18

Figure II.2. Conceptual diagram for effects of picoxystrobin uses on non-target aquatic organisms.

19 Picoxystrobin applied to use site Stressor

Direct Spray drift Atmospheric Runoff Source application transport

Exposure Media Dew (formed on Puddles (formed on Air terrestrial plants) treated fields)

Inhalation Ingestion

Terrestrial Terrestrial Receptors vertebrates invertebrates

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

Figure II.3. Conceptual diagram for drinking water and inhalation exposure pathways and effects of picoxystrobin uses on non-target terrestrial animals.

II.6. Analysis Plan

In order to address the risk hypothesis, the potential for adverse effects on non-target aquatic and terrestrial animals and plants is estimated. In the following sections, the use, environmental fate, and ecological effects of picoxystrobin are characterized and integrated to assess the risks. This is accomplished using a risk quotient (ratio of exposure concentration to effects concentration) approach. Although risk is often defined as the likelihood and magnitude of adverse ecological

20 effects, the risk quotient-based approach does not provide a quantitative estimate of likelihood and/or magnitude of an adverse effect. Such estimates may be possible through a more refined, probabilistic assessment; however, they are beyond the scope of this baseline assessment. This analysis provides the basis for estimating and describing risks, identifying uncertainties in the risk hypothesis, and recommendations for new data collection if needed to fill the data gaps.

This assessment only considers the potential effects of picoxystrobin fungicide exposure as a result of the currently proposed uses. The Agency does not routinely include 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 (that 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 the active ingredient and degradates, they may be used qualitatively or quantitatively in accordance with the Agency’s Overview Document and the Services’ Evaluation Memorandum (U.S., EPA 2004; USFWS/NMFS 2004).

For this baseline ecological risk assessment, estimated environmental concentrations (EECs) for aquatic and terrestrial systems were calculated using exposure scenarios for the proposed new uses according to label information. EECs were calculated using PRZM/EXAMS (PRZM v3.12.2; May 12, 2005; Carousel et al., undated; EXAMS v2.98.4.6; Apr. 25, 2005; Burns, 2004) and T-REX (v.1.5, an updated version used in this revised risk assessment). The resulting risk quotients from the TerrPlant model (v.1.2.2) for terrestrial plants growing in dry and semi- aquatic environments are generated by using the seedling emergence and vegetative vigor toxicity information at the maximum proposed single application rate.

II.6.1 Preliminary Identification of Data Gaps

EFED has enough environmental fate data to do risk assessment for this chemical. One possible data gap was identified pending on information from the registrant to clarify whether the submitted anaerobic aquatic metabolism study (OPPTS 835.4400; MRID# 48073840) was conducted on a soil or sediment system (two sediments as should be included in the study).

The quality of the submitted data is generally adequate; however some uncertainties exist and are discussed below. A catalog of submitted environmental fate studies for picoxystrobin and its degradates, along with justified review classifications, can be found in Appendix D. A complete summary of all submitted environmental fate data is included in Appendix E.

The ecological toxicity database for picoxystrobin is largely complete for terrestrial and aquatic animals and plant species. A complete summary of all submitted ecological effects data is included in Appendix B.

The following uncertainties and information gaps are identified as part of the problem formulation:

In the passerine acute oral study, regurgitation occurred in 10%, 40%, 70% of birds at the three

21 highest treatment levels where mortality and >50% frank sub-lethal effects were observed. Because regurgitation confounds the ability to determine the LD50, it can be assumed that excluding those doses at which regurgitation, mortality, and sub-lethal effects occurred, the LD50 is at least >486 mg a.i./kg bw. The value of 486 mg a.i./kg bw obtained from the study with passerines turned out to be the lowest acute screening-level endpoint used in the assessment to evaluate the potential acute exposure to non-listed and listed birds via the oral route. In the assessment, the RQ value was greater than 0.1 of the acute ratio (acute listed species LOC = 0.1) indicating there is a potential risk to 20 g and 100 g birds consuming short grass and 20 g birds consuming tall grass, broadleaf plants and arthropods. Since the screening-level endpoint tested is not 10 times greater than the maximum expected exposure level, mortality and >50% frank sub-lethal effects occurred, and one incident report of probable azoxystrobin (a strobilurin) effects on a bald eagle (Incident No. I018723-002) indicate that there is a potential risk for adverse effects on survival in addition to sub-lethal effects of ecological significance to passerines from the use of this pesticide. The risk to all federally listed birds including the smaller passerine species from the use of picoxystrobin cannot be precluded until data are made available to address the uncertainty. And in order to fully evaluate the potential risk to birds, data are needed on either an avian acute oral study with a passerine species if regurgitation does not occur up to or greater than 1400 mg a.i./kg (10x of the highest EEC at 140 mg a.i./kg) or using an avian subacute dietary study with a modified protocol for passerines where food consumption is monitored closely to generate an LD50, in addition to an LC50. A protocol should be submitted to and approved by the Agency prior to test initiation.

Data was not available to evaluate the risk of picoxystrobin to listed dicots because the listed toxicity threshold (NOAEC) is less than the limit dose in the seedling emergence and vegetative vigor tests. In order to draw a conclusion for listed dicots, a NOAEC would need to be ≤0.029 lb a.i./A to yield an RQ that exceeds the Listed Plant Species LOC of 1.0 or 16 times less than the limit dose tested. In the absence of a definitive NOAEC, risk to listed terrestrial dicot plants is uncertain. A multiple-dose toxicity test using cucumber, soybean, sugar beet, and tomato would be recommended to fully evaluate the effect to listed terrestrial dicot plants exposed to picoxystrobin; however, the level of uncertainty in the risk assessment and the value of additional data are low since the effects are not expected at environmentally relevant concentrations.

Toxicity data on sediment dwelling organisms are not available and are triggered based on 40 CFR Part 158 criteria. Available laboratory data from OECD-guideline studies, fate studies, and the chemical characteristics indicate that benthic invertebrates may be exposed to picoxystrobin uses. Based on calculations in this assessment where estimated sediment concentrations were calculated, the 21-day sediment porewater EECs predicted for picoxystrobin was 3.70 µg a.i./L. This 21-day sediment EEC exceeds the chronic LOC of 1.0 using the daphnid and mysid NOAECs of 1 and 3.6 µg a.i./L, respectively, which satisfies one of the criteria for requiring whole sediment toxicity testing under 40 CFR Part 158. Submitted soil metabolism and aquatic metabolism studies indicate picoxystrobin is moderately persistence (aerobic soil t1/2: 29.4 – 73.7 days; aerobic aquatic metabolism t1/2: 39.2 – 47.5 days; anaerobic aquatic metabolism t1/2: 83.5 days). These half-life values are greater than 40 CFR Part 158 criterion of 10 days. The third set of trigger criteria for requiring chronic testing (Kd >50 or log Kow >3 or Koc >1000) is also met for picoxystrobin (log Kow is 3.6 and Koc values range from 741 to 1089). The physicochemical

22 property triggers (log Kow and Koc) reflect the propensity of the chemical to partition onto the particulate or organic matter phases of sediment. Exceeding any one of the physicochemical property triggers listed above is sufficient for indicating the pesticide has reasonable potential for partitioning to the sediment compartment. The absence of these studies introduces uncertainty as to the effects of picoxystrobin on sediment-dwelling invertebrates. In addition, picoxystrobin has the potential to enter estuarine/marine water bodies based on current usage patterns (sweet and field corn, wheat, barley, sorghum, and soybeans) that include coastal counties. Also, toxicity studies with the free-swimming freshwater and estuarine/marine invertebrates indicate picoxystrobin is very toxic to these aquatic organisms. Until data are available, the risks to sediment-dwelling invertebrates are assumed. A protocol should be submitted and approved by the Agency prior to test initiation.

II.6.2. Measures of Exposure and Effects

II.6.2.1 Measures of Exposure

Measures of exposure are based on aquatic and terrestrial models that estimate environmental concentrations of picoxystrobin using labeled application rates and methods. The potential exposure pathways include deposition from spray applications, runoff/leaching from treated areas, spray drift, and wind erosion of soil particles resulting in residues on non-target species as well as residues on food items for non-target species.

The measure of exposure for aquatic species in water bodies receiving runoff and/or spray drift to surface water is a return frequency of 1-in-10 years of the estimated environmental concentration (EEC), based on 30 years of simulations. The 1-in-10 year peak concentration is used for estimating acute effects to aquatic organisms (plants and animals); the 1-in-10 year 21- day mean concentration is used for assessing aquatic invertebrate chronic exposure; 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).

Terrestrial exposure assumes application of the active ingredient to a one-acre agricultural field that settles on food items of avian and mammalian species (short and tall grass, broadleaf forage, arthropods, fruits, pods, and seeds) within the field. Plant exposure assumes application of the active ingredient to a one-acre agricultural field that drifts and/or is subject to runoff off site to adjacent fields of non-target plants inhabiting dry and semi-aquatic areas.

Model input parameters are selected based on laboratory fate data in accordance with EFED’s input parameter guidance3. Modeling is conducted based on the maximum potential number of applications, maximum application rate, and the shortest application interval.

II.6.2.2. Measures of Effects

Measures of ecological effects are obtained from submitted guideline studies conducted with a limited number of surrogate species on picoxystrobin. The test species are not intended to be representative of the most sensitive species but rather were selected based on their ability to thrive under laboratory conditions and their standardized use for toxicity studies of a variety of

23 chemicals. Submitted ecological effects data comply with good laboratory testing requirements. These data are summarized in the Ecological Effects Section and in Appendix B.

As stated above, toxicity testing does not represent all species of birds, mammals, or aquatic animals. Only a few surrogate species for both freshwater fish and birds are used to represent all freshwater fish (2000+) and bird (680+) species in the United States. For mammals, acute studies are usually limited to the laboratory rat. Estuarine/marine testing is usually limited to a crustacean, a mollusk, and a fish. In addition, neither reptiles nor amphibian data are available. The risk assessment assumes that avian, terrestrial-phase amphibian and reptilian toxicities are similar. The same assumption is used for fish and aquatic-phase amphibians.

A summary of the assessment and measurement endpoints selected to characterize potential ecological risks associated with exposure to the active ingredient are summarized in Table II.3.

Table II.3. Summary of Assessment Endpoints and Measures of Ecological Effects* Surrogate Species and Measures of Ecological Assessment Endpoint Measures of Exposure Effect1

Lowest acute oral LD50 Birds, terrestrial- Survival (zebra finch) and subacute dietary LC50 (Northern phase bobwhite quail and mallard duck) amphibians and 2 Reproduction reptiles Lowest reproduction NOAEC (duck) Upper bound residues on and growth food items

Survival Laboratory rat acute oral LD50 Mammals Reproduction and growth Laboratory rat reproduction NOAEC 4 Freshwater fish, Survival Lowest acute LC50 (fathead minnow) Peak EEC

aquatic-phase Reproduction 4 3 60-day average EEC amphibians and growth Lowest reproduction NOAEC (fathead minnow) Survival Water flea acute EC Peak EEC4 Freshwater 50 Reproduction invertebrates 21-day average EEC4 and growth Water flea reproduction NOAEC

4 Survival Sheepshead minnow acute LC50 Peak EEC Estuarine/marine fish Reproduction 60-day average EEC4 and growth Sheepshead minnow reproduction NOAEC 4 Survival Lowest acute EC50/LC50 (Eastern oyster) Peak EEC Estuarine/marine Reproduction invertebrates 21-day average EEC4 and growth Mysid shrimp reproduction NOAEC Peak sediment Survival Eastern oyster and daphnid acute EC50 porewater EEC Benthic invertebrates Reproduction 21-day sediment and growth Daphnid and mysid reproduction NOAECs porewater EEC

Lowest EC25 for non-listed plants and corresponding NOAEC (or EC ) for listed plants from seedling Estimates of runoff and Survival and 05 Terrestrial plants5 emergence (monocot- ryegrass; dicot- soybean) and spray drift to non-target growth vegetative vigor (monocot- onion; dicot- cucumber) areas studies

24 Table II.3. Summary of Assessment Endpoints and Measures of Ecological Effects* Surrogate Species and Measures of Ecological Assessment Endpoint Measures of Exposure Effect1 Survival (not Maximum application Insects quantitatively Honeybee acute contact LD 50 rate assessed)

Survival Earthworm subchronic LC50 Soil-dwelling Estimates of soil invertebrates concentration Reproduction Earthworm subchronic NOAEC

Lowest EC for non-listed plants and corresponding Aquatic plants and Survival and 50 NOAEC (or EC ) for listed plants for algal (marine Peak EEC4 algae growth 05 diatom) and vascular plant (duckweed) 1 If species listed in this table represent most commonly encountered species from submitted studies, risk assessment guidance indicates most sensitive species tested within taxonomic group are to be used for baseline risk assessments. 2 Birds represent surrogates for amphibians (terrestrial phase) and reptiles. 3 Freshwater fish may be surrogates for amphibians (aquatic phase). 4 Based on PRZM/EXAMS active ingredient modeling. 5 Four species of two families of monocots - one is corn, six species of at least four dicot families, of which one is soybeans. * LD50 = Lethal dose to 50% of the test population; NOAEC = No observed adverse effect concentration; LOAEC = Lowest observed adverse effect concentration; LC50 = Lethal concentration to 50% of the test population; EC50/EC25 = Effect concentration to 50%/25% of the test population.

III. ANALYSIS

III.1. Use Characterization

DuPont™ is seeking the registration for the new active ingredient, picoxystrobin, for use to control foliar and soil-borne plant diseases on the following proposed uses: sweet corn, field corn, seed, popcorn, soybean, sorghum, legume vegetables, dried shelled beans, peas, cereal grains (except rice) and canola. Picoxystrobin is formulated as a suspension concentrate. Methods of application include foliar broadcast spray via ground or air methods. The label states that after two sequential applications of picoxystrobin, switching to a fungicide with a different mode of action is recommended to reduce the risk of fungicide resistance development.

This risk assessment focuses exclusively on the use patterns of picoxystrobin for control of susceptible plant diseases. Use patterns tabulated in Table III.1 below serve as the basis for selecting the appropriate application rates and method used as part of the input parameters needed to obtain EECs with simulation models.

25 Table III.1. Picoxystrobin Application Information Maximum Maximum Method of Application Maximum Number of Applications Seasonal Crop Application Rate Use Rate lb a.i./A (lb a.i./A) Field corn, Early season application sweet, seed, Variable1 1 application (4 fl oz) and popcorn Additional applications 1st application (12 fl oz) Cereal grains Variable1 2nd application (12 fl oz) (except rice) 3rd application (8 fl oz) A 0.585 Sorghum 0.195 3 applications (7-day interval) Broadcast Foliar Spray Soybean 0.195 3 applications (7-day interval) (ground & (grain) aerial) Canola 0.195 2 applications Legume 0.39 vegetables, (7-day interval) Dried shelled 0.195 beans, peas Soybean (forage and hay) 0.195 1 application 0.195 1 The maximum application rate for the first, second, third, and fourth application is 0.065, 0.195, 0.195, and 0.13 lb a.i./A. A The reapplication intervals for corn uses is 44, 7, 7, and 7 days; for cereal grains uses it is 18, 7, 7 and 7 days.

III.2. Exposure Characterization

III.2.1. Environmental Fate and Transport Characterization

The general physical/chemical properties of picoxystrobin are summarized in Table III.2. Environmental fate and transport properties of picoxystrobin are characterized in further detail in the following sections. The Agency’s understanding of these properties is limited by the available data set. Many of the chemical properties and environmental fate parameters of picoxystrobin listed in Table III.3 are based on supplemental studies. Additional detail on each study is provided in Appendix E.

26 Table III.2 General Physical and Chemical Properties of Picoxystrobin Parameter Value Reference PC code 129200 -- CAS No. 117428-22-5 -- Structure -- F F N O F O O H3C CH3

O Chemical name Methyl(E)-2-{2-[6-(trifluoromethyl)pyridin-2- -- (IUPAC) yloxymethyl]phenyl}-3-methoxyacrylate. Methyl (2E)-3-methoxy-2-{2-[6-(trifluoromethyl)-2- pyridyloxymethyl]phenyl}acrylate. Chemical name (CAS) 1H-Pyrazole-4-carboxamide, N-[2-(1,3-dimethylbutyl)phenyl]-5- -- fluoro-1,3-dimethyl- Common name Picoxystrobin --

Chemical formula C18H16F3NO4 -- Molecular weight 367.3 g/mol MRID# 48073842 Water solubility (20ºC, 3 mg/L MRID# 48073834 pH 7) Vapor pressure ((20ºC) 4.14 x 10-8 torr MRID# 48073833 Henry's law constant 6.64 x 10-9 atm·m3/mol Calculated Octanol-water 3.6 MRID#48073710 partitioning coefficient Log KOW (20ºC, pH 7) Dissociation Constant N/A (No dissociation) MRID#48073710 (pKa)

Picoxystrobin is moderately persistent in aerobic and anaerobic conditions, and is moderately mobile based on the FAO Soil mobility classifications (mean Koc = 924 L/kg-organic carbon; MRID 48073832). Picoxystrobin (with Koc values below 500 L/kg-OC) has the potential to leach into groundwater. Picoxystrobin is moderately persistent in soil with half-lives ranging from 29 to 73 days in aerobic soil from three studies conducted in four soils (MRID 48073837). There is no evidence of degradation via hydrolysis which was studied across environmental pHs (pH 5, pH 7 at 25ºC, and pH 9 at 50 ºC; MRID 48073834). Picoxystrobin degraded under the conditions of aerobic aquatic metabolism with half-lives ranging from 39 to 41 days (MRID 48073839); and under anaerobic aquatic systems with a half-life of 83 days (MRID 48073840). The primary route of degradation may include aqueous photolysis (half-life of 16 days; MRID 48073835); however photolysis only plays a significant role in shallow clear waters. Under other conditions, aerobic metabolism is expected to be the primary route of degradation.

Major degradates include Compound 2 (IN-QDY62 R403092), Compound 3 (IN-QDK50 R403814), Compound 4, Compound 7 (IN-QFA35), Compound 12, Compound 8 (IN-QDY63),

27 and CO2 were identified in the environmental fate studies at concentrations >10% of the applied radioactivity. In all four soils and under aerobic soil conditions, Compounds 2 and 3 were reported at decreasing concentrations at the study termination (119 and 365 days). See Table in Appendix K.

A summary of the submitted environmental fate and transport data is summarized below in Table III.3.

Table III.3 Environmental Fate Data Summary for Picoxystrobin OPPTS Data Requirement Data Summary Source Guideline

835.2120 Hydrolysis t 1/2 at 50°C Stable MRID# 48073834

835.2240 Aqueous photolysis t1/2 at 25°C 28.9 days MRID# 48073835

835.2410 Soil photolysis t1/2 at 20°C 11.6 days MRID# 48073836

835.4100 Aerobic soil metabolism t1/2 at 20°C 73.7 days (sandy loam) MRID 48073837 (combined radio-label half-life)* 29.4 days (clay loam) 38.3 days (sand) 34.7 days (sandy loam)

835.4200 Anaerobic Soil Metabolism t½ at Waived MRID 48073838 20°C

835.4300 Aerobic aquatic metabolism t1/2 at 39.2 days (the total system) MRID 48073839 20°C (sandy clay loam sediment 47.5 days (the total system) system and sand system, 2 radio- labels) * 835.4400 Anaerobic aquatic metabolism t1/2 at 83.5 days (the total system) MRID 48073840 20°C (,sandy loam soil system combined labels) 835.1230 Organic carbon partitioning 837 (sandy loam) MRID 48073832 coefficient 1089 (silty clay loam) (Koc, mL/g oc) 741 (sandy loam) 933 (sandy loam) 1067 (sand) 878 (Sandy clay loam)

Freundlich adsorption value, Kf , 4.9 (sandy loam) MRID 48073838 mL/g oc (1/n) 22.4 (silty clay loam) 22.4 (sandy loam) 15.7 (sandy loam) 3.5 (sand) 14 (Sandy clay loam)

835.6100 Terrestrial field dissipation DT50 41.3 days (Porterville, California/Sandy loam) MRID 48073842 US soils 34.7 days (Arkansaw, Wisconsin/Sandy loam-loamy) MRID 48073843

Terrestrial field dissipation DT50 151 days (Manitoba, Canada/Clay loam-loam) MRID 48073841 Foreign soils 39.4 days (Prince Edward Island, Canada/Sandy loam) MRID 48073844 62 days (Grissoles, France/Silty clay loam) MRID 48073846 108 days (Maidenhead, UK/Sandy clay loam) MRID 48073847 94 days (Saxe-Anhalt, Germany/Sandy clay loam) MRID 48073848 80 days (Cessac, France/Clay loam) MRID 48073849 53 days (Schleswig-Holstein, Germany/Sandy loam) MRID 48073850 80 days (Bracknell, Berkshire, UK/Sandy clay loam) MRID 48073851 850.1730 Fish bioconcentration 1400 in viscera, MRID 48073776 (steady state BCF ) µg/kg 110 in flesh and 170 in the carcass. 290 in whole fish

28 Table III.3 Environmental Fate Data Summary for Picoxystrobin OPPTS Data Requirement Data Summary Source Guideline

*: Based on first-order linear regression analyses.

III.2.1.1. Transport and Mobility

Picoxystrobin is not volatile, with a partial vapor pressure of 4.14 x 10-9 torr at 25ºC, for (MRID

48073840). The open-literature Kow for picoxystrobin at 25ºC for pH 7 was 3981 (Log Kow = 3.6; MRID# 48073710; Footprint Pesticide Properties Database).

Picoxystrobin is moderately mobile to mobile based on FAO Soil Mobility Classification Guidance (USEPA, 2006a), with reported organic carbon partitioning coefficients ranging from 741 to 1089 L/kg-organic carbon (Freundlich adsorption values (Kf) from six soils range from 3.5 to 22.4 L/kg-organic carbon; MRID 48073838). Batch equilibrium data for picoxystrobin show that adsorption to soil is well correlated with organic carbon content (r2 = 0.91, p = 0.92).

II.2.1.2. Degradation

Picoxystrobin is stable to hydrolysis; there was no evidence of degradation at pH 4, 7, and 9 at 50ºC (MRID# 48073834). It is photolyzed in water (combined label, corrected environmental half-life of 28.9 days at pH 7; MRID# 48073835). Picoxystrobin biodegrades slowly in aerobic soil with half-lives ranging from 29.4 to 73.7 days in four soils (parent-only half-lives; MRID 48073837).

Based on the study results, picoxystrobin degrades to Compound 2 via ester hydrolysis and also to numerous minor compounds including Compounds 7 and 8. Picoxystrobin and Compound 2 are converted to Compound 3 via ether cleavage. Compound 3 is methylated to Compound 26, which is volatilized from the soil. Picoxystrobin residues are ultimately bound to the soil or converted to CO2.

An aerobic aquatic metabolism study was conducted for picoxystrobin investigating the biotransformation of [pyridinyl-5-14C]- and [phenylacrylate-2-14C]-labeled methyl (2E)-3- methoxy-2-{2-[6-(trifluoromethyl)-2-pyridyloxymethyl]phenyl}acrylate (picoxystrobin, ZA1963) in two water-sediment systems from England (a water-sandy clay loam sediment system and a water-sand sediment system). In both systems (sandy clay loam sediment system and sand system) picoxystrobin degraded with a linear regression half-lives of 39.2 days and 47.5 days (the total system); respectively (MRID# 48073839).

An anaerobic aquatic metabolism study was conducted for picoxystrobin investigating the biotransformation of [pyridinyl-5-14C]- and [phenylacrylate-2-14C]-labeled methyl(E)-2-{2-[6- (trifluoromethyl)pyridin-2-yloxymethyl]phenyl}-3-methoxyacrylate (picoxystrobin, ZA1963) in a purified water-UK sandy loam soil system. Picoxystrobin degraded with the total system half- life of 83.5 days (MRID# 48073840).

29 III.2.1.3. Field Studies

Ten terrestrial field dissipation studies were conducted for picoxystrobin using two sites in the United States (California and Wisconsin), two sites in Canada (Manitoba and Prince Edward Island), and six sites in the European Union (France, UK, and Germany).

All North American studies were conducted with broadcast applications to bare ground (MRIDs 48073841, 48073842, 48073843, 48073844), each site studied four bare ground plots that had <1% slope gradient. Picoxystrobin was broadcast once at a nominal rate of 1.0 kg a.i./ha (0.89 lb a.i./A) onto three replicate plots (the maximum proposed rate was not reported). Picoxystrobin was not detected in soil below the 0-5 cm depth. For the total soil profile, dissipation rates (expressed as a DT50) for picoxystrobin from the North American field studies ranged from 3- 108 days.

An additional study of six sites in Europe (France, Germany, and the UK) was conducted to study the dissipation in European soils (MRID 48073846-51). Picoxystrobin was sprayed once at a target rate of 0.750 kg a.i./ha (0.670 lb a.i./A) onto one plot measuring 5 x 45 m. The test application was made at the highest European label application rate for cereals Dissipation rates (DT50s) from the European studies ranged from 53 to 108 days were comparable to the North American field studies.

III.2.1.4. Bioconcentration

A flow-through bioconcentration study of bluegill sunfish (Lepomis macrochirus) exposed to picoxystrobin in pH 7.3-7.9 water for 28 days indicates that the compound does not bioconcentrate. The 28-day exposure period was followed by a 14 day depuration period. Bioconcentration factors (BCF) in various fish tissues were 1400 µg/kg in viscera, 110 µg/kg in flesh and 170 µg/kg in the carcass. The steady state whole fish BCF was 290 µg/kg (MRID 48073776).

BCF values (whole fish) less than 1000 do not trigger criteria for further evaluation of whether picoxystrobin is a bioaccumulative compound [64 Fed. Reg. 60194-60204 (November 4, 1999)].

III.2.1.5. Environmental Degradates

Major degradates (Appendix K) including Compound 2 (IN-QDY62 R403092), Compound 3 (IN-QDK50 R403814), Compound 4, Compound 7 (IN-QFA35), Compound 12, Compound 8 (IN-QDY63), and CO2 were identified in the environmental fate studies at concentrations >10% of the applied radioactivity. In all four soils and under aerobic soil conditions, Compounds 2 and 3 were reported at decreasing concentrations at the study termination (119 and 365 days).

Compound 2 was also detected as a major degradate in the aerobic aquatic and the anaerobic aquatic metabolism studies with no sign of decrease in concentrations at the study termination.

Compound 2 and 3 were both detected in the terrestrial field dissipation studies, however detections were largely restricted to the 0-30 cm range of the soil profile.

30

Compound 4 was detected in the aquatic photolysis study at maximum concentration of 14.2% of the applied radiation but decreased by the end of the study (18 days). Compound 7 was detected at a maximum concentration of 38.3% of the applied radiation at the study termination (120 days) under aerobic aquatic conditions. Maximum concentrations of Compound 12 (15.3 % of the applied radiation) were detected under aquatic photolysis conditions at the study termination (18 days; MRID# 48073835).

According to the Report of the Residues of Concern Knowledgebase Subcommittee (ROCKS) memo dated (Aug 22, 2011); the environmental degradates of picoxystrobin that are considered an exposure concern for drinking water are Compounds 2, 3, and 7, under aquatic photolysis and metabolism (aerobic and anaerobic). These degradates were formed at increasing concentrations through the termination of the environmental fate studies in which they were formed.

Batch equilibrium data for Compound 2 show that it will be mobile to slightly mobile (based on FAO Standardized Soil Mobility Classifications) depending on soil pH. The Koc values, which varied from 23 to 42 L/kg-organic carbon for the three alkaline soils and from 170 to 1200 L/kg- organic carbon for the three acidic soils (compared to the parent’s Koc : 741-1089 L/kg-organic carbon; MRID 48073838). The difference in adsorptive behavior between alkaline and acidic soils was attributed to Compound 2 having a pKa value of 4.71, meaning that in alkaline soils it would be expected to be present mainly in its dissociated, negatively charged form, and as such would not be strongly adsorbed to lipophilic organic surfaces. In acidic soils, by contrast, much of the substance should be present as the uncharged associated form, resulting in stronger attraction to organic matter.

The results of the adsorption/desorption study on Compound 3 showed that it was weakly adsorbed to all six soils, with Koc values in the range 10-29 L/kg-organic carbon indicating it is mobile in the environment according to the FAO Standardized Soil Mobility Classifications.

A minor degradation product that may be an exposure concern is Compounds 26 which was detected at nearly 9% in various studies (Appendix K).

III.2.2. Measures of Aquatic Exposure

III.2.2.1. Surface Water Exposure

The 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 Tier II PRZM/EXAMS model shell (PE v5.0, Nov. 15, 2006), i.e., PRZM/EXAMS) was 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 loading via runoff, erosion, and spray drift assuming a standard 1-ha pond, 2-m deep (20,000 m3) 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 once every ten years based on the daily values estimated. The coupled PRZM/EXAMS model and users manuals are available from the U.S.

31 Environmental Protection Agency Water Models web-page (USEPA, 2011b).

Exposure estimates generated using this standard pond are intended to represent a wide variety of vulnerable water bodies that occur at the top of watersheds including prairie pot holes, playa lakes, wetlands, vernal pools, man-made and natural ponds, and intermittent and first-order streams. As a group, there are factors that make these water bodies more or less vulnerable than the standard surrogate pond. Static water bodies that have larger ratios of pesticide-treated drainage area to water body volume would be expected to have higher peak EECs than the standard pond. These water bodies will be either smaller in size or have large drainage areas. Smaller water bodies have limited storage capacity and thus may overflow and carry pesticide in the discharge, whereas the standard pond has no discharge. As watershed size increases, it becomes increasingly unlikely that the entire watershed is planted with a non-major single crop that is all treated simultaneously with the pesticide. Headwater streams can also have peak concentrations higher than the standard pond, but they likely persist for only short periods of time and are then carried and dissipated downstream.

The general chemical and environmental fate data for picoxystrobin listed in Tables III.2 and III.3 were used for generating model input parameters for PRZM and EXAMS (listed in Table III.4). Chemical specific and model input values were chosen in accordance with current divisional guidance (USEPA, 2009).

32 Table III.4. PRZM and EXAMS Surface Water Chemical Input Parameters for Picoxystrobin.

Input Parameter Value Source /Comment

-1 Molecular Mass (g·mol ) 367.31 MRID# 48073842

Vapor Pressure at 25°C 4.14 X 10-8 MRID# 48073840 (torr) Solubility in Water at -1 3 MRID# 48073834 20ºC, pH7 (mg·L ) Organic carbon partition Mean of six Koc values: 837, 1089, 741, 933, 1067, and 878; 799 coefficient (Koc, mL/g oc) Input parameter guidance V. 2.1. ( 2009). MRID# 48073832. Aerobic Soil Metabolism The 90th percentile of the upper confidence bound on the Half-life (days) 60.5 mean of 4 half-life values: 73.7, 29.4, 38.3, and 34.7 days. Input parameter guidance V. 2.1. ( 2009). MRID# 48073837. Aerobic Aquatic The 90th percentile of the upper confidence bound on the Metabolism Half-life 43.8 mean of 2 half-life values: 39.2, 41.5 days. Input parameter (days) guidance V. 2.1. ( 2009). MRID# 48073839. Anaerobic Aquatic Single value of 83.5 days multiplied by 3; Input parameter Metabolism Half-life 250 guidance V. 2.1. ( 2009). MRID# 48073840. (days) Hydrolysis Half-lives Stable. Input parameter guidance V. 2.1. ( 2009). MRID# Stable (0) (days) 48073834 Aqueous Photolysis 28.9 MRID# 48073835. Input parameter guidance V. 2.1. ( 2009). Half-life (days) CAM 2 Input parameter guidance V. 2.1. ( 2009). Application Efficiency 0.95 Aerial Input parameter guidance V. 2.1. ( 2009). (0.99 Ground) Spray Drift Fraction 0.05 Aerial Input parameter guidance V. 2.1. ( 2009). (0.01 Ground) *: Dates of applications were chosen based on label directions and crop growth stages: Corn V4 (19-26 days after seeding) V7 (28-35 days after seeding) VT (65-72 days after seeding) R3 (91-98 days after seeding) @ http://www.sdstate.edu/ps/extension/crop-mgmt/corn/upload/Corn-growth-stage-day-and-GDU-calendar10.pdf Wheat Single application between tillering through jointing Additional applications at “flag leaf out” stage @http://www.ag.ndsu.edu/pubs/plantsci/smgrains/w564.pdf.

The model input parameters used in PRZM to simulate picoxystrobin application with aerial and ground equipements and management practices are provided in Table III.5. Application rates for modeling purposes were selected in accordance with the proposed labels to generate the most conservative estimates of aquatic exposure. The label does recommend a day of application for picoxystrobin but to be used at first sign of infestation. Application dates were chosen to reflect the highest Average Daily Precipitation over 30 years (according to the met file) for the specific PRZM scenario modeled.

33 Table III.5 PRZM/EXAMS Model Input Parameters for Picoxystrobin. Application Application Rate in lbs a.i./A Applications Application Use Scenario Interval (kg a.i./ha) per Year Method (days) Field corn, Early season application sweet, seed, MSCornstdSTD.txt 1 application @0.065 (0.073) 4 44, 7, 7, 7 Aerial/ground popcorn1 Additional applications 1st application @ 0.195 (0.218) Cereal grains NDWheatSTD.txt 2nd application @ 0.195 (0.218) 4 18, 7, 7, 7 Aerial/ground (except rice) 2 3rd application @ 0.13 (0.146) Sorghum, 0.195 MSsoybeanSTD.txt 3 7 Aerial/ground Soybean (0.585) Canola, Legume 0.195 vegetables MIbeansSTD.txt 2 7 Aerial/ground (0.390) Dried shelled beans, peas 1 First application at 0.065 lb a.i/A, after 44 days 2nd, 3rd, 4th application at 0.195, 0.195, 0.13 lb a.i./A applied 7 days apart. 2 First application at 0.065 lb a.i/A, after 18 days 2nd, 3rd, 4th application at 0.195, 0.195, 0.13 lb a.i./A applied 7 days apart.

Although there is more than one PRZM scenario available for the proposed crops, the ones used in this assessment were chosen to represent the more conservative ones based on the weather and soil type (i.e wet weather and soil types that are more vulnerable to surface runoff).

The modeled aquatic EECs resulting from the proposed picoxystrobin uses (listed in Table III.6) were used for risk estimation in this screening-level assessment. The model input and output filenames supporting these values are listed in Appendix F.

Table III.6. Modeled Aquatic Surface Water EECs (ppb or µg/L) for Proposed Uses of Picoxystrobin Aerial Application Scenario Peak 21-Day Avg 60-Day Avg 90-Day Avg MS-Corn 8.74 7.12 5.29 4.64 MS-Soybean 8.92 7.31 5.75 5.21 ND-Wheat 3.57 3.06 2.34 2.07 MI-Beans 3.62 2.97 2.33 2.20 Ground Application Scenario Peak 21-Day Avg 60-Day Avg 90-Day Avg MS-Corn 8.34 6.75 4.99 4.40 MS-Soybean 8.90 7.29 5.59 5.09 ND-Wheat 2.75 2.27 1.75 1.53 MI-Beans 2.85 2.55 2.13 1.85

34 The ecological pond modeled with EXAMS is a static water body of fixed volume with no outlet. Exposure endpoints, in this assessment, are based on yearly peak concentrations. In the case of persistent compounds, a 1-in-10 year EEC does not reflect varying meteorological conditions that are expected once every 10 years, since the yearly peaks are not independent but are actually correlated to the previous year’s peak concentration.

The exposure to aquatic species from sediment concentrations in water bodies was determined to be of concern after a review of the appropriate fate and effects data; pore-water EECs were calculated for maximum use patterns (Table III.7).

Table III.7. Modeled Aquatic Sediment Pore Water EECs (ppb) for Proposed Uses of Picoxystrobin Scenario Peak 21-Day Avg 60-Day Avg 90-Day Avg MS-Soybean 3.70 3.68 3.53 3.34

III.3. Measures of Terrestrial Exposure

III.3.1. Terrestrial Wildlife

Terrestrial wildlife exposure estimates are typically calculated for birds and mammals, emphasizing a dietary exposure route for uptake of pesticide active ingredients. These exposures are considered as surrogates for terrestrial-phase amphibians as well as reptiles. For exposure to terrestrial wildlife, such as birds and small mammals, pesticide residues on food items are estimated, based on the assumption that animals are exposed to a single pesticide residue in a given exposure scenario.

For picoxystrobin spray applications, estimation of pesticide concentrations in wildlife food items focuses on quantifying possible dietary ingestion of residues on vegetative matter and insects. No field residue data or field study information is available for picoxystrobin; therefore, the residue estimates were based on a nomogram that relates food item residues to pesticide application rate. The residue EECs were generated from a spreadsheet-based model (T-REX 1.5, a updated version for this revised risk assessment from the original version of 1.4.1) that calculates the decay of a chemical applied to foliar surfaces for single or multiple applications, and is based on the methods of Hoerger and Kenaga (1972) as modified by Fletcher et al. (1994). Uncertainties in the terrestrial EECs are primarily associated with a lack of data on interception and subsequent dissipation from foliar surfaces. T-REX does not differentiate between aerial or ground applications, the method of application is not considered; thus, aerial and ground applications are considered equivalent. To provide potential exposures to non-target birds and mammals based on proposed label uses of picoxystrobin, residue EECs were calculated using four exposure scenarios: four applications of variable rates and intervals with the first maximum application rate at 0.065 lb a.i./A followed by three additional applications at 0.195 lb a.i./A, 0.195 lb a.i./A and 0.013 lb a.i./A with a 18-day interval between the first and second application followed by 7-day intervals for the rest of applications (cereal grain (except rice)); four applications of variable rates and intervals with the first maximum application rate at 0.065 lb a.i./A followed by three additional applications at 0.195 lb a.i./A, 0.195 lb a.i./A and 0.013 lb a.i./A with a 44-day interval between the first and second application followed by 7-day intervals

35 for the rest of applications (sweet corn, field corn, seed, popcorn); three applications at 0.195 lb a.i./A with a 7-day reapplication interval (sorghum and soybean), and two applications at 0.195 lb a.i./A with a 7-day reapplication interval (canola, legume vegetables, dried shelled beans, and peas). EECs were calculated using a foliar dissipation default half-life of 35 days (Willis and McDowell, 1987). In addition, an optional test species body weight (g) input of 14 g was assumed for the zebra finch, obtained from the study data.

The EECs on terrestrial food items may be compared directly with dietary toxicity data or converted to an oral dose (see Tables III.8 (birds and mammals) and III.9 (birds) and III.10 (mammals). The residue concentration is converted to daily oral dose based on the fraction of body weight consumed daily as estimated through allometric relationships. The risk assessment for picoxystrobin uses upper bound predicted residues as the measure of exposure.

Table III.8. Terrestrial Dietary-Based EECs (Bird and Mammal) Following Picoxystrobin Spray Application. Upper Bound EEC1 Uses # of App. x App. Rate Food Items (mg a.i./kg diet) Short Grass 123.01 3 applications at Tall Grass 56.38 Sorghum, Soybean 0.195 lb a.i./A with 7-day Broadleaf Plants 69.19 intervals Fruits, Pods, Seeds 7.69 Arthropods 48.18 4 applications; first app at Short Grass 115.69 0.065 lb a.i/A, after 18 days Tall Grass 53.02 Cereal grains (except 2nd, 3rd, 4th app at Broadleaf Plants 65.07 rice) 0.195, 0.195, 0.13 lb a.i./A Fruits, Pods, Seeds 7.23 with 7-day intervals Arthropods 45.31 4 applications; first app at Short Grass 112.36 0.065 lb a.i/A, after 44 days Tall Grass 51.50 Sweet corn, Field corn, 2nd, 3rd, 4th app at Broadleaf Plants 63.20 seed, popcorn 0.195, 0.195, 0.13 lb a.i./A Fruits, Pods, Seeds 7.02 with 7-day intervals Arthropods 44.01 Short Grass 87.54 Canola, 2 applications at Tall Grass 40.12 Legume vegetables, 0.195 lb a.i./A with 7-day Broadleaf Plants 49.24 Dried shelled beans, peas intervals Fruits, Pods, Seeds 5.47 Arthropods 34.29 1 Used to determine the potential risk to non-target wildlife and the need to consider regulatory action.

36 Table III.9. Terrestrial Dose-Based EECs (Birds) Following Picoxystrobin Spray Application. Avian Classes and Body Weights # of App. x App. Uses Food items small mid large Rate 20 g 100 g 1000 g Upper Bound EEC (mg a.i./kg bw)1 Short Grass 140.10 79.89 35.77 3 applications at Tall Grass 64.21 36.62 16.39 Sorghum, Soybean 0.195 lb a.i./A with Broadleaf Plants 78.80 44.94 20.12 7-day intervals Fruits, Pods 8.76 4.99 2.24 Arthropods 54.87 31.29 14.01 Seeds 1.95 1.11 0.50 4 applications; first Short Grass 131.76 75.13 33.64 app at 0.065 lb a.i/A, Tall Grass 60.39 34.44 15.42 after 18 days 2nd, 3rd, Cereal grains (except Broadleaf Plants 74.11 42.26 18.92 4th app at rice) Fruits, Pods 8.23 4.70 2.10 0.195, 0.195, 0.13 lb Arthropods a.i./A with 7-day 51.60 29.43 13.17 intervals Seeds 1.83 1.04 0.47 4 applications; first Short Grass 127.96 72.97 32.67 app at 0.065 lb a.i/A, Tall Grass 58.65 33.44 14.97 after 44 days 2nd, 3rd, Sweet corn, Field corn, Broadleaf Plants 71.98 41.05 18.38 4th app at seed, popcorn Fruits, Pods 8.00 4.56 2.04 0.195, 0.195, 0.13 lb Arthropods 50.12 28.58 12.80 a.i./A with 7-day Seeds intervals 1.78 1.01 0.45 Short Grass 99.70 56.85 25.45 Canola, Tall Grass 45.70 26.06 11.67 2 applications at Legume vegetables, Broadleaf Plants 56.08 31.98 14.32 0.195 lb a.i./A with Dried shelled beans, 7-day intervals Fruits, Pods 6.23 3.55 1.59 peas Arthropods 39.05 22.27 9.97 Seeds 1.38 0.79 0.35 1 Used to determine the potential risk to non-target wildlife and the need to consider regulatory action.

37 Table III.10. Terrestrial Dose-Based EECs (Mammalian) Following Picoxystrobin Spray Application. Mammalian Classes and Body # of App. x App. Weights Uses Food items Rate small mid large 15 g 35 g 1000 g Upper Bound EEC (mg a.i./kg bw)1 Short Grass 117.28 81.06 18.79 3 applications at Tall Grass 53.75 37.15 8.61 Sorghum, Soybean 0.195 lb a.i./A with Broadleaf Plants 65.97 45.59 10.57 7-day intervals Fruits, Pods 7.33 5.07 1.17 Arthropods 45.93 31.75 7.36 Seeds 1.63 1.13 0.26 4 applications; first Short Grass 110.30 76.23 17.67 app at 0.065 lb a.i/A, Tall Grass 50.55 34.94 8.10 after 18 days 2nd, 3rd, Cereal grains (except Broadleaf Plants 62.04 42.88 9.94 4th app at rice) Fruits, Pods 6.89 4.76 1.10 0.195, 0.195, 0.13 lb Arthropods a.i./A with 7-day 43.20 29.86 6.92 intervals Seeds 1.53 1.06 0.25 4 applications; first Short Grass 107.12 74.04 17.17 app at 0.065 lb a.i/A, Tall Grass 49.10 33.93 7.87 after 44 days 2nd, 3rd, Sweet corn, Field corn, Broadleaf Plants 60.26 41.65 9.66 4th app at seed, popcorn Fruits, Pods 6.70 4.63 1.07 0.195, 0.195, 0.13 lb Arthropods 41.96 29.00 6.72 a.i./A with 7-day Seeds intervals 1.49 1.03 0.24 Short Grass 83.46 57.69 13.37 Canola, Tall Grass 38.25 26.44 6.13 2 applications at Legume vegetables, Broadleaf Plants 46.95 32.45 7.52 0.195 lb a.i./A with Dried shelled beans, Fruits, Pods 5.22 3.61 0.84 7-day intervals peas Arthropods 32.69 22.59 5.24 Seeds 1.16 0.80 0.19 1 Used to determine the potential risk to non-target wildlife and the need to consider regulatory action.

The Screening Imbibition Program (SIP v.1.0, Released June 15, 210) was used to calculate an upper bound estimate of exposure using picoxystrobin’s solubility (3.0 mg/L), the most sensitive acute and chronic avian toxicity endpoints (LD50 >486 mg a.i./kg-bw and NOAEC = 157 mg a.i./kg-diet, respectively) and the most sensitive acute and chronic mammalian toxicity endpoints (LD50 >5000 mg a.i./kg-bw and NOAEL = 5.4 mg a.i./kg-bw/day, respectively). Drinking water exposure alone was determined not to be a potential pathway of concern for avian/mammalian species on an acute and chronic basis (Appendix I). Although drinking water exposure alone does not appear to be of concern, this does not take into account that when aggregated with other exposure pathways (dietary food sources, dermal, inhalation) drinking water may contribute to a total exposure that has a potential for effects on non-target animals and should be explored further. Because there is a high degree of conservatism in the SIP 1.0 exposure estimate, there is limited expectation that use scenarios not triggering a SIP 1.0 concern would contribute significantly to aggregate risks from water plus diet when a refined water exposure model is incorporated in the actual quantitative risk assessment. Detailed information about SIP v.1.0, as well as the tool, can be found on the EPA’s website at

38 http://www.epa.gov/pesticides/science/models_pg.htm#terrestrial.

The Screening Tool for Inhalation Risk (STIR v.1.0, November 19, 2010) was used to calculate an upper bound estimate of exposure using picoxystrobin’s vapor pressure and molecular weight for vapor phase exposure as well as the maximum application rate and method of application for spray drift. STIR incorporates results from several toxicity studies, including acute oral and inhalation rat toxicity endpoints obtained from the “six-pack” of core studies, which are a series of six guideline studies that are submitted to the Registration Division of the Office of Pesticide Programs for technical and formulated products of a pesticide (LD50 >5000 mg a.i./kg-bw and LC50 = 3.19 mg/L, respectively) as well as the most sensitive acute oral avian toxicity endpoint (LD50 >486 mg a.i./kg-bw). Based on the results of the STIR model, inhalation exposure alone was determined not to be a potential pathway of concern for avian and mammalian species on an acute basis (Appendix I). Inhalation exposure via spray drift and vapor-phase of the pesticide alone does not appear to be of concern. The analysis of the inhalation route of in STIR does not consider that aggregation with other exposure pathways such as dietary, dermal, or drinking water may contribute to a total exposure that has a potential for effects to non-target animals. However, the Agency does consider the relative importance of other routes of exposure in situations where data indicate that pesticide exposures through other routes may be potentially significant contributors to wildlife risk (USEPA, 2004). The risk characterization section (Section IV), discusses the impact of consideration of other routes of exposure that have been identified as potentially important and the degree of certainty associated with screening-level risk assessment conclusions. Detailed information about STIR v.1.0, as well as the tool, can be found on the EPA’s website at: http://www.epa.gov/pesticides/science/models_pg.htm#terrestrial.

III.3.2. Terrestrial Plants

TerrPlant, a Tier I model, predicts EECs for terrestrial plants located in dry and semi-aquatic areas adjacent to the treated field. The active ingredient EECs are based on the application rate, soil incorporation, runoff fraction, drift fraction and solubility of the pesticide in water and drift characteristics, which depend on ground and aerial applications. The amount of picoxystrobin that runs off is a proportion of the application rate and is assumed to be 1% based on picoxystrobin’s solubility of 3.0 mg/L in water. Drift from ground and aerial applications are assumed to be 1% and 5%, respectively, of the application rate. An application efficiency of 100% is assumed for aerial application. For this terrestrial exposure assessment, ground and aerial application methods to plants for picoxystrobin are considered in TerrPlant.

For a standard scenario on an agricultural field when applications are occurring on land, EFED’s runoff scenario for terrestrial plants inhabiting dry areas adjacent to a field is characterized as “sheet runoff” (one treated acre to an adjacent acre: a 1:1 ratio) and inhabiting semi-aquatic or wetland areas adjacent to a field is characterized as “channelized runoff” (10 treated acre to a distant low-lying acre: a 10:1 ratio). The EECs for terrestrial and semi-aquatic plants for a single application of picoxystrobin at the maximum label rate for the proposed uses are presented in Table III.11. Details of the TerrPlant model are presented in Appendix G.

39 TABLE III.11. EECs for Terrestrial Plants Located Adjacent to Picoxystrobin (broadcast spray application) Treated Sites. Concentration (lbs a.i./A) Application Total Loading to Total Loading to Semi- Drift to Sites Method Areas Adjacent to Aquatic Areas Adjacent Adjacent Areas3 (Non-granular) Treated Areas1 to Treated Areas2 Ground Unincorp. 4 0.0039 0.02145 0.00195 All Proposed Uses Aerial 5 0.0117 0.02925 0.00975 1 EEC = Sheet Runoff + Drift (1% for ground; 5% for aerial) 2 EEC = Channelized Runoff + Drift (1% for ground; 5% for aerial) 3 EEC for ground (appl. rate x 1% drift); for aerial (appl. rate x 5% drift) 4 EEC for Unincorporated Ground Spray Application 5 EEC for Aerial Spray Application

III.4. Ecological Effects Characterization

Ecological effects studies have been submitted for picoxystrobin (technical grade: EPA Reg. No. 352-IGO), its transformation products, and the formulated product of picoxystrobin, picoxystrobin 250 g/L SC (EPA Reg. No. 352-IUN). In the ecological effects characterization section and in Appendix B, all exposure concentrations and toxicity values are expressed based on percent active ingredient (a.i.), transformation products (deg, unless identified as compound #1, 2, etc) and its formulated product (TEP).

Given that picoxystrobin is a new active ingredient with no previous registration in the U.S., it is assumed that no ecological incidents exist for picoxystrobin. With other strobilurins, probable incidents have been reported for phytotoxic effects on apples, almonds, bell peppers, corn, fern, gala apples, tobacco, ornamentals, peanut, cypress, soybean, sugar beet, and wheat. Most of the reports identified the route of exposure as drift, direct use on the crop, or carry-over. There was one report of azoxystrobin effects on a bald eagle (Incident No. I018723-002) and two reports of pyraclostrobin effects on fish (bluegill, bullhead, green sunfish, Johnny darter, largemouth bass, minnow, stoneroller, white sucker, and madtom) and honeybees (Incidents No. I020252-001 and I021220-001).

III.4.1. Aquatic Effects Characterization

III.4.1.1. Aquatic Animals

Freshwater Fish, Acute

The available freshwater fish toxicity data for picoxystrobin, transformation products, and TEP are summarized in Tables III.12, III.13, and III.14, respectively.

Fish toxicity studies for two freshwater species using the technical grade active ingredient (TGAI) are required to establish the acute toxicity of picoxystrobin to fish. The preferred test species are rainbow trout (a coldwater fish) and bluegill sunfish (a warm water fish). Acute studies submitted for the trout, sunfish, carp, minnow and stickleback categorize the TGAI as

40 very highly to highly toxic to freshwater fish on an acute toxicity basis. Results of the acute studies with freshwater fish indicate fathead minnow is the most sensitive fish to the TGAI; therefore, the minnow LC50 value of 65 µg a.i./L with the TGAI (Table III.14) is used to evaluate potential acute effects of the TGAI to freshwater fish. The guideline requirement for acute freshwater fish toxicity (MRIDs 48073769, 48073770, 48258008, 48258010 and 48258012) fulfills the OPPTS 850.1075 test guideline for acute toxicity of picoxystrobin to freshwater fish.

Table III.12. Freshwater Fish Acute Toxicity with Picoxystrobin TGAI. Species % a.i. 96-hour Mean- Toxicity MRID No. Study measured Category Author/Year Classification

LC50 (µg a.i./L) 48073769 Rainbow trout Very highly 96.6 70 A Kent & Shillabeer. Acceptable (Oncorhynchus mykiss) toxic (1996) 48073770 Bluegill sunfish Very highly 93.3 77 B Kent & Shillabeer. Acceptable (Lepomis macrochirus) toxic (1997) 48258010 Mirror carp Highly 93.3 160C Kent, Shillabeer & Acceptable (Cyprinus carpio) toxic Long. (1997) 48258008 Fathead minnow Very highly 93.3 65D Acceptable (Pimephales promelas) toxic Kent & Shillabeer. (1997)

Three-spined 48258012 stickleback Highly 93.3 100 E Acceptable (Gasterosteus toxic Kent & Shillabeer. aculeatus) (1997) A Trout 95% Confidence Interval = 49-100 µg a.i./L; probit slope = N/A (binomial method) B Sunfish 95% Confidence Interval = 67-108 µg a.i./L; probit slope = N/A (binominal method) C Carp 95% Confidence Interval = 130 - 210 µg a.i./L; probit slope = N/A (binomial method) D Minnow 95% Confidence Interval = 50-87 µg a.i./L; probit slope = N/A (binomial method) E Stickleback 95% Confidence Interval = 88-130 µg a.i./L; probit slope = N/A (binominal method)

In addition, the registrant provided acceptable acute studies with freshwater fish species using the major transformation products of picoxystrobin, Compound #7 (R408631 / QFA35), Compound #3 (R403814 / QFA75), Compound # 2 (R403092 / QDY62), Compound # 8 (R408509 / QDY63) and the minor transformation product, Compound # 26 (R413834 / QDY64). The freshwater fish 96-h LC50 for the products are all >10 mg deg/L (Table III.13), which indicates the transformation products are at least 154 times less toxic than the TGAI.

41 Table III.13. Freshwater Fish Acute Toxicity with Picoxystrobin Transformation Products. Species Transformation % Nominal Toxicity MRID No. Study

Product LC50 (mg deg/L) Category Author/Year Classification No more 48258014 than Compound # 7 >99 >10 Magor & Acceptable slightly Shillabeer. toxic (1997) No more 48258016 than Compound # 3 100 >10 Magor & Acceptable slightly Shillabeer. Fathead minnow toxic (1998) (Pimephales promelas) No more 48258018 than Compound # 2 99 >10 Magor & Acceptable slightly Shillabeer. toxic (1998) No more 48258020 than Compound # 8 100 >10 Magor & Acceptable slightly Shillabeer. toxic (1998) 48258022 Rainbow trout No more than Magor & (Oncorhynchus Compound # 26 98 >10 Acceptable slightly Shillabeer. mykiss) toxic (1999)

An acceptable acute freshwater fish study using the formulation product of picoxystrobin, picoxystrobin 250 g/L SC, provides information on the toxicity of the TEP to freshwater species. The freshwater fish 96-h LC50 for the TEP is 51 µg a.i./L (Table III.14), which indicates the TEP is as toxic as the TGAI.

Table III.14. Freshwater Fish Acute Toxicity with Picoxystrobin TEP. Species % a.i. 96-hour Toxicity MRID No. Study

LC50 (µg a.i./L) Category Author/Year Classification 51A 48073771 Rainbow trout Very highly 93.3 (220 µg Kent & Shillabeer. Acceptable (Oncorhynchus mykiss) toxic product/L) (1997) A Trout 95% Confidence Interval = 35-76 µg a.i./L; probit slope = N/A (binomial method)

Aquatic-phase Amphibians

No amphibian toxicity studies were submitted. Consequently, the freshwater fish toxicity data were used as a surrogate for aquatic-phase amphibian species, and toxicity between taxa is assumed to be similar.

Freshwater Invertebrates, Acute

The available freshwater invertebrate toxicity data for picoxystrobin, transformation products, and TEP are summarized in Tables III.15, III.16, and III.17, respectively.

42

A freshwater aquatic invertebrate toxicity test using the TGAI is required to establish the acute toxicity of picoxystrobin to aquatic invertebrates. The preferred test species is Daphnia magna, a water flea. Submitted data indicate the TGAI is categorized as very highly toxic to Daphnia magna with an acute 48-hour EC50 of 24 µg a.i./L (Table III.15). The daphnid EC50 value of 24 µg a.i./L with the TGAI is used to evaluate potential acute effects of the TGAI to freshwater invertebrates. The guideline requirement (OPPTS 850.1010) for acute freshwater invertebrate toxicity is fulfilled (MRID 48073764).

Table III.15. Freshwater Invertebrate Acute Toxicity with Picoxystrobin TGAI Species % 48-hour Mean- Toxicity MRID No. Study a.i. measured EC50 Category Author/Year Classification (µg a.i./L) 48073764 Water flea A Very highly 93.3 24 Kent & Shillabeer. Acceptable (Daphnia magna) toxic (1997) A Daphnid 95% C.I. = 18-32 μg a.i./L; Probit slope = N/A (binomial method)

In addition, the registrant provided acceptable acute studies with the freshwater invertebrate species, Daphnia magna, using the transformation products of picoxystrobin, Compound #7 (R408631 / QFA35), Compound #3 (R403814 / QFA75), Compound # 2 (R403092 / QDY62), Compound # 8 (R408509 / QDY63) and the minor transformation product, Compound # 26 (R413834 / QDY64). Results of the acute transformation product studies with daphnids indicate Compound #26 is the most sensitive transformation product to daphnids (Table III.16). A closer look indicates that transformation product Compound #26 is 333 times less toxic than the TGAI.

Table III.16. Freshwater Invertebrate Acute Toxicity with Picoxystrobin Transformation Products. Species Transformation % Nominal Toxicity MRID No. Study Product EC50 Category Author/Year Classification (mg deg/L) 48258015 No more than Magor & Compound # 7 >99 >10 Acceptable slightly toxic Shillabeer. (1998) 48258017 No more than Magor & Compound # 3 100 >10 Acceptable slightly toxic Shillabeer. (1998) Water flea 48258019 (Daphnia No more than Magor & Compound # 2 99 >10 Acceptable magna) slightly toxic Shillabeer. (1998) 48258021 No more than Magor & Compound # 8 100 >10 Acceptable slightly toxic Shillabeer. (1998) No more than Compound # 26 98 8.0A 48258023 Acceptable slightly toxic Magor &

43 Table III.16. Freshwater Invertebrate Acute Toxicity with Picoxystrobin Transformation Products. Species Transformation % Nominal Toxicity MRID No. Study Product EC50 Category Author/Year Classification (mg deg/L) Shillabeer. (1999) A Daphnid 95% C.I. = 6.7 – 9.3 mg a.i./L; Probit slope = 1.393

An acceptable acute freshwater invertebrate study using the formulation product of picoxystrobin, picoxystrobin 250 g/L SC, provides information on the toxicity of the TEP to freshwater invertebrate species. The freshwater invertebrate 48-h EC50 for the TEP is 20 µg a.i./L (Table III.17), which indicates the TEP is as toxic as the TGAI.

Table III.17. Freshwater Invertebrate Acute Toxicity with Picoxystrobin TEP. Species % a.i. 48-hour Mean- Toxicity MRID No. Study measured Category Author/Year Classification

EC50 (µg a.i./L) 20A 48073765 Water flea Very highly 93.3 (86 µg Kent & Shillabeer. Acceptable (Daphnia magna) toxic product/L) (1997) A Daphnid 95% Confidence Interval = 17-22 µg a.i./L; probit slope = N/A

Estuarine/Marine Fish, Acute

Acute toxicity testing with estuarine/marine fish using the TGAI is required for picoxystrobin because the end-use product is expected to reach this environment due to its potential use in coastal areas where corn, sorghum, soybean and wheat are grown. An acute toxicity study with the TGAI (Table III.18) was performed with the preferred test species, sheepshead minnow. The 96-hour LC50 is 330 µg a.i./L; therefore, the AI is categorized as highly toxic to estuarine/marine fish on an acute basis. EFED will use this TGAI value of 330 µg a.i./L to evaluate potential acute effects of the AI to estuarine/marine fish. The OPPTS guideline 850.1075 for estuarine/marine fish is fulfilled (MRID 48073768). No acute toxicity data with estuarine/marine fish tested with the TEP and transformation products were available and are not required because the TEP was as toxic as the TGAI while the transformation products were not as toxic as the TGAI in the freshwater animal and alga/diatom studies.

Table III.18. Estuarine/Marine Fish Acute Toxicity with Picoxystrobin TGAI. 96-hour Mean- Toxicity MRID No. Study measured LC Species % a.i. 50 Category Author/Year Classification (µg a.i./L)

Sheepshead minnow 48073768 99.3 330* Highly toxic Acceptable (Cyprinodon variegatus) Fournier. 2009. * Minnow 95% C.I. = 200-520 µg a.i./L; Probit slope = N/A (binomial method)

44 Estuarine and Marine Invertebrates, Acute

Acute toxicity testing with estuarine/marine invertebrates using the TGAI is required for picoxystrobin because the end-use product is expected to reach this environment due to its potential use in coastal areas where corn, soybeans, sorghum and wheat are grown. The preferred test species are mysid shrimp and Eastern oyster. Studies with Eastern oyster and mysid shrimp show that the TGAI is categorized as very highly toxic to these species (Table III.19) on an acute basis. Results of the acute studies with estuarine/marine invertebrates indicate that mollusk is more sensitive to the TGAI than shrimp; consequently, the EC50 value of 5.7 mg a.i./L for Eastern oyster is used to evaluate potential acute effects of the AI to estuarine/marine invertebrates. The OPPTS guidelines 850.1025 and 850.1035 for mollusks and shrimp, respectively, are fulfilled (MRIDs 48073766 and 48073767). No acute toxicity data with estuarine/marine invertebrates tested with the TEP and transformation products were available and are not required because the TEP was as toxic as the TGAI while the transformation products were not as toxic as the TGAI in the freshwater animal and alga/diatom studies.

Table III.19. Estuarine/Marine Invertebrate Acute Toxicity with Picoxystrobin TGAI 96-hour Mean- measured Toxicity MRID No. Study Species % a.i. LC50/EC50 Category Author/Year Classification (µg a.i./L) Eastern oyster 48073766 (shell deposition) A Very highly 99.3 EC50 = 5.7 Duncan and York. 2009. Acceptable (Crassostrea virginica) toxic Mysid B Very highly 48073767 99.3 LC50 = 33 Acceptable (Americamysis bahia) toxic Fournier. 2009. A Oyster 95% Confidence Interval = 1.7-25 µg a.i./L; Probit slope (95% C.I.) = N/A B Mysid 95% Confidence Interval = 24-46 µg a.i./L; Probit slope (95% C.I.) = N/A.

Freshwater Fish, Chronic

A freshwater fish early life-stage test using the TGAI is required to establish the chronic toxicity of picoxystrobin to freshwater fish. The preferred test species is the fathead minnow. EFED will use this NOAEC value of 36 µg a.i./L to evaluate potential chronic effects of the AI to freshwater fish. The OPPTS 850.1400 guideline is fulfilled (MRID 48073775). The available freshwater fish early life-stage toxicity data is summarized in Table III.20. Chronic freshwater fish data with the TEP and transformation products of picoxystrobin were not available and are typically not required because chronic exposure to TEP or transformation products is not expected.

45 Table III.20. Freshwater Fish Early Life-Stage Toxicity with Picoxystrobin TGAI Species % Mean- Mean- Endpoints MRID No. Study a.i. measured measured Affected Author/Year Classification NOAEC LOAEC (µg a.i./L) (µg a.i./L) Embryo Fathead minnow 48073775 hatching and (Pimephales 93.3 36 73 Kent and acceptable larval survival promelas) Shillabeer. 1997. and growth

Freshwater Invertebrate, Chronic

A freshwater aquatic invertebrate life-cycle test using the TGAI is required to establish the chronic toxicity of picoxystrobin to freshwater invertebrates. The preferred test is a 21-day life cycle with Daphnia magna. EFED will use the NOAEC of 1 µg a.i./L to evaluate potential chronic effects of the AI to freshwater invertebrates. The OPPTS guideline 850.1300 is fulfilled for MRID 48073772. The available freshwater invertebrate life cycle data is summarized in Table III.21. Chronic freshwater invertebrate data with the TEP and transformation products of picoxystrobin were not available and are typically not required because chronic exposure to TEP or transformation products is not expected.

Table III.21. Freshwater Invertebrate Life-Cycle Toxicity with Picoxystrobin TGAI Species % Mean- Mean- Endpoints MRID No. Study a.i. measured measured Affected Author/Year Classification NOAEC LOAEC (µg a.i./L) (µg a.i./L) 48073772 Water flea Kent, 96.6 1 2 Length Acceptable (Daphnia magna) Shallabeer. 1996.

Estuarine and Marine Fish, Chronic

An estuarine/marine fish early life-stage toxicity test using the TGAI is required to establish the chronic toxicity of picoxystrobin to estuarine/marine fish due to applications occurring in coastal counties, the acute estuarine/marine fish LC50 was 330 µg a.i./L which is less than 1 mg/L, and the reproductive physiology of freshwater species was effected. The preferred test is a 28-day life cycle with sheepshead minnow. EFED will use the NOAEC of 21 µg a.i./L to evaluate potential chronic effects of the AI to estuarine/marine fish. The OPPTS guideline 850.1400 is fulfilled for MRID 48073774. The available estuarine/marine fish early life stage data is summarized in Table III.22. Chronic estuarine/marine fish data with the TEP and transformation products of picoxystrobin were not available and are typically not required because chronic exposure to TEP or transformation products is not expected.

46 Table III.22. Estuarine/marine Fish Early Life-Stage Toxicity with Picoxystrobin TGAI Species % Mean- Mean- Endpoints MRID No. Study a.i. measured measured Affected Author/Year Classification NOAEC LOAEC (µg a.i./L) (µg a.i./L) Sheepshead minnow Growth 48073774 (Cyprinodon 99.3 21 49 (length and Acceptable Lee. 2009. variegatus) weight)

Estuarine and Marine Invertebrates, Chronic

An estuarine/marine invertebrate life-cycle toxicity test using the TGAI is required to establish the chronic toxicity of picoxystrobin to estuarine/marine invertebrates due to applications occurring in coastal counties, the acute estuarine/marine LC/EC50s ranged 5.7 to 33 µg a.i./L which are less than 1 mg/L, and the reproductive physiology of freshwater species was effected. The preferred test is a 28-day life cycle with the mysid (Americamysis bahia). EFED will use the NOAEC of 3.6 µg a.i./L to evaluate potential chronic effects of the TGAI to estuarine/marine invertebrates. The OPPTS guideline 850.1350 is fulfilled for MRID 48073773. The available estuarine/marine invertebrate life cycle data is summarized in Table III.23. Chronic estuarine/marine invertebrate data with the TEP and transformation products of picoxystrobin were not available and are typically not required because chronic exposure to TEP or transformation products is not expected.

Table III.23. Estuarine/marine Invertebrate Life-Cycle Toxicity with Picoxystrobin TGAI Species % Mean- Mean- Endpoints MRID No. Study a.i. measured measured Affected Author/Year Classification NOAEC LOAEC (µg a.i./L) (µg a.i./L) Mysid Offspring per 48073773 (Americamysis 99.3 3.6 7.6 Acceptable adult Lee. 2010. bahia)

III.4.1.2. Sub-lethal Effects

Sub-lethal effects observed in few acute aquatic organism studies included loss of equilibrium, lethargy, quiescence, sounding, dark discoloration, and lying on bottom at treatment levels higher than observed for mortality or immobilization. In addition to acute studies, the sublethal effects observed in the chronic studies were embryo hatching and larval survival, offspring per adult, and growth (length and weight). The observed sub-lethal effects in these chronic studies with fish and invertebrates occurred at levels higher than or equal to the NOAEC.

III.4.1.3. Field Studies

No field studies were submitted for use in this assessment.

47 III.4.2. Aquatic Plants

Aquatic Vascular and Non-Vascular Plants

The available aquatic plant toxicity studies for picoxystrobin, transformation products, and TEP are summarized in Tables III.24, III.25, and III.26, respectively.

Aquatic plant toxicity studies using the TGAI or TEP are required to establish the toxicity of picoxystrobin to non-target aquatic plants. The registrant submitted TGAI Tier II testing with five species; the species are freshwater green alga (Pseudokirchneriella subcapitata), duckweed (Lemna gibba), marine diatom (Skeletonema costatum), blue-green algae (Anabaena flos-aquae), and a freshwater diatom (Navicula pelliculosa). Of the four non-vascular species tested with the TGAI, the marine diatom is the most sensitive non-vascular plant. Results with one vascular species and four nonvascular species indicate that non-vascular species are more sensitive to picoxystrobin than vascular species. The 7-day EC50 for the vascular plant (duckweed) is 210 µg a.i./L (NOAEC = 20 µg a.i./L), based on frond density; and the lowest 4-day EC50 for the non- vascular plant (marine diatom) is 4 µg a.i./L (NOAEC = 2.3 µg a.i./L), based on cell density (Table III.24). The marine diatom and duckweed toxicity values will be used in the risk assessment to evaluate potential effects to aquatic plants. These aquatic plant toxicity studies (MRIDs 48073803, 48073804, 48073805 and 48258024) are scientifically sound and acceptable; however, the Navicula study is not scientifically sound and does not fulfill the OPPTS 850.5400 guideline requirement for a Tier II freshwater alga toxicity study. The Navicula study is required to be repeated to satisfy EPA guideline requirements.

Table III.24. Toxicity of Picoxystrobin TGAI to Nontarget Aquatic Plants - Tier II

Species % Mean- Mean- MRID No., Study a.i. measured measured Author/Year Classification EC50 NOAEC (µg a.i./L) (µg a.i./L) VASCULAR PLANTS Duckweed 48073803 99.3 210 A 20 Acceptable Lemna gibba Softcheck. 2010.

NON-VASCULAR PLANTS

Marine diatom 48073804 99.3 4 B 2.3 Acceptable Skeletonema costatum Softcheck. 2010.

Freshwater blue-green algae 48073805 99.3 >3000 C 3000 Acceptable Anabaena flos-aquae Dengler. 2010.

Freshwater diatom 48073806 99.3 N/A N/A Invalid1 Navicula pelliculosa Softcheck. 2010.

Freshwater green algae 48258024 Pseudokirchneriella 96.6 26 D 4.4 Smyth, Kent, Acceptable subcapitata Shillabeer. 1999.

48 Table III.24. Toxicity of Picoxystrobin TGAI to Nontarget Aquatic Plants - Tier II

Species % Mean- Mean- MRID No., Study a.i. measured measured Author/Year Classification EC50 NOAEC (µg a.i./L) (µg a.i./L) VASCULAR PLANTS Duckweed 48073803 99.3 210 A 20 Acceptable Lemna gibba Softcheck. 2010.

NON-VASCULAR PLANTS 1 High variation in blank control, potential hormesis, unsound statistical results with the blank control and significant difference in blank and solvent controls. A L. gibba 95% Confidence Interval = 150-300 µg a.i./L; Probit slope = 1.1. B S. costatum 95% Confidence Interval = 3.4-4.3 µg a.i./L; Probit slope = Not reported. C The EC50 was greater than the highest concentration; therefore, it was not possible to calculate its 95% confidence intervals and a probit slope. D P. subcapitata 95% Confidence Interval = 19-38 µg a.i./L; Probit slope = 1.6.

The registrant also provided acceptable and supplemental toxicity studies with the freshwater green algae Pseudokirchneriella subcapitata, using the transformation products of picoxystrobin, Compound #7 (R408631 / QFA35), Compound #3 (R403814 / QFA75), Compound # 2 (R403092 / QDY62), Compound # 8 (R408509 / QDY63) and the minor transformation product, Compound # 26 (R413834 / QDY64). Results of the transformation product toxicity studies with P. subcapitata indicate the EC50s are all >10 mg deg/L. However, significant effects were observed at the limit concentration in those studies except the Compound #2 study, for which the NOAEC could not be determined (NOAEC <10 mg deg/L). The NOAEC for the Compound #2 study is 10 mg deg/L (Table III.25). A closer look at the P. subcapitata data indicates that the transformation product EC50s are 385 times less toxic than the EC50 of the TGAI. No toxicity data with the duckweed, a vascular plant, tested with transformation products of picoxystrobin were available and are not required because the transformation products were not as toxic as the TGAI in the freshwater animal and alga/diatom studies.

49 Table III.25. Toxicity of Picoxystrobin Transformation Products to Nontarget Aquatic Non-Vascular Plants - Tier I. Species Transformation % Nominal Nominal MRID No. Study Product EC50 NOAEC Author/Year Classification (mg deg/L) (mg deg/L) 48258026 Compound #3 100 >10 <10 Smyth, Magor & Supplemental1 Shillabeer. (1998) 48258027 Compound #7 >99 >10 <10 Smyth, Magor & Supplemental1 Shillabeer. (1998) 48258028 Freshwater green algae Compound #2 99 >10 10 Smyth, Magor & Acceptable Shillabeer. (P.subcapitata) (1998) 48258029 Compound #8 100 >10 <10 Smyth, Magor & Supplemental1 Shillabeer. (1998) 48258030 Compound #26 98 >10 <10 Smyth, Magor & Supplemental1 Shillabeer. (1999) 1 A NOAEC could not be established at the limit concentration; other endpoints or a toxicity test with multiple levels to determine a NOAEC could be considered if the screening level risk assessment using this limit concentration exceeds the level of concern.

An acceptable aquatic non-vascular plant study using the formulation product of picoxystrobin, picoxystrobin 250 g/L SC, provides the results on the toxicity of the TEP to freshwater green algae species. The freshwater green algae 72-h EC50 for the TEP is 160 µg product/L; NOAEC = 45 µg product/L (corresponds to 40 µg a.i./L; 10 µg a.i./L, respectively), and the studies with the freshwater green algae species indicates the TEP is as toxic as the TGAI. The available freshwater green algae toxicity data for picoxystrobin TEP is summarized in Table III.26. Duckweed data with the formulation product of picoxystrobin was not available to evaluate the effects of the TEP to aquatic vascular plants and are not required because the TEP was as toxic as the TGAI in the freshwater animal and alga/diatom studies.

50 Table III.26. Toxicity of Picoxystrobin TEP to Nontarget Aquatic Plants - Tier II

Species % Mean- Mean- MRID No., Study a.i. measured measured Author/Year Classification EC50 NOAEC (µg a.i./L) (µg a.i./L) Freshwater green algae 40 A 10 48258025 Pseudokirchneriella 93.3 (160 µg (45 µg Smyth, Kent, Acceptable subcapitata product/L) product/L) Shillabeer. 1997. A P. subcapitata 95% Confidence Interval = 20-60 µg a.i./L; Probit slope = 2.2 (95% C.I. = 1.05 – 3.39).

III.4.3. Terrestrial Effects Characterization

III.4.3.1. Terrestrial Animals

Birds, Acute Oral

An acute oral toxicity study using the technical grade active ingredient (TGAI) is required to establish the acute toxicity of picoxystrobin to birds. The preferred guideline bird test species is either mallard duck (a waterfowl) or Northern bobwhite quail (an upland game bird), and a passerine bird. The registrant submitted data with bobwhite quail and zebra finch to establish the acute toxicity of picoxystrobin TGAI to birds via the oral route. The submitted acute data indicate that the TGAI is categorized as practically nontoxic to upland game birds (LD50 >2250 mg a.i./kg bw, the maximum dose tested). However, for passerines, it was not possible to categorize the toxicity of picoxystrobin to these species because 10, 40, and 70% of the passerines regurgitated in the three highest doses and sub-lethal effects of lethargy, ruffled appearance, prostrate posture and loss of righting reflex on day of dosing in 50% and 70% of birds dosed at the two highest dose levels that confounds the ability to determine the actual LD50. For this assessment, a non-definitive LD50 of >486 mg a.i./kg bw where no regurgitation, mortality, and clinical signs of toxicity occurred will be used as a screening-level endpoint for passerines (Table III.27). With the quail, a single mortality was observed in the highest dose level; however, a NOAEC based on sublethal effects was not reliable because the tests for the different doses were conducted at different times and the birds were coming from different sources and hatches. Thus, the bobwhite quail and zebra finch of >2250 and >486 mg a.i./kg bw, respectively, will be used to evaluate potential acute effects of the TGAI to non-passerines and passerines, respectively, via the oral route. The guideline requirement (OPPTS 850.2100) is partially fulfilled for acute oral toxicity to birds exposed to the TGAI. The quail (MRID 48073781) study is classified as acceptable. The finch study (MRID 48073780) is classified as supplemental because a definitive LD50 for mortality could not be obtained due to regurgitation observed in higher doses which introduce uncertainty as to their ingested dose. The available avian acute oral toxicity data are summarized in Table III.27. No avian acute oral toxicity data with the TEP and transformation products of picoxystrobin were available and are typically not required because exposure to TEP or transformation products is not expected.

51 Table III.27. Avian Acute Oral Toxicity with Picoxystrobin TGAI Species % a.i. Nominal Toxicity MRID No. Study LD50 Category Author/Year Classification (mg a.i./kg bw) Zebra finch 48073780 99.3 >486 Uncertain Supplemental1 (Poephila guttata) Hubbard & Beavers. 2009. Northern bobwhite Practically 48073781 quail 98.4 >2250 A Acceptable2 nontoxic (Colinus virginianus) Gallagher et al. 1998. A The LD50 was greater than the highest concentration; therefore, it was not possible to calculate a probit slope and 95% confidence intervals. 1 Non-definitive LD50; dose with no regurgitation, mortality, or clinical signs of toxicity were noted. Other endpoints or a toxicity test could be considered if the screening-level risk assessment using this non-definitive LD50 as a screening-level acute toxicity endpoint indicates the level of concern is exceeded. 2 Sub-lethal endpoints were not reliable and excluded as the tests for the different doses were conducted at different times and the birds were from different sources and came from different hatches. However, LD50 and NOAEC based on mortality from initial portion of the study are acceptable.

Birds, Subacute Dietary

Two dietary studies using the TGAI are required to establish the subacute toxicity of picoxystrobin to birds. The preferred test species are mallard duck (waterfowl) and bobwhite quail (upland game bird). The submitted data indicate no mortality occurred and that the 8-day acute dietary LC50 for duck and quail to be both >5200 mg a.i./kg diet, the maximum dose tested. Treatment-related reduction in weight gain for duck relative to the control were observed in the two highest dose levels, the sub-lethal effect NOAEC based on reduction in weight gain was 1300 mg a.i./kg diet. No sub-lethal effects were observed in the quail study. Therefore, the TGAI is categorized as practically non-toxic to upland game birds and waterfowl on a subacute dietary basis (Table III.28). Results of the acute dietary studies with birds indicate the duck and quail are both equally sensitive to picoxystrobin TGAI; therefore, the LD50 value of >5200 mg a.i./kg-diet will be used to evaluate potential acute effects of the TGAI to birds via the dietary route. The guideline (OPPTS 850.2200) is fulfilled for a subacute dietary study with birds. The available avian subacute dietary studies are summarized in Table III.28. No avian subacute dietary toxicity data with the TEP and transformation products of picoxystrobin were available and are typically not required because exposure to TEP or transformation products is not expected.

Table III.28. Avian Subacute Dietary Toxicity with Picoxystrobin TGAI

Species % a.i. Nominal LC 50 Toxicity MRID No. Study (mg a.i./kg-diet) Category Author/Year Classification Northern bobwhite 48073782 Practically quail 98.4 >5200 A Acceptable nontoxic Gallagher et al. (Colinus virginianus) 1998. 48073783 Mallard duck Practically 98.4 >5200 A Gallagher et al. Acceptable (Anas platyrhynchos) nontoxic 1998. A The LD50 was greater than the highest concentration; therefore, it was not possible to calculate a probit slope and 95% confidence intervals.

52

Mammals, Acute Oral

Wild mammal testing is required on a case-by-case basis, depending on the results of lower Tier laboratory mammalian studies, intended use pattern and pertinent environmental fate characteristics. In most cases, rat or mouse toxicity values obtained from the Agency's Health Effects Division (HED) substitute for wild mammal testing. These toxicity values are reported below in Table III.29.

The results indicate that the TGAI is categorized as practically non-toxic (LD50 >5000 mg a.i/kg- bw) to small mammals, while its formulated product is categorized as practically nontoxic (LD50 >2000 mg product/kg-bw, corresponds to >460 mg a.i./kg-bw) to rat on an acute oral basis. The LD50 value of >5000 mg a.i./kg-bw will be used to evaluate potential acute effects to mammals.

Table III.29. Mammalian Acute Toxicity for Picoxystrobin TGAI and Picoxystrobin 250 g/L SC. Nominal LD 50 Affected MRID No. Toxicity Species % a.i. Test Type (mg a.i./kg Endpoints Author, Year Category bw) Picoxystrobin TGAI Rat Practically 98 acute oral Females Mortality 48073718 (Sprague-Dawley) >50001 nontoxic Picoxystrobin 250 g/L SC Practically 23 acute oral >460 Mortality 48073720 Rat nontoxic 1 The LD50 was greater than the highest concentration; therefore, it was not possible to calculate a probit slope and 95% confidence intervals.

Reptiles and Terrestrial-phase Amphibians

No amphibian or reptile toxicity studies were submitted. Consequently, the avian toxicity data are used as a surrogate for terrestrial-phase amphibian and reptilian species, and toxicity between taxa is assumed to be similar.

Beneficial Insects, Acute

A honeybee acute contact study using the TGAI is required for picoxystrobin because its use as a fungicide treatment use will result in honeybee exposure (Table III.30). The acute contact LD50, using the honey bee, Apis mellifera, is derived from a laboratory study designed to estimate the quantity of toxicant required to cause 50% mortality in a test population of bees. The contact 48- h LD50 is >200 µg a.i./bee for the TGAI. In addition, the registrant provided studies using the formulation product of picoxystrobin. The contact 48-h LD50 for the formulated product is >200 µg a.i./bee. Results of the acute contact studies with honeybees indicate the TGAI and formulated product of picoxystrobin are practically non-toxic to bees on a contact exposure basis. The guideline (OPPTS 850.3020) is fulfilled. The contact tests (MRIDs 48073786 and 48073787) are classified as acceptable for the TGAI and TEP of picoxystrobin. The oral test is

53 not EPA guideline study; thus, is classified as supplemental. The available honeybee acute contact and oral studies are summarized in Table III.32.

Table III.30. Acute Contact and Oral Toxicity of Picoxystrobin TGAI and Picoxystrobin 250 g/L SC to Honeybees Species % a.i. Nominal Toxicity MRID No. Study LD50/LC50 Category* Classification (µg a.i./bee) Picoxystrobin TGAI

Practically non- >200 (contact) 48073786 Acceptable toxic Honey bee 93.3 Gough and Not able to test1 Jackson. 1997. Not categorized Supplemental † (oral) Picoxystrobin 250 g/L SC Practically non- 48073787 >200 (contact) Acceptable toxic Honey bee 22.5 Gough and † >200 (oral) Not categorized Jackson. 1997. Supplemental † Acute oral - a non-guideline study * The LD50s were greater than the highest concentration; therefore, it was not possible to calculate a probit slope and 95% confidence intervals. 1 Due to its low solubility in water, picoxystrobin could not be homogeneously dispersed in 50% w/w aqueous sucrose solution. Therefore, the acute oral toxicity of picoxystrobin to bees could not be tested.

Soil-dwelling Invertebrates, Subchronic

A subchronic toxicity study with earthworms using the typical end-use product of picoxystrobin (TEP) is available to establish the toxicity of picoxystrobin to soil-dwelling invertebrates. The submitted data indicate the 28-day LC50 and 56-day NOAEC for earthworms were >5 and 2.5 mg a.i./kg soil, respectively, and will be used to evaluate potential effects of picoxystrobin to soil-dwelling invertebrates in a soil environment. The available earthworm subchronic study is summarized in Table III.31.

Table III.31. Soil-Dwelling Invertebrate Subchronic Toxicity with Picoxystrobin 250 g/L SC Species % a.i. 28-D Mean- 56-D Mean- MRID No. Study measured LC50 measured Author/Year Classification (mg a.i./kg-soil) NOAEC (mg a.i./kg- soil) Earthworm 48073811 22.34 >5A 2.5 Acceptable (Eisenia fetida) Friedrich. 2003. A The LD50 was greater than the highest concentration; therefore, it was not possible to calculate a probit slope and 95% confidence intervals.

54 Birds, Chronic

Avian reproduction studies using the TGAI are required to establish the chronic toxicity of picoxystrobin to birds (Table III.32). The preferred test species are mallard duck and bobwhite quail. The data that were submitted show the reproduction NOAEC for duck and quail to be 157 and 1200 mg a.i./kg diet, respectively. Results indicate mallard duck is more sensitive to the TGAI than bobwhite quail with treatment-related reduction in the % of eggs set of eggs laid in the two highest dose levels with 76 and 81%, respectively, compared to 88% for the control level, the only parameter affected. No treatment-related effects on quails were observed. Therefore, the duck NOAEC value of 157 mg a.i./kg-diet is used to evaluate potential chronic effects of the TGAI to birds. The guideline (OPPTS 850.2300) is fulfilled. The duck and quail studies (MRIDs 48073784 and 48073785) are classified as acceptable. The available avian reproduction studies are summarized in Table III.32. No avian reproduction toxicity data with the TEP and transformation products of picoxystrobin were available and are typically not required because chronic exposure to TEP or transformation products is not expected.

Table III.32. Chronic Toxicity of Picoxystrobin TGAI to Bobwhite Quail and Mallard Ducks. Species % Mean- Mean- Affected MRID no. Study a.i. measured measured endpoints Author/Year classification NOAEC LOAEC (mg a.i./kg- (mg a.i./kg- diet) diet) Northern bobwhite quail 46073784 99.3 1200 >1200 None Acceptable (Colinus Temple et al. virginianus) 2010. Mallard duck 48073785 Egg 98.4 157 481 Acceptable (Anas reproduction Frey et al. platyrhynchos) 1998.

Mammals, Chronic

In the 2-generation reproduction studies (Table III.33) with rats exposed to the TGAI showed no reproductive effects; however, reduced body weight, body weight gains and other sub-lethal effects were observed. The lowest NOAEC value of 50 ppm (5.4 mg a.i./kg-bw/day) will be used to evaluate potential chronic effects of the TGAI to mammals. The available mammalian reproduction studies are summarized in Table III.33. No mammalian reproduction toxicity data with the TEP and transformation products of picoxystrobin were available and are typically not required because chronic exposure to TEP or transformation products is not expected.

55 Table III.33. Mammalian Reproductive Toxicity for Picoxystrobin TGAI.

Species % Test Toxicity Affected MRID No. a.i. Type ppm (mg a.i./kg bw/day) Endpoints Decreased body NOAEL = 1000 (55.6 in P weight, body males; 70.3 in P females) weight gains, Parental food LOAEL = 2500 (137.5 in P consumption and males; 173.4 in P females) lymphoid atrophy NOAEL = 2500 (137.5 in 99.3 48073739 Reproductive males; 173.4 in females) None LOAEL >2500 Decreased mean NOAEL = 1000 (55.6 in P Rat pup body males; 70.3 in P females) weight/litter, (Sprague Offspring Dawley) LOAEL = 2500 (137.5 in P body weight males; 173.4 in P females) gains, and organ weights Decreased body NOAEL = 50 (5.4) weight, body Parental weight gains, LOAEL = 200 (21.5) and food consumption 93.3 2-generation 48073740 NOAEL = 750 (87.2) Reproductive None LOAEL = >750 NOAEC = 200 (21.5) Decreased body Offspring LOAEC = 750 (80) weights

III.4.3.2. Sub-lethal Effects

Of all the acute studies with birds and mammals, sublethal effects were only observed in the mallard dietary and passerine oral studies which included reduced body weight gains in mallard and regurgitation, lethargy, ruffled appearance, prostrate posture, and loss of righting reflex in passerines at levels higher than for mortality. In addition to acute studies, the only sublethal effects observed in the chronic studies were reduced % egg set of egg laid in mallards and decreased body weight, body weight gain, food consumption, and mean pup body weight/litter and lymphoid atrophy. The observed sub-lethal effects in these chronic studies with birds and mammals occurred at levels higher than or equal to the NOAEC.

III.4.3.3 Field Studies

Data were not available to evaluate population recovery, age-class strengths, or shifts in species composition of terrestrial animals when exposed to picoxystrobin.

56

III.4.4. Terrestrial Plants

Terrestrial plant studies are required for all terrestrial outdoor pesticides. Tier I terrestrial plant toxicity studies were conducted to establish the toxicity of the TEP, picoxystrobin 250 g/L SC, at the maximum limit dose of 0.45 lb a.i./A to non-target terrestrial plants which was tested at doses higher than the maximum labeled application rate of 0.195 lb a.i./A. The recommendations for seedling emergence and vegetative vigor studies are for testing of (1) six species of at least four dicotyledonous families, one species of which is soybean (Glycine max), and the second of which is a root crop, and (2) four species of at least two monocotyledonous families, one of which is corn (Zea mays). Results indicate the plants were not inhibited 25% or more to the TEP at the limit dose. The EC25s are >0.45 lbs a.i./A for all monocotyledonous and dicotyledonous species tested and will be used a screening-level endpoint to assess risk to non-listed terrestrial plants. Because there was a significant reduction in both seedling emergence soybean and vegetative vigor cucumber, the most sensitive dicot of all dicots tested in the studies that a toxicity endpoint could not be established to assess risk to listed dicots and is assumed to be lower than the limit dose (<0.45 lb a.i./A). This leads to an uncertainty because significant phytotoxicity effects were seen at the limit dose which a definitive NOAEC could not established to assess the potential risk to listed dicots. Meanwhile, for listed monocots, there was a significant reduction in seedling emergence onion but not in vegetative vigor ryegrass; the most sensitive monocots of all monocots tested in the studies; and since there was a 17% reduction in dry weight for vegetative vigor ryegrass to 13% reduction in phytotoxicity for seedling emergence onion, ryegrass is the most sensitive monocot of all monocots. Thus, the vegetative vigor ryegrass NOAEC of 0.45 lb a.i./A will be used as a screening-level endpoint to assess risk to listed monocots. Both studies are scientifically sound but do not fulfill the guidelines (OPPTS 850.4100 and 850.4150) and are classified as supplemental because the NOAEC for the most sensitive dicot in both studies could not be determined and is significantly lower than the limit dose. If the limit dose at 0.45 lb a.i./A exceeds the level of concern (LOC) in the screening-level risk assessment, other endpoints or a multi-level study may be required to better evaluate potential effects to listed dicot plants. The description and classification of the available terrestrial plants studies are summarized in Tables III.34 and III.35.

57 Terrestrial Plants, Seedling Emergence

Table III.34. Summary of Tier I Seedling Emergence Results for Picoxystrobin 250 g/L SC * Significant Nominal Nominal Most sensitive % t-Test1,2 Study Species Effect? EC NOAEC endpoint Inhibition (p-value) 25 Classification (yes or no) (lb a.i./A) (lb a.i./A) 3 Corn Emergence 13 0.09 No >0.45 0.45 Supplemental Oat Emergence 11 0.52 No >0.45 0.45 Onion Phytotoxicity 13 0.017 Yes >0.45 <0.45 Ryegrass Dry weight 17 0.26 No >0.45 0.45 Cucumber Phytotoxicity 10 0.049 Yes >0.45 <0.45 Oilseed Rape None 0 n/a No >0.45 0.45 Pea Phytotoxicity 10 0.049 Yes >0.45 <0.45 Soybean Phytotoxicity 15 0.005 Yes >0.45 <0.45 Sugar beet Phytotoxicity 11 0.049 Yes >0.45 <0.45 Tomato Phytotoxicity 11 0.13 No >0.45 0.45 * 22.5% a.i picoxystrobin, tested at the limit dose of 0.45 lb a.i./A; MRID 48073801, Porch & Kendall. 2006. 1 A t-test is required when any endpoint exhibits >5% inhibition at the maximum dose when compared to negative control. For any endpoint with less than 5% inhibition, a t-test is not required. 2 A p-value of 0.05 or smaller indicates a significant effect at the maximum dose. 3 The NOAEC for the most sensitive dicot, soybean, of the limit concentration test could not be determined (<0.45 lb a.i./A). An NOAEC is needed to evaluate the impacts of picoxystrobin to listed dicots.

Terrestrial Plants, Vegetative Vigor

Table III.35. Summary of Tier I Vegetative Vigor Results for Picoxystrobin 250 g/L SC * Significant Nominal Nominal Most sensitive % t-Test1,2 Study Species Effect? EC NOAEC endpoint Inhibition (p-value) 25 Classification (yes or no) (lb a.i./A) (lb a.i./A) Corn None 0 n/a No >0.45 0.45 Oat Dry weight 4 n/a No >0.45 0.45 A Onion Dry weight 8 0.031 Yes >0.45 <0.45 Ryegrass Phytotoxicity 2 n/a No >0.45 0.45 Cucumber Phytotoxicity 20 7.6E-09 Yes >0.45 <0.45 Supplemental3 Oilseed Rape Height 8 n/a No >0.45 0.45 Pea None 0 n/a No >0.45 0.45 Soybean Phytotoxicity 8 0.0002 Yes >0.45 <0.45 Sugar beet Phytotoxicity 19 9.1E-10 Yes >0.45 <0.45 Tomato Phytotoxicity 8 0.012 Yes >0.45 <0.45

58 * 22.5% a.i. picoxystrobin, tested at the maximum application rate of 0.45 lb a.i./A; MRID 48073802 – Porch & Kendall, 2009. 1 A t-test is required when any endpoint exhibits >5% inhibition at the maximum dose when compared to negative control. For any endpoint with less than 5% inhibition, a t-test is not required. 2 A p-value of 0.05 or smaller indicates a significant effect at the maximum dose. 3 The NOAEC for the most sensitive dicot, cucumber, of the limit concentration test could not be determined (<0.45 lb a.i./A). An NOAEC is needed to evaluate the impacts of picoxystrobin to listed dicots. A The most sensitive endpoint, a 13% reduction in dry weight, for onion did not result in a significant effect at the limit concentration; however, a 8% effect for phytotoxicity was statistically significant (p = 0.031) at the limit concentration which the NOAEC for the endpoint is <0.45 lb a.i./A.

Non-Guideline Studies

Non-guideline studies that have been submitted by the registrant are summarized in Table III.36. These data are all classified as supplemental and if deemed useful, the data would be used qualitatively.

Table III.36. Summary of Non-Guideline Studies

Species % of LD50, (LOAEC) MRID No. Endpoint Affected or Comments Ingredient LC50, or / NOAEC Author/Year EC50 Earthworm TGAI (mg a.i./kg soil) Earthworm 48073819 93.3 6.7 (5.6) / 3.2 Mortality and body weight (Eisenia fetida) Jackson & Coulson. 1997. Earthworm TEP (mg a.i./kg soil) Earthworm (0.7) / 48073812 22.34 0.89 Mortality and body weight (Eisenia fetida) 0.47 Friedrich. 2002. Earthworm Transformation Products (mg degradate/kg soil) 99% (1000) / 48073817 >1000 Body weight R403092 100 Lees & Gough. 1999. Earthworm 100% (1000) / 48073816 320 Mortality and body weight (Eisenia fetida) R403814 100 Lees & Gough. 1998. 100% (1000) / 48073815 320 Mortality and body weight R408509 100 Lees & Gough. 1998. Earthworm Field Studies with Formulated Product (g a.i./ha) 48073807 93.3 N/A N/A Mortality higher when soil wetter Blake et al. No 48073808 14% sites where mortality exceeded Not reported significant N/A 5/m2 effects Coulson et al. 2003. Picoxystrobin applied up to 2 x 250 g No 48073809 a.i./ha is not expected to cause Not reported significant N/A unacceptable effects on earthworm effects Coulson et al. 2003. Earthworm populations in the field. populations Recovery of total earthworm populations occurred one year after application (374 DAA) with the (<62.5) / exception of the adult species number 168.5 g 48073810 Not reported <62.5g and biomass of Aporrectodea a.i./ha a.i./ha Klein. 2004. caliginosa at a rate of 62.5 and 125 g a.i./ha, respectively. At a rate of 500 g a.i./ha, a reduction in the number of earthworms was observed one year

59 Table III.36. Summary of Non-Guideline Studies

Species % of LD50, (LOAEC) MRID No. Endpoint Affected or Comments Ingredient LC50, or / NOAEC Author/Year EC50 after application, which is probably resulting from a slight reduction in juveniles. A single application of picoxystrobin at rates of 62.5, 125, 250 and 500 g a.i./ha did not result in significant effects on natural earthworm population in terms of total abundance or total biomass on the No 48073813 given test site. This equally applies to Not reported significant N/A A. caliginosa and endogeic A. Results effects Krück. 2003. of the species L. terrestris indicate a greater sensitivity which would be attributed to the surface feeding of this species since the test item showed no significant infiltration into deeper soil profiles. At rates of 250 and 500 g a.i./ha had a negative effect on natural earthworm population in terms of abundance and biomass on the given test site. At 250 g a.i./ha, earthworm populations fully recovered in the course of one year. An application rate of 500 g a.i./ha (>500) / 48073814 reduced total earthworm numbers by Not reported N/A 500 Krück. 2003. more than 50% (179 DAA). In the course of the following months, populations recovered, but were still reduced by approximately 39% in total earthworm numbers and 42% in total biomass after one year, the reduction in total numbers being statistically significant. Applied twice, at an interval of 14 days, to bare earth field plots at rates No 48073818 of 50, 125 and 250 g a.i./ha had no Not reported significant N/A adverse effects on naturally occurring effects Travis and Coulson. 1999. field populations of earthworms up to twelve months after application. Applied at 62.5 g a.i./ha, picoxystrobin resulted in no observed effects on either abundance or biomass of any earthworm taxonomic No 48073820 or ecological group. At application Not reported significant N/A rates up to and including 500 g effect Forster and Pease. 2003. a.i./ha, no effects of picoxystrobin on abundance or biomass of any taxonomic or ecological group were apparent by seven months after treatment. Parasite TGAI Parasitic wasp Mortality (100% in 250 and 500 g 48073821 a.i./ha groups). No LR could be Aphidius Not reported N/A N/A 50 Austin. 1997. estimated with two test rhopalosiphi concentrations.

60 Table III.36. Summary of Non-Guideline Studies

Species % of LD50, (LOAEC) MRID No. Endpoint Affected or Comments Ingredient LC50, or / NOAEC Author/Year EC50 Parasite Field Study with Formulated Product Mortality (68.8 and 77.1% on fresh Parasitic wasp residues (day 0) in 250 g a.i./ha 48073822 treatments applied once and twice, Aphidius Not reported N/A N/A Austin. 1999. respectively). No LR50 could be rhopalosiphi estimated with two test concentrations. Predator TGAI Mortality (56 and 49% at 250 and Predatory mite 48073824 500 g a.i./ha, respectively). No LR Not reported N/A N/A 50 Typhlodromus pyri Gill & Austin. 1997. could be estimated with two test concentrations. Predator Field Study with Formulated Product Green Lacewing 48073823 Mortality (32.6 and 25.9% on fresh Chrysoperla Not reported N/A N/A residues in 250 g a.i./ha treatments Brown. 1999. carnea applied once and twice, respectively) Sediment Studies 19 mg 5 mg 48073777 Chironomids 93.3 a.i./kg dry a.i./kg dry Total adult emergence Gentle. 1997. Chironomus weight weight riparius (46.7) / 48073778 93.3 56.4 Total adult emergence 19.6 Gentle & Rapley. 1997. Fathead minnow 48258009 Pimephales 93.3 56.8 49 Mortality Kent & Shillabeer. 1998. promelas Microcosm Study with Formulated Product No adverse effects on freshwater organisms following three applications at spray drift deposition Freshwater rates up to 100 g a.i./ha. Reductions 12 µg 48073779 organisms Not reported N/A of macroinvertebrates were observed a.i./litre population Cole et al. 1999. at 250 g a.i./ha, which showed no evidence of recovery. Others were reduced; however, recovered by end of the study. Aquatic Organisms (µg a.i./L) Rainbow trout 48258011 28-Day Subchronic LC for Oncorhynchus 93.3 27 10 50 Kent & Shillabeer. 1997. mortality mykiss Aquatic invertebrates (platyhelminthes, Range: 5 to 482548013 95.3 N/A Mortality rotatoria, mollusca, >4000 Farrelly & Prevo. 1996. annelida, insecta and crustacea)

61 IV. RISK CHARACTERIZATION

Risk characterization provides the final step in the risk assessment process. In this step, exposure and effects characterization are integrated to provide an estimate of risk relative to Agency’s established levels of concern (LOCs). The results are then interpreted for the risk manager through a risk description and synthesized into an overall conclusion.

IV.1. Risk Estimation - Integration of Exposure and Effects Data

A deterministic approach is used to evaluate the likelihood of adverse ecological effects to non- target species. In this approach, risk quotients (RQs) are calculated by dividing exposure estimates (EECs) by ecotoxicity values for non-target species, both acute and chronic.

RQ = EXPOSURE/TOXICITY

RQs are then compared to Agency's levels of concern (LOCs). These LOCs are criteria used by the Agency to indicate potential risk to non-target wildlife and the need to consider regulatory action. Exceedance of the LOC by the RQ indicates that a pesticide used as directed has the potential to cause adverse effects on non-target wildlife. LOCs currently address the following risk presumption categories: (1) acute risk - potential for acute risk to non-target animals which may warrant regulatory action in addition to restricted use classification, (2) acute restricted use – potential for acute risk to non-target animals, but may be mitigated through restricted use classification, (3) acute listed species – listed species may be potentially affected by use, (4) chronic risk – potential for chronic risk may warrant regulatory action, listed species may potentially be affected through chronic exposure, (5) non-listed plant risk - potential for effects in non-target (non-listed) plants, and (6) listed plant risk – potential for effects in listed plants. Currently, EFED does not perform baseline assessments for risk to plants or acute and chronic risks to non-target insects.

For acute studies on taxa where an LC/LD50 is not established due to insufficient mortality or no effects were observed, an RQ was not calculated, and the study is discussed further in the Risk Description section.

Risk presumptions, along with the corresponding RQs and LOCs are tabulated below in Tables IV.1, IV.2, and IV.3:

62 Table IV.1. Risk Presumptions for Terrestrial Animals Risk Presumption RQ LOC Birds: 1 2 3 Acute Risk EEC /LC50 or LD50/sqft or LD50/day ≥0.5 EEC/LC or LD /sqft or LD /day (or LD < 50 Acute Restricted Use 50 50 50 50 ≥0.2 mg a.i./kg) Listed Species EEC/LC50 or LD50/sqft or LD50/day ≥0.1 Chronic Risk EEC/NOAEC ≥1 Wild Mammals: Acute Risk EEC/LC50 or LD50/sqft or LD50/day ≥0.5 EEC/LC or LD /sqft or LD /day Acute Restricted Use 50 50 50 ≥0.2 (or LD50 < 50 mg a.i./kg) Listed Species EEC/LC50 or LD50/sqft or LD50/day ≥0.1 Chronic Risk EEC/NOAEC ≥1 Invertebrates: Listed Species EEC/LD50 ≥0.05 1 EEC=abbreviation for Estimated Environmental Concentration (mg a.i./kg) on avian/mammalian food items

2 mg/ft 3 mg of toxicant consumed/day

LD50 * wt. of bird LD50 * wt. of bird

Table IV.2. Risk Presumptions for Aquatic Animals Risk Presumption RQ LOC 1 Acute Risk EEC /LC50 or EC50 ≥0.5 Acute Restricted Use EEC/LC50 or EC50 ≥0.1 Acute Listed Species EEC/LC50 or EC50 ≥0.05 Chronic Risk EEC/NOAEC ≥1 EEC = (mg a.i./L or µg a.i./L) in water

Table IV.3. Risk Presumptions for Plants Risk Presumption RQ LOC Terrestrial Plants in Terrestrial and Semi-Aquatic Areas: 1 Non-Listed Plant Species EEC /EC25 ≥1 3 Listed Plant Species EEC/NOAEC or EC05 ≥1 Aquatic Plants: 2 Non-Listed Plant Species EEC /EC50 ≥1 3 Listed Plant Species EEC/NOAEC or EC05 ≥1 1 EEC = lbs a.i./acre 2 EEC = (µg a.i./L or mg a.i./L) in water 3 An EC05 is only used when a definitive NOAEC is not available.

The following section presents the acute and chronic risk quotients calculated for picoxystrobin and the LOCs (if any) that are exceeded. Further discussion of the risk quotients and uncertainties in the assessment is presented in Section IV.

IV.1.1. Non-target Aquatic Animals and Plants

For this baseline risk assessment with aquatic organisms and plants, acute and chronic risk quotients (RQs) were derived based on ecological toxicity data for the TGAI and then compared

63 to the EECs based on surface runoff combined with spray drift generated from the Tier II PRZM/EXAM model. RQs for Picoxystrobin 250 g/L SC and the transformation products were not calculated due to its low or equal toxicity compared to the TGAI and is discussed in the Risk Description section.

IV.1.1.1. Picoxystrobin Toxicity Endpoints Used to Assess Risk to Aquatic Organisms and Plants

Table IV.4 presents the most sensitive TGAI toxicity endpoint values selected from each taxonomic group to calculate acute and chronic risk quotients (RQs). These toxicity values were used to estimate risk to aquatic receptors from exposure to the TGAI through a combination of spray drift and surface runoff/leaching. Details of the acute and chronic EEC calculations for aquatic organisms and plants using PRZM/EXAMS are provided in Section III.2. The potential risks to aquatic organisms and plants are described further in the Risk Description section.

Table IV.4. Picoxystrobin TGAI Toxicity Endpoint Values Used for Assessing Risk to Aquatic Organisms and Plants Exposure Species Exposure Toxicity Endpoint Endpoint Reference Scenario Duration Value (Classification) Freshwater Fish MRID 48258008 Acute 96 hour LC = 65 µg a.i./L Survival 50 (Acceptable) Fathead minnow Survival, Pimephales promelas Early Life MRID 48073775 Chronic NOAEC = 36 µg a.i./L Reproduction, Stage (Acceptable) and Growth Freshwater Invertebrates MRID 448073764 Acute 48 hour EC = 24 µg a.i./L Immobility Water flea 50 (Acceptable) Daphnia magna MRID 48073772 Chronic Life-cycle NOAEC = 1 µg a.i./L Growth (Acceptable) Estuarine/Marine Fish

MRID 48073768 Acute 96 hour LC = 330 µg a.i./L Survival Sheepshead minnow 50 (Acceptable) Cyprinodon variegatus Early Life MRID 48073774 Chronic NOAEC = 21 µg a.i./L Growth Stage (Acceptable) Estuarine/Marine Invertebrates Eastern oyster MRID 48073766 Acute Crassostrea virginia 96 hour EC = 5.7 µg a.i./L Growth 50 (Acceptable) (shell deposition) Mysid MRID 48073773 Chronic Life Cycle NOAEC = 3.6 µg a.i./L Reproduction Americamysis bahia (Acceptable) Aquatic Plants Marine diatom EC = 4 µg a.i./L; MRID 48073804 Nonvascular 72 hour 50 Growth Skeletonema costatum NOAEC = 2.3 µg a.i./L (Acceptable) Duckweed EC = 210 µg a.i./L; MRID 48073803 Vascular 7 day 50 Growth Lemna gibba NOAEC = 20 µg a.i./L (Acceptable)

64 IV.1.1.2. Risk Quotient Calculations for Aquatic Organisms

There is a potential for exposure of the active ingredient to aquatic organisms, toxicity information on the TGAI are used to estimate the risks to aquatic organisms as a result of surface runoff and spray drift from multiple applications. The LD50 and EC50 is used to estimate acute risk for adverse effects on survival to fish and invertebrates, respectively, and the NOAEC is used to estimate chronic risk for adverse effects on reproduction and growth to both fish and invertebrates.

(1). Fish

Acute Risk Quotients of the TGAI The acute RQs for fish exceeded the Acute Restricted Use LOC of 0.1 and the Acute Listed Species LOC of 0.05 for freshwater fish inhabiting water bodies adjacent to sorghum, soybean and cornfields treated with picoxystrobin via ground or air. The acute listed species LOC of 0.05 (RQ=0.06) was exceeded for freshwater fish when applied via air twice at the maximum single application rate of 0.195 lb a.i./A to canola, legume vegetables, bean, pea, and cereal grain (except rice) fields; no LOC exceedance when picoxystrobin is applied to the ground twice. For estuarine/marine fish, no acute LOC exceedances occurred as a result of picoxystrobin applications. The results for acute risk to freshwater and estuarine/marine fish are provided in Table IV.5 and discussed further in the Risk Description section.

65

Table IV.5. Picoxystrobin Acute Risk Quotients for Freshwater Fish. PRZM Max. No. Peak Crop Scenario Single of PRZM/EXAMS Freshwater Fish Estuarine/marine Acute RQ 1 Fish Rate (lb Apps EEC 1 a.i./A) (µg a.i./L) (LC50= 65 µg Acute RQ a.i./L) (LC50= 330 µg a.i./L) Sorghum, MS 8.92 (aerial) 0.1** 0.03 0.195 3 Soybean soybean 8.90 (ground) 0.1** 0.03 Sweet Corn, field 8.74 (aerial) 0.1** 0.03 MS corn Variable2 4 corn, seed, popcorn 8.34 (ground) 0.1** 0.03 Canola, 3.62 (aerial) 0.06* 0.01 Legume vegetables MI bean 0.195 2 Dried 2.85 (ground) 0.04 <0.01 shelled beans, peas Cereal grains 3.57 (aerial) 0.06* 0.01 ND wheat Variable3 4 (except rice) 2.75 (ground) 0.04 <0.01 Bold value indicate LOC exceedance (**exceeds the Acute Restricted Use LOC of 0.1 and Acute Listed Species LOC of 0.05; *exceeds the Acute Listed Species LOC of 0.05) 1 Fish acute RQ = Peak EEC ÷ LC50 2 First application at 0.065 lb a.i/A, after 44 days 2nd, 3rd, 4th application at 0.195, 0.195, 0.13 lb a.i./A applied 7 days apart. 3 First application at 0.065 lb a.i/A, after 18 days 2nd, 3rd, 4th application at 0.195, 0.195, 0.13 lb a.i./A applied 7 days apart.

Chronic Risk Quotients of the TGAI For the proposed uses, the Chronic Risk LOC was not exceeded for freshwater and estuarine/marine fish from multiple applications. Using the highest estimated PRZM/EXAMS EEC for the aerial spray to the MS soybean use scenario (60-day aerial EEC value of 5.75 µg a.i./L) and the chronic NOAECs (36 µg a.i./L for freshwater fish and 21 µg a.i./L for estuarine/marine fish), the chronic RQs do not exceed the Chronic Risk LOC of 1. Chronic RQs for freshwater and estuarine/marine fish based on the other proposed uses with lower exposure scenarios including ground and aerial applications are also less than the LOC. The RQs for chronic risk to freshwater and estuarine/marine fish are provided in Table IV.6 and discussed further in the Risk Description section.

66

Table IV.6. Picoxystrobin Chronic Risk Quotients for Freshwater Fish. PRZM Max. No. Crop Scenario Single of 60-day Freshwater Fish Estuarine/marine PRZM/EXAMS Chronic RQ 1 Fish Rate Apps 1 (lb EEC (NOAEC = 36 Chronic RQ a.i./A) (µg a.i./L) µg a.i./L) (NOAEC = 21 µg a.i./L) Sorghum 5.75 (aerial) 0.16 0.27 MS and 0.195 3 soybean 5.59 (ground) 0.16 0.27 Soybean Bold value indicate LOC exceedance (*exceeds the Chronic Risk LOC of 1.0) 1 Fish chronic RQ = 60-day EEC ÷ NOAEC

(2). Aquatic-phase Amphibians and Reptiles

EFED currently uses surrogate data (freshwater fish) for aquatic-phase amphibians when data are not available. Risks are discussed in the Risk Description section.

(3). Invertebrates

Acute Risk Quotients of the TGAI The acute RQs of 0.5 – 1.6 for all the exposure scenarios considered in this assessment exceed the Acute Risk, Acute Restricted Use, and Acute Listed Species LOCs for estuarine/marine invertebrates inhabiting water bodies adjacent to sites with multiple picoxystrobin applications. The Acute Restricted Use and Acute Listed Species LOCs (RQ=0.1-0.4) were only exceeded for freshwater fish. The method of application (ground or aerial) used did not change the results. The results for acute risk to freshwater and estuarine/marine invertebrates exposed to picoxystrobin are provided in Table IV.7 and discussed further in the Risk Description section.

67

Table IV.7. Picoxystrobin Acute Risk Quotients for Invertebrates. PRZM Max. No. Peak Crop Scenario Single of PRZM/EXAMS FW E/M Rate (lb Apps EEC Invertebrates Invertebrates Acute RQ 1 Acute RQ1 a.i./A) (µg a.i./L) (EC50= 24 µg (EC50=5.7 µg a.i./L) a.i./L) Sorghum, MS 8.92 (aerial) 0.4** 1.6*** 0.195 3 Soybean soybean 8.90 (ground) 0.4** 1.6*** Sweet Corn, field 8.74 (aerial) 0.4** 1.6*** MS corn Variable2 4 corn, seed, popcorn 8.34 (ground) 0.4** 1.5*** Canola, Legume 3.62 (aerial) 0.2** 0.6*** vegetables MI bean 0.195 2 Dried shelled 2.85 (ground) 0.1** 0.5*** beans, peas Cereal grains 3.57 (aerial) 0.2** 0.6*** ND wheat Variable3 4 (except rice) 2.75 (ground) 0.1** 0.5*** Bold value indicate LOC exceedance (***exceeds the Acute Risk LOC of 0.5, Acute Restricted Use LOC of 0.1 and Acute Listed Species LOC of 0.05; **exceeds the Acute Restricted Use LOC of 0.1 and Acute Listed Species LOC of 0.05; *exceeds the Acute Listed Species LOC of 0.05) 1 Invertebrate acute RQ = Peak EEC ÷ LC50 2 First application at 0.065 lb a.i/A, after 44 days 2nd, 3rd, 4th application at 0.195, 0.195, 0.13 lb a.i./A applied 7 days apart. 3 First application at 0.065 lb a.i/A, after 18 days 2nd, 3rd, 4th application at 0.195, 0.195, 0.13 lb a.i./A applied 7 days apart.

Chronic Risk Quotients of the TGAI Chronic RQs for freshwater invertebrates exposed to multiple picoxystrobin applications were 2.3 to 7.3, which exceeded the Chronic Risk LOC for all proposed uses. For estuarine/marine invertebrates, the exceedance was for those inhabiting adjacent to sorghum, soybean, and cornfields (RQs = 1.9 – 2.0). No chronic LOC exceedance for estuarine/marine invertebrates exposed to picoxystrobin uses on canola, legume vegetables, bean, pea, and cereal grains. The method of application (aerial or ground) used did not change the results. The results for chronic risk to freshwater and estuarine/marine invertebrates exposed to picoxystrobin are provided in Table IV.8 and discussed further in the Risk Description section.

68

Table IV.8. Picoxystrobin Chronic Risk Quotients for Freshwater Invertebrates. PRZM Max. No. Crop Scenario Single of 21-day Freshwater Estuarine/marine PRZM/EXAMS Invertebrates Invertebrates Rate (lb Apps 1 1 a.i./A) EEC Chronic RQ Chronic RQ (µg a.i./L) (NOAEC = 1 (NOAEC = 3.6 µg µg a.i./L) a.i./L) Sorghum, MS 7.31 (aerial) 7.3* 2.0* 0.195 3 Soybean soybean 7.29 (ground) 7.3* 2.0* Sweet 7.12 (aerial) 7.1* 2.0* Corn, field MS corn Variable2 4 corn, seed, 6.75 (ground) 6.8* 1.9* popcorn Canola, Legume 2.97 (aerial) 3.0* 0.8 vegetables MI bean 0.195 2 Dried shelled 2.55 (ground) 2.6* 0.7 beans, peas Cereal 3.06 (aerial) 3.1* 0.9 grains ND Variable3 4 (except wheat 2.27 (ground) 2.3* 0.6 rice) Bold value indicate LOC exceedance (*exceeds the Chronic Risk LOC of 1.0) 1 Invertebrate chronic RQ = 21-day EEC ÷ NOAEC 2 First application at 0.065 lb a.i/A, after 44 days 2nd, 3rd, 4th application at 0.195, 0.195, 0.13 lb a.i./A applied 7 days apart. 3 First application at 0.065 lb a.i/A, after 18 days 2nd, 3rd, 4th application at 0.195, 0.195, 0.13 lb a.i./A applied 7 days apart.

IV.1.2. Risk Quotient Calculations for Aquatic Plants

There is a potential for exposure of the active ingredient to aquatic vascular and nonvascular plant species, toxicity information on the TGAI are used to estimate the risks to aquatic plants as a result of surface runoff and spray drift from multiple applications. The EC50 is used to estimate risk for adverse effects on growth to non-listed aquatic plants and the NOAEC is used to estimate risk for adverse effects on growth to listed aquatic plants.

(1). Non-listed Aquatic Plants

Non-listed Plant Risk Quotients of the TGAI According to peak PRZM/EXAMS EEC for the scenarios and toxicity values of the TGAI, the RQs of 2.1 to 2.2 for non-target aquatic non-vascular plants based on the marine diatom exceeded the Non-listed Plant Species LOC inhabiting sites adjacent to sorghum, soybean, and corn treated with picoxystrobin applications; no exceedance when picoxystrobin applications are occurring in canola, legume vegetables, beans, peas, and cereal grain fields. For aquatic vascular plants, there were no LOC exceedances, the RQs were all <0.1. The method of application used did not differentiate between ground and aerial. Results for risk to non-target (non-listed) aquatic

69 plants are provided in Table IV.9 and discussed further in the Risk Description section.

Table IV.9. Picoxystrobin Risk Quotients for Non-listed Aquatic Plants. Max. No. Peak Non-Listed Plant RQs1 PRZM Single of PRZM/EXAMS Duckweed Diatom Crop Scenario Rate (lb Apps EEC (EC50 = 210 (EC50 = 4 µg a.i./A) (µg a.i./L) µg a.i./L) a.i./L) Sorghum, MS 8.92 (aerial) <0.1 2.2* 0.195 3 Soybean soybean 8.90 (ground) <0.1 2.2* Sweet Corn, field 8.74 (aerial) <0.1 2.2* corn, seed, MS corn Variable2 4 popcorn 8.34 (ground) <0.1 2.1* Canola, 3.62 (aerial) <0.1 0.9 Legume vegetables MI bean 0.195 2 Dried shelled 2.85 (ground) <0.1 0.7 beans, peas Cereal grains ND 3.57 (aerial) <0.1 0.9 Variable3 4 (except rice) wheat 2.75 (ground) <0.1 0.7 Bold value indicate LOC exceedance (*exceeds the Non-listed Plant Species LOC of 1.0) 1 Non-listed plant RQ = peak EEC ÷ EC50 2 First application at 0.065 lb a.i/A, after 44 days 2nd, 3rd, 4th application at 0.195, 0.195, 0.13 lb a.i./A applied 7 days apart. 3 First application at 0.065 lb a.i/A, after 18 days 2nd, 3rd, 4th application at 0.195, 0.195, 0.13 lb a.i./A applied 7 days apart.

(2). Listed Aquatic Plants

Listed Plant Risk Quotients of the TGAI According to peak PRZM/EXAMS EEC for the scenarios and toxicity values of the TGAI, the RQs of 1.2-3.9 for listed aquatic non-vascular plants based on the marine diatom exceeded the Listed Plant Species LOC inhabiting sites adjacent to a picoxystrobin treated site. There was no LOC exceedance for aquatic vascular plants based on the duckweed endpoint, the RQs ranged 0.1 to 0.4. The method of application (aerial or ground) used did not change the results. Results for risk to endangered (listed) aquatic plants are provided in Table IV.10 and discussed further in the Risk Description section.

70 Table IV.10. Picoxystrobin Risk Quotients for Listed Aquatic Plants. Max. No. Peak Listed Plant RQs PRZM Single of PRZM/EXAMS Duckweed Diatom Crop Scenario Rate (lb Apps EEC (NOAEC = (NOAEC = 2.3 a.i./A) (µg a.i./L) 20 µg a.i./L) µg a.i./L) Sorghum, MS 8.92 (aerial) 0.4 3.9* 0.195 3 Soybean soybean 8.90 (ground) 0.4 3.9* Sweet Corn, field 8.74 (aerial) 0.4 3.8* corn, seed, MS corn Variable2 4 popcorn 8.34 (ground) 0.4 3.6* Canola, 3.62 (aerial) 0.2 1.6* Legume vegetables MI bean 0.195 2 Dried shelled 2.85 (ground) 0.1 1.2* beans, peas Cereal grains ND 3.57 (aerial) 0.2 1.6* Variable3 4 (except rice) wheat 2.75 (ground) 0.1 1.2* Bold value indicate LOC exceedance (*exceeds the Listed Plant Species LOC of 1.0) 1 Non-listed plant RQ = peak EEC ÷ NOAEC 2 First application at 0.065 lb a.i/A, after 44 days 2nd, 3rd, 4th application at 0.195, 0.195, 0.13 lb a.i./A applied 7 days apart. 3 First application at 0.065 lb a.i/A, after 18 days 2nd, 3rd, 4th application at 0.195, 0.195, 0.13 lb a.i./A applied 7 days apart.

IV.1.3. Non-target Terrestrial Animals

For this baseline risk assessment with birds and mammals, acute and chronic RQs are derived based on ecological toxicity data for picoxystrobin TGAI, and then directly compared to the dietary-based EECs generated from T-REX. For dose-based RQs, the EECs and toxicity values are first adjusted based on food intake and body weight differences of the terrestrial animals prior to the assessment. T-REX is discussed further below.

Brief Description of T-REX Modeling for Birds and Mammals

Formulas presented below in Table IV.11 are used to calculate dose-based and dietary based risk quotients:

71 Table IV.11. Formulas Used to Calculate Dose-Based and Dietary-Based Risk Quotients Duration Dose or Surrogate Equation Dietary RQ Organism

Acute Dose-based Birds and Acute Daily Exposure (mg/kg-bw) / adjusted LD50 (mg/kg- mammals bw)1,2

Dietary-based Birds Kenaga EEC (mg/kg-food item) / LC50 (mg/kg-diet)

Chronic Dietary-based Birds and EEC (mg/kg-food item) / NOAEC (mg/kg-diet) mammals Dose-based Mammals only EEC (mg/kg-bw) / Adjusted NOAEL (mg/kg-bw)2

1 (a-1) Adj. Bird LD50 = Bird LD50 (AW/TW) 2 0.25 Adj. Mammal LD50 or NOAEL = Mammal LD50 or NOAEL (TW/AW)

IV.1.3.1. Picoxystrobin Toxicity Endpoints Used to Assess Risk to Terrestrial Animals

Table IV.12 presents the TGAI toxicity endpoint values used to calculate RQs and estimate risk to terrestrial receptors from picoxystrobin residues as a result of direct deposition and spray drift from broadcast applications. The potential risks to terrestrial animals are described further in the Risk Description section.

72 Table IV.12. Picoxystrobin Toxicity Endpoint Values Used for Assessing Risk to Terrestrial Animals Exposure Species Exposure Toxicity Endpoint Value Endpoint Reference Scenario Duration (Classification) Mammal

Laboratory Single Oral MRID 48073718 Acute Oral LD >5000 mg a.i./kg bw Survival ray Dose 50 (Acceptable) Chronic Laboratory 2- NOAEC = 50 mg a.i./kg-diet MRID 48073740 Parental toxicity Reproduction rat generation (5.4 mg a.i./kg bw/day). (Acceptable) Birds

Single Oral 1 MRID 48073780 Acute Oral Zebra finch LD50 >486 mg a.i./kg bw None Dose (Supplemental)2

Mallard duck Subacute MRID 48073782 Anas 8 days LC >5200 mg a.i./kg-diet None Dietary 50 (Acceptable) platyrhynchos Mallard duck one NOAEC = 157 mg a.i./kg- Chronic Anas MRID 48073785 generation diet Egg reproduction platyrhynchos (Acceptable) Soil-dwelling Invertebrates

Earthworm LC >5 mg a.i./kg-soil Subchronic 28 days 50 Eisenia fetida NOAEC = 2.5 mg a.i./kg-soil Mortality 48073811 1 A non-definitive LD50; not the maximum dose test but the highest dose with no regurgitation observed, no mortality or clinical signs of toxicity were noted. 2 Other endpoints or a toxicity test could be considered if the screening-level risk assessment using the non-definitive LD50 as a screening-level endpoint indicates the level of concern is exceeded.

IV.1.3.2. Risk Quotient Calculations for Terrestrial Animals

There is a potential for exposure of the active ingredient to terrestrial animals, toxicity information on the TGAI are used to estimate the risks to terrestrial animals as a result of consuming selected feed items coated with picoxystrobin residues from multiple applications. The LD50 and LC50 are used to estimate acute risk for adverse effects on survival to both birds and mammals; the NOAEC is used to estimate chronic risk for adverse effects on reproduction and growth to both birds and mammals. Note: T-REX does not differentiate between aerial and ground applications, the method of application is not considered; thus, all aerial and ground applications are considered equivalent.

(1) Birds

Acute Risk Quotients of the TGAI There is a potential for acute exposure to birds via the oral and dietary routes, but acute RQs were not calculated because toxicity information on the TGAI was not established (acute oral LD50s >486 mg a.i./kg-bw (finch) and >2250 mg a.i./kg-bw (quail); acute dietary LC50s both >5200 mg a.i./kg-diet (quail and duck)). The potential for acute risk to birds is discussed in the Risk Description section.

73 Chronic Risk Quotients of the TGAI To evaluate the chronic risk of the TGAI to birds, chronic dietary-based RQs were calculated using the mallard duck NOAEC of 157 mg a.i./kg-diet. The chronic RQs are summarized in Table IV.13. Chronic dose-based RQs are generally not calculated due to difficulties in identifying an acceptable daily dose for birds.

The chronic dietary-based RQs did not exceed the Chronic Risk LOC for birds consuming short grass with the maximum amount of picoxystrobin residues. Using the most conservative T-REX dietary-based EEC (EEC value of 123 mg a.i./kg for short grass following picoxystrobin uses on soybean and sorghum) and the mallard duck NOAEC (157 mg a.i./kg-diet), the chronic RQs were all below the Chronic Risk LOC of 1 when consuming the selected feed items. Chronic RQs for all other proposed uses with lower exposure scenarios were also less than the Chronic Risk LOC (Table IV.13). The chronic risk to birds is discussed further in the Risk Description section.

Table IV.13. Upper Bound Kenaga, Chronic Avian Dietary-Based Risk Quotients for Picoxystrobin Uses EECs and RQs NOAEC Broadleaf Fruits/Pods/ Site (mg/kg- Short Grass Tall Grass Arthropods Plants Seeds diet) EEC RQ EEC RQ EEC RQ EEC RQ EEC RQ Sorghum, and 123 0.78 56 0.36 39 0.44 8 0.05 48 0.31 Soybeans1 Cereal 2 157 Grains 116 0.74 53 0.34 65 0.41 7 0.05 45 0.29 Corn3 112 0.72 52 0.33 63 0.40 7 0.04 44 0.28 Peas, Beans, 88 0.56 40 0.26 49 0.31 5.5 0.03 34 0.03 and Canola4 Size class not used for dietary risk quotients Bold values indicate LOC exceedances (*exceeds the LOC of 1 for chronic risk) 1 Exposure scenario based on 3 applications of 0.195 lb a.i./A with a 7-day reapplication interval 2 Exposure scenario based on 4 applications; first application at 0.065 lb a.i/A, after 18 days 2nd, 3rd, 4th application at 0.195, 0.195, 0.13 lb a.i./A applied 7 days apart. 3 Exposure scenario based on 4 applications; first application at 0.065 lb a.i/A, after 44 days 2nd, 3rd, 4th application at 0.195, 0.195, 0.13 lb a.i./A applied 7 days apart. 4 Exposure scenario based on 2 applications of 0.195 lb a.i./A with a 7-day reapplication interval

(2) Terrestrial-phase Amphibians and Reptiles

EFED currently uses surrogate data (birds) for terrestrial amphibians and reptiles when data are not available. Risks are discussed in the Risk Description section.

(3) Mammals

Acute Risk Quotients of the TGAI There is a potential for acute exposure to mammals via the oral route, but acute RQs were not

74 calculated because toxicity information on the TGAI was not established (acute oral LD50 >5000 mg a.i./kg-bw for the rat). The potential for risk to mammals is discussed in the Risk Description section.

Dietary-based RQs are not estimated for mammals since acute dietary mammal studies were not available.

Chronic Risk Quotients of the TGAI To evaluate the chronic risk to mammals, chronic dose-based and dietary-based RQs for the TGAI were calculated using the rat NOAEL of 5.4 mg a.i/kg-bw/day and NOAEC of 50 mg a.i./kg-diet, respectively, from the 2-generation study in rats. The chronic dietary-based and dose-based RQs are summarized in Table IV.14 and Table IV.15, respectively.

Assuming maximum residue levels of the proposed uses, the chronic dietary-based RQs of the TGAI exceed the Chronic Risk LOC for mammals (Table IV.14), the chronic dietary-based RQs of 2.5, 2.3, and 2.3 were all above the Chronic Risk LOC of 1 when consuming short grass with picoxystrobin residues following applications on sorghum and soybean, cereal grains, and corn, respectively; RQs were also above the chronic LOC when consuming tall grass and broadleaf plants. Following applications on peas, dried shelled beans and canola, the LOC is marginally exceeded for short grass (RQ = 1.8) but not for tall grass (RQ = 0.8) and broadleaves (RQ = 0.98). There were no chronic LOC exceedances for mammals consuming fruits/seeds/pods and arthropods following picoxystrobin applications (RQ <0.2).

Table IV.14. Upper Bound Kenaga, Chronic Mammal Dietary-Based Risk Quotients for Picoxystrobin Uses EECs and RQs NOAEC Broadleaf Fruits/Pods/ Site (mg/kg- Short Grass Tall Grass Arthropods Plants Seeds diet) EEC RQ EEC RQ EEC RQ EEC RQ EEC RQ Sorghum, and 123 2.5 56 1.1 69 1.4 7.7 0.2 48 0.96 Soybeans1 Cereal 2 116 2.3 53 1.06 65 1.3 7.2 0.1 45 0.9 Grains 50 Corn3 112 2.3 52 1.03 63 1.3 7.0 0.1 44 0.9 Peas, Beans, and 88 1.8 40 0.8 49 0.98 5.5 0.1 34 0.7 Canola4 Size class not used for dietary risk quotients Bold values indicate LOC exceedances (*exceeds the LOC of 1 for chronic risk) 1 Exposure scenario based on 3 applications of 0.195 lb a.i./A with a 7-day reapplication interval 2 Exposure scenario based on 4 applications; first application at 0.065 lb a.i/A, after 18 days 2nd, 3rd, 4th application at 0.195, 0.195, 0.13 lb a.i./A applied 7 days apart. 3 Exposure scenario based on 4 applications; first application at 0.065 lb a.i/A, after 44 days 2nd, 3rd, 4th application at 0.195, 0.195, 0.13 lb a.i./A applied 7 days apart. 4 Exposure scenario based on 2 applications of 0.195 lb a.i./A with a 7-day reapplication interval

75 Using the most conservative T-REX dose-based EECs of the exposure scenarios modeled and the laboratory rat NOAEL (5.4 mg a.i./kg-bw/day), the chronic dose-based risk quotients (RQs: 3.22-9.88) for the 15 g, 35 g, and 1000 g mammal weight classes all exceed the Chronic Risk LOC of 1 when consuming short grass with picoxystrobin residues following applications on the proposed uses (Table IV.15). The exceedance for all mammal weight classes is also presumed for those that depend on tall grass, broadleaves and insects as their food resource. No LOC exceedance as a result of consuming on fruits/pods/seeds and for granivores that depend on seed and grain.

These dietary-based and dose-based exceedances indicate that mammals may be at risk for adverse effects on reproduction and growth from chronic exposure to picoxystrobin as a result of the proposed uses and will be discussed in the Risk Description section.

Table IV.15. Upper Bound Kenaga, Chronic Mammalian Dose-Based Risk Quotients for Picoxystrobin Uses

EECs and RQs Size Adjusted Broadleaf Fruits/Pods/ Site Class Short Grass Tall Grass Arthropods Granivores NOAEL1 Plants Seeds (grams) EEC RQ EEC RQ EEC RQ EEC RQ EEC RQ EEC RQ Sorghum, 15 11.87 117.28 9.88 53.75 4.53 65.97 5.56 7.33 0.62 45.93 3.87 1.63 0.14 and 35 9.60 81.06 8.44 37.15 3.87 45.59 4.75 5.07 0.53 31.75 3.31 1.13 0.12 1 Soybeans 1000 4.15 18.79 4.52 8.61 2.07 10.57 2.55 1.17 0.28 7.36 1.77 0.26 0.06 15 11.87 110.30 9.29 50.55 4.26 62.04 5.23 6.89 0.58 43.20 3.64 1.53 0.13 Cereal 2 35 9.60 76.23 34.94 42.88 4.76 0.50 29.86 1.06 0.11 Grains 7.94 3.64 4.47 3.11 1000 4.15 17.67 4.26 8.10 1.95 9.94 2.39 1.10 0.27 6.92 1.67 0.25 0.06 15 11.87 107.12 9.03 49.10 4.14 60.26 5.08 6.70 0.56 41.96 3.54 1.49 0.13 Corn3 35 9.60 74.04 7.71 33.93 3.53 41.65 4.34 4.63 0.48 29.00 3.02 1.03 0.11 1000 4.15 17.17 4.13 7.87 1.89 9.66 2.32 1.07 0.26 6.72 1.62 0.24 0.06 Peas, 15 11.87 83.46 7.03 38.25 3.22 46.95 3.96 5.22 0.44 32.69 2.75 1.16 0.10 Beans, 35 9.60 57.69 6.01 26.44 2.75 32.45 3.38 3.61 0.38 22.59 2.35 0.80 0.08 and Canola4 1000 4.15 13.37 3.22 6.13 1.48 7.52 1.81 0.84 0.20 5.24 1.26 0.19 0.04 Bold values indicate LOC exceedances (excess the LOC of 1 for chronic risk) 1 The NOAEL of 5.4 mg a.i./kg-bw from the 2-generation reproduction study with rat was adjusted for body weight (size) classes; the adjusted NOAEL for a 15 g, 35 g, and 1000 g mammal is 12, 10, and 4 mg a.i./kg-bw, respectively. 1 Exposure scenario based on 3 applications of 0.195 lb a.i./A with a 7-day reapplication interval 2 Exposure scenario based on 4 applications; first application at 0.065 lb a.i/A, after 18 days 2nd, 3rd, 4th application at 0.195, 0.195, 0.13 lb a.i./A applied 7 days apart. 3 Exposure scenario based on 4 applications; first application at 0.065 lb a.i/A, after 44 days 2nd, 3rd, 4th application at 0.195, 0.195, 0.13 lb a.i./A applied 7 days apart. 4 Exposure scenario based on 2 applications of 0.195 lb a.i./A with a 7-day reapplication interval

(4) Beneficial Insects

Risk assessments are not conducted for beneficial insects at the screening-level at this time. Potential risks to beneficial insects are discussed in the Risk Description section of this document.

76

IV.1.4. Non-target Terrestrial Plants in Terrestrial and Semi-aquatic Environments

For this baseline risk assessment with terrestrial monocots and dicots, Non-listed and listed plant species RQs are derived based on ecological toxicity data for picoxystrobin and then compared to the TERRPLANT EECs for plants in non-target area receiving surface runoff combined with spray drift adjacent to the target area. Details of the TERRPLANT model and EECs are presented in Table III.10 and in Appendix F.

IV.1.4.1. Picoxystrobin Toxicity Endpoints Used to Assess Risk to Terrestrial Plants

Table IV.16 presents the toxicity endpoint values used to calculate RQs and estimate risk to non- listed and listed terrestrial plants from picoxystrobin residues as a result of direct deposition and spray drift from ground and aerial applications. Details of the RQ calculations for terrestrial plants are provided below and in Appendix F. The potential risks to terrestrial plants are discussed further in the Risk Description section.

Table IV.16. Picoxystrobin 250 g/L SC Toxicity Endpoint Values Used for Assessing Risk to Terrestrial Plants Exposure Species Exposure Toxicity Endpoint Endpoint Reference Scenario Duration Value (Classification)

Terrestrial Plants Monocot – EC >0.45 lb a.i./A; 25 None ryegrass NOAEC = 0.45 lb a.i./A Seedling Significant MRID 48073801 Emergence 1 Dicot – EC25 >0.45 lb a.i./A; difference (Supplemental) soybean NOAEC <0.45 lb a.i./A observed in phytotoxicity 21-day

Monocot - limit dose EC >0.45 lb a.i./A; 25 None onion NOAEC = 0.45 lb a.i./A

Vegetative MRID 48073802 Significant Vigor 1 Dicot – EC25 >0.45 lb a.i./A; difference (Supplemental) cucumber NOAEC <0.45 lb a.i./A observed in phytotoxicity 1 The NOAEC for the most sensitive dicot in the limit concentration test could not be determined (<0.45 lb a.i./A). An NOAEC is needed to evaluate the impacts of picoxystrobin to listed dicots.

IV.1.4.2. Risk Quotient Calculations for Terrestrial Plants Exposed to Picoxystrobin

There is a potential for exposure of the active ingredient to terrestrial plants, toxicity information on the TGAI are used to estimate the risks to non-target terrestrial plants inhabiting dry or semi-

77 aquatic areas adjacent to a treated field as a result of surface runoff and/or spray drift. The EC25 was used to estimate risk for adverse effects on growth to non-listed plant species while the NOAEC (or EC05 when a NOAEC is not available) was used to estimate risk for adverse effects on growth to listed plant species. Note: TerrPlant does not consider exposures to plants from multiple pesticide applications, thus, results are based on single pesticide applications.

(1) Non-listed and Listed Terrestrial Plants

Risk Quotients of Picoxystrobin 250 g/L SC to Non-Listed and Listed Monocots and Dicots

Table IV.17 presents RQs for the formulated product of picoxystrobin to terrestrial plants via ground and aerial spray applications. For the proposed uses of picoxystrobin and the maximum labeled application rate of 0.195 lbs a.i./A, LOCs were not exceeded for all non-listed dicots and non-listed/listed monocots located adjacent to treated areas, in semi-aquatic areas, and as a result of offsite runoff and/or spray drift. However, the toxicity threshold (NOAEC <0.45 lb a.i./A) for listed dicots was determined to be less than the limit dose test because a definitive NOAEC could not be established due to a significant effect observed in seedling emergence cucumber and vegetative vigor soybean; therefore, RQs for listed dicots were not calculated, and the risk to terrestrial monocots and dicots is described further in the Risk Description section.

Table IV.17. Terrestrial Plant Risk Quotient Summary for Picoxystrobin 250 g/L SC 1,2,3, 4

Non-listed RQs Listed RQs Scenario Terrestrial Semi-aquatic Terrestrial Semi-aquatic Drift Drift Adjacent area Adjacent area Adjacent area Adjacent area Maximum Labeled Rate for Picoxystrobin Uses (0.195 lb a.i./A) Ground spray Monocot <0.1 <0.1 <0.1 <0.1 <0.1 <0.1 Dicot <0.1 <0.1 <0.1 INC INC INC Aerial spray Monocot <0.1 <0.1 <0.1 <0.1 <0.1 <0.1 Dicot <0.1 <0.1 <0.1 INC INC INC 1Detailed calculations for RQs and TerrPlant Ver. 1.2.2 input and output are provided in Appendix G. 2 RQs for ground and/or aerial spray applications in this table were calculated using the maximum application rate for picoxystrobin uses (0.195 lb a.i./A). 3 Non-listed toxicity thresholds (EC25) were all >0.45 lb a.i./A for seedling emergence monocot, seedling emergence dicot, vegetative vigor monocot, and vegetative vigor dicot. 4 Listed toxicity thresholds (NOAEC) were 0.45 lb a.i./A for seedling emergence monocot and vegetative vigor monocot; while the seedling emergence dicot and vegetative vigor dicot were <0.45 lb a.i./A. INC – inconclusive; discussed further in the risk description

IV.2. Risk Description

The risk hypothesis states that the use of picoxystrobin as a fungicide for terrestrial crop sites has the potential to adversely affect survival, reproduction, and/or growth of non-target aquatic and terrestrial animals and plants, including Federally-listed endangered and threatened species. Based on the available ecotoxicity data and predicted environmental exposures, the hypothesis is

78 confirmed for potential adverse effects to fish, aquatic-phase amphibians, invertebrates, mammals and aquatic non-vascular plants (algae/diatoms) based on the proposed uses for picoxystrobin. Results of the risk estimation indicate terrestrial monocots and dicots and aquatic vascular plants (duckweed) were not affected and uncertain for birds, terrestrial-phase amphibians and reptiles. The following sections discuss the potential risks of picoxystrobin to these taxonomic groups.

IV.2.1. Risks to Aquatic Organisms and Plants

In the conceptual model, spray drift and surface runoff/leaching to adjacent bodies of water were predicted as the most likely sources of exposure of picoxystrobin to non-target aquatic organisms and plants. Risks to aquatic species (i.e. fish, invertebrates, and plants) were assessed based on modeled estimated environmental concentrations (EECs) and available toxicity data. The aquatic EECs for the ecological exposure to the acute and chronic toxicity values of the TGAI were estimated using PRZM/EXAMS (Table III.8).

Risk to Freshwater and Estuarine/marine Fish

(1) Risk to Fish Exposed to Picoxystrobin

Available acute toxicity data indicates that picoxystrobin is very highly toxic to freshwater fish and highly toxic to estuarine/marine fish on an acute basis. The most sensitive endpoint derived from the available studies for freshwater species (fathead minnow) and the sheepshead minnow study for estuarine/marine species were compared to several PRZM exposure scenarios for fish inhabiting adjacent to crops applied with picoxystrobin. All acute RQs (RQ = 0.06 – 0.1 (aerial application)) for freshwater species of the exposure scenarios representative of the proposed uses modeled exceeded the acute LOCs following picoxystrobin applications. In detail, the freshwater fish acute RQs exceeded the Acute Restricted Use and Acute Listed Species LOCs following picoxystrobin applications on soybeans, soyghums, and corn and only exceeded the Acute Listed Species LOC following picoxystrobin applications on canola, legume vegetables, peas, cereal grain (excluding rice), and dried shelled beans. For estuarine/marine fish five times less sensitive than freshwater fish, the estuarine/marine fish acute RQs do not exceed the Acute Listed Species LOC of 0.05 following multiple picoxystrobin applications (RQ = 0.03).

The EECs for the method of application (aerial or ground) utilized were similar and the risks to fish were the same whether application is occurring by air or ground for most proposed uses (field and sweet corn, wheat/barley, sorghum, and soybeans); with the exception for canola, legume vegetables, dried shelled bean, and pea uses that were only at risk when two applications of picoxystrobin is applied aerially. No risk to fish from these crops that were treated with two ground applications of picoxystrobin at the proposed maximum single application at 0.195 lb a.i./A.

Of the acute studies submitted, picoxystrobin was marginally less toxic to rainbow trout and bluegill sunfish than to the minnow; however, slightly more toxic than the mirror carp and three- spined stickleback; the range of sensitivity is narrow (LC50 range: 65 – 160 µg a.i./L). To assess the range of freshwater species affected when exposed to picoxystrobin, a comparison of the

79 least sensitive species (mirror carp LC50 of 160 µg a.i./L) and the highest PRZM/EXAMS EEC using the MS soybean scenario (8.92 µg a.i./L), the RQ is 0.06 and exceeds the acute listed species LOC of 0.05. Thus it is anticipated that a range of freshwater species would be adverse effected when exposed to picoxystrobin. With the acute estuarine/marine fish toxicity data limited, the range of estuarine/marine species adversely affected to picoxystrobin applications could not be assessed.

Sub-lethal effects to fish were minimal or mortality occurred before any effects were observed. Dark discoloration was reported in the rainbow trout study where the only symptom of toxicity was found in 2 out of 30 fish. Nevertheless, the study author identified the sub-lethal NOAEC to be several levels lower than for mortality; however, due to an insignificant percentage of trout affected, it unlikely that dark coloration is treatment-related. With acute estuarine/marine fish toxicity data limited to the sheepshead minnow, one fish was observed to be on the bottom of the test vessel and one fish was observed to have a partial loss of equilibrium; but at the 72-hour observation interval, all minnows that were observed to be lethargic at the highest level and then died at test termination occurred at levels higher than observed for mortality.

Following chronic exposure, the NOAEC for freshwater fish is 36 µg a.i./L due to significant reductions of embryo hatching, larval survival, and growth. The NOAEC for estuarine/marine fish is 21 µg a.i./L based on reduced length and weight. Chronic RQs for both freshwater and estuarine/marine fish resulted in no exceedance of the Chronic Risk LOC. The freshwater RQ of 0.16 and the estuarine/marine RQ of 0.27 are below the Chronic Risk LOC of 1.0. A comparison of the NOAECs of the TGAI with the highest 60-day PRZM/EXAMS EEC (5.75 µg a.i./L) indicates a small difference between the EEC and the concentrations that produced no significant reproductive or growth effects. A fish NOAEC value would need to be ≤5.75 µg a.i./L or 3.7 times lower to yield an RQ that exceeds the chronic risk LOC of 1.0.

Risk quotients for freshwater fish indicate that aquatic-phase amphibians are anticipated to be at risk for adverse effects on survival from exposures to the TGAI as a result of runoff and spray drift to adjacent water bodies following picoxystrobin treatments. In addition, an evaluation of the probit-dose response relationship using the default slope of 4.5 and the highest acute RQ for fish (RQ = 0.2) suggests the chance for acute direct effects to individual listed fish and aquatic- phase amphibians is 1 in 294,000. If the dose response curve was shallower (e.g., slope of 2), the chance of an individual mortality increases (1 in 44). On the other hand, the Chronic Risk LOC was not exceeded for freshwater fish; thus, aquatic-phase amphibians are not anticipated to be at risk for adverse effects on reproduction and growth when exposed to picoxystrobin.

Based on a bioconcentration study with bluegills, 86% of the steady state residues were depurated after 14 days, which indicates picoxystrobin is not expected to bioaccumulate in fish (Steady state whole fish BCF value = 290 µg/kg). An assessment of the Agency’s KABAM (KOW (based) Aquatic BioAccumulation Model) v1.0 model indicates bioaccumulation in fish or through the food chain is unlikely (Appendix H).

80 (2) Formulated Product, Transformation Products, Non-Guideline Studies, Etc.

Acute RQs for freshwater fish exposed to the formulated and transformation products are not calculated. Toxicity data of the formulated product (Picoxystrobin 250 g/L SC) with rainbow trout indicate the product is as toxic as the TGAI to freshwater fish on an acute basis. The toxicity of the formulated product appears to be from picoxystrobin in the formulation, since the toxicity of the product is similar to the TGAI. Five transformation product studies with freshwater fish species observed no significant mortality at the limit dose of 10 mg/L, the transformation products are at least 154 times less toxic than the TGAI.

Acute estuarine/marine fish toxicity data with the TEP and transformation products were not available. Chronic fish toxicity data (both freshwater and estuarine/marine) with the TEP and transformation products were not available.

A 28-day non-guideline fish prolonged toxicity study (MRID 48258011) with rainbow trout observed mortality and symptoms of toxicity such as surfacing, dark discoloration, sounding, loss of balance, reduced feeding, quiescence, hemorrhaging, skittering, gulping air, damaged fins, twitching, cataracts and irregular and rapid respiration at lethal concentrations of 18 µg a.i./L and higher, resulting in a 28-day LC50 and NOAEC of 27 and 10 µg a.i./L, respectively, based on mortality and nominal concentrations. The toxicity data indicate the LD50 of 27 µg a.i./L is the lowest endpoint for both acute and subchronic fish studies combined for freshwater species, indicating rainbow trout were more sensitive to picoxystrobin at 28 days than at 96 hours; in addition, the mortality NOAEC of 10 µg a.i./L in the 28-day fish prolonged study is more sensitive than the 32-day fish early life-stage NOAEC of 36 µg a.i./L (based on effects on reproduction and growth) with fathead minnows indicating the toxicity of picoxystrobin to fish’s survivability continues to persist after 28 days. However, the potential for chronic risk of adverse effects on reproduction and growth to fish is not expected because the 60-day EEC of 5.75 µg a.i./L does not exceed the 28-day and 32-day NOAECs of 10 and 36 µg a.i./L, respectively, to result in a LOC exceedance (LOC = 1.0) for potential chronic exposure to fish from picoxystrobin uses.

A 96-hour non-guideline toxicity study (MRID 48258009) with fathead minnow exposed to picoxystrobin in the presence of sediment observed 29% (44 dead/150 fish) mortality in the five treatment levels within the first 24 hours. After 48 hours, two additional mortalities were only observed for a total percent mortality of 31% at test termination. The results reported that the concentrations at test initiation were 100 – 127% of nominal and declined to 24 - 40% after 24 hours were likely due to sorption to the sediment as observed in a similar study with the chironomids (MRID 48073778) exposed to overlying water spiked with picoxystrobin.

(3) Risk Summary for Fish

Based on the available information, this ecological risk assessment for freshwater and estuarine/marine fish, including Federally-listed endangered and threatened species, suggests potential risk for adverse effects on survival to freshwater fish and aquatic-phase amphibians from acute exposure to picoxystrobin as a result of the labeled uses. However, there are no

81 concerns for adverse effect on survival to estuarine/marine fish from acute exposure to picoxystrobin and to both fish species from acute exposure to the transformation products. In addition, the potential risk for adverse effects on reproduction and growth to fish, both freshwater and estuarine/marine species, and aquatic-phase amphibians from chronic exposure are expected to be minimal.

Supplemental data suggest that the toxicity of picoxystrobin to fish is likely for a short period until the material binds to sediment, making picoxystrobin less toxic to fish from chronic exposure.

Risk to Freshwater and Estuarine/marine Invertebrates

(1) Risk to Invertebrates Exposed to Picoxystrobin

Registrant-submitted studies suggest that picoxystrobin is very highly toxic to both freshwater and estuarine/marine invertebrates. The most sensitive endpoint derived from the daphnid study for freshwater invertebrates and from the available studies for estuarine/marine invertebrates (Eastern oyster) were compared to several PRZM exposure scenarios for invertebrates inhabiting adjacent to crops applied with picoxystrobin. With oysters more acutely sensitive than daphnids, the acute RQs for estuarine/marine invertebrates exceeded the Acute Non-Listed Species, Acute Restricted Use, and Acute Listed Species LOCs following multiple picoxystrobin applications on the proposed uses as labeled, while the acute LOCs for restricted use and listed species was only exceeded for freshwater invertebrates. The highest RQ of 1.6 for estuarine/marine invertebrates exposed to picoxystrobin applications using the highest EEC was 32 times higher than the LOC threshold of 0.05 for acute risk to non-target estuarine/marine invertebrates.

The EECs for the method of application (aerial or ground) utilized were similar and the risks to invertebrates did not change whether application is occurring by air or ground for all proposed uses.

Of the acute studies submitted for estuarine/marine invertebrates, the crustacean (mysid) was less sensitive than the mollusk (Eastern oyster); the range of sensitivity is somewhat narrow (toxicity range: 5.7 – 33 µg a.i./L). To assess the range of estuarine/marine invertebrate species affected when exposed to picoxystrobin, a comparison of the least sensitive species (mysid LC50 of 33 µg a.i./L) and the most conservative PRZM/EXAMS EEC using the MS soybean scenario (8.9 µg a.i./L), the RQ is 0.3 and exceeds the acute LOC. Thus it is anticipated that a range of crustaceans and mollusks would both be adversely affected when exposed to picoxystrobin. With the acute freshwater invertebrate toxicity data limited, the range of freshwater invertebrates adversely affected by picoxystrobin applications were assessed using supplementary information in an exploratory study (MRID 48258013; Table IV.18), discussed below. The study shows the range of sensitivity of freshwater invertebrates to be wide indicating that not all freshwater invertebrate species were adversely affected.

Sub-lethal effects of lethargic and lying on the bottom of the vessels were only observed in mysids at levels higher than at the level where mortality occurred and were uncertain. Sub-lethal effects were not reported in the daphnid study. No mortality or sub-lethal effects were observed

82 in the oyster study; however, the reduction in shell deposition was 4 - 6 times lower than the acute toxicity endpoints in the mysid and daphnid studies.

Chronic RQ estimations for both freshwater and estuarine/marine invertebrates resulted in an exceedance of the Chronic Risk LOC for all PRZM exposure scenarios except for estuarine/marine invertebrates inhabiting bodies of water adjacent to canola, cereal grain (excluding rice), dried shelled bean, and pea sites exposed to ground or aerial picoxystrobin applications. The highest RQ of 7.3 based on the most conservative scenario for freshwater species was 7 times higher than the LOC threshold of 1.0 for chronic risk to non-target and listed freshwater invertebrates. For estuarine/marine invertebrates in bodies of water adjacent to canola, cereal grains, dried shelled bean, and pea sites treated with picoxystrobin as directed, the RQ was 0.8 and is below the chronic LOC of 1.0.

No acceptable EPA-guideline toxicity studies with sediment-dwelling invertebrates were available to analyze the toxicity of picoxystrobin to benthic invertebrates; however, available data from OECD-guideline studies, discussed below (MRIDs 48073777 and 48073778), and the chemical characteristics indicate that benthic invertebrates may be exposed to picoxystrobin uses. In addition, RQ estimations using the sediment porewater concentrations were found to exceed the Agnecy’s LOCs for acute and chronic risk to benthic invertebrates. In order to gain a better understanding of the potential risk to soil-dwelling invertebrates, the most sensitive endpoint derived from the available EPA-guideline studies for invertebrate species (Eastern oyster, daphnid, and mysid) were compared to PRZM sediment porewater EECs (Table III.9). In this exercise, the most sensitive acute endpoints (5.7 µg a.i./L, Eastern oyster; 24 µg a.i./L, daphnid) were compared to peak sediment porewater EEC (3.70 µg a.i./L) and the chronic endpoints (1 µg a.i./L, daphnid; 3.6 µg a.i./L, mysid) were compared to 21-day sediment porewater EEC (3.68 µg a.i./L). Given that peak EEC result in an acute RQ of 0.65 (oyster) and 0.15 (daphnid), the listed species LOC of 0.05 is exceeded for both species and the non-listed species LOC of 0.5 is exceeded for the most sensitive acute endpoint (oyster), there is a risk concern for acute exposure to listed and non-listed soil-dwelling invertebrates; the 21-day sediment porewater EEC result in a chronic RQ of 3.68 (daphnid) and 1.02 (mysid), the chronic LOC of 1.0 is exceeded for both non-listed and listed soil-dwelling invertebrates which satisfies one of the criteria for requiring whole sediment toxicity testing under 40 CFR Part 158. Submitted soil metabolism and aquatic metabolism studies indicate picoxystrobin is moderately persistence (aerobic soil t1/2: 29.4 – 73.7 days; aerobic aquatic metabolism t1/2: 39.2 – 47.5 days; anaerobic aquatic metabolism t1/2: 83.5 days). These half-life values are greater than 40 CFR Part 158 criterion of 10 days. The third set of trigger criteria for requiring chronic testing (Kd >50 or log Kow >3 or Koc >1000) is also met for picoxystrobin (log Kow is 3.6 and Koc values range from 741 to 1089). The physicochemical property triggers (log Kow and Koc) reflect the propensity of the chemical to partition onto the particulate or organic matter phases of sediment. Exceeding any one of the physicochemical property triggers listed above is sufficient for indicating the pesticide has reasonable potential for partitioning to the sediment compartment. The absence of these studies introduces uncertainty as to the effects of picoxystrobin on sediment-dwelling invertebrates. In addition, picoxystrobin has the potential to enter estuarine/marine water bodies based on current usage patterns (sweet and field corn, wheat, barley, sorghum, and soybeans) that include coastal counties. Until data are available, the risks to sediment-dwelling invertebrates cannot be precluded and are assumed.

83

(2) Formulated Product, Transformation Products, Non-Guideline Studies, Etc.

Acute RQs for freshwater invertebrates exposed to the formulated and transformation products are not quantitatively calculated. Picoxystrobin 250 g/L SC data indicates the formulated product is as toxic as the TGAI to freshwater invertebrates on an acute basis. The toxicity of the formulated product appears to be from picoxystrobin in the formulation, since the toxicity of the product is similar to the TGAI. Five transformation product studies with freshwater invertebrate species observed no significant mortality at doses up to 8 mg/L, which indicate the transformation products are at least 154 times less toxic than the TGAI.

Chronic freshwater invertebrate toxicity data with the formulated products were not available and are not needed because chronic exposure to the entire formulation is not expected to occur in the environment. No acute or chronic data on the formulated or transformation products for estuarine/marine invertebrates were available.

A 48-hr non-guideline toxicity study (MRID 48258013) with picoxystrobin to a range of freshwater aquatic invertebrates was assessed in an exploratory study for a period of 24 to 48 hours, depending on the taxa, to observe the range of sensitivity in those invertebrates. Nineteen different organisms representing most of the major taxa present in freshwater habitats were tested: Platyhelminthes (planarians), Rotatoria (rotifers), Mollusca (freshwater snails), Annelida (oligochaete worms and leeches), Insecta (Ephemeroptera, Odonata, Trichoptera, Diptera and Hemiptera) and Crustacea (Cladodera, Copepoda, Cyclopoda, Isopoda and Amphipoda). The 24- hour LC50 (for the rotifer, Brachionus) and 48-hour LC50s for all other species tested ranged from 5 to >4000 µg a.i./L (Table IV.18). Data on the toxicity of picoxystrobin to a variety of aquatic invertebrate species range from very highly toxic to no more than highly toxic with copepods the most sensitive species although the freshwater rotifer (B. calcyciflorus), snail (L. stagnalis), damselfly (C. puella), water-boatman (Notonecta sp.), creeping water bug (Naucoridae), and pond water flea (D. pulex) were not affected. Caution should be considered since the study was not in compliance with GLP standards as it was exploratory in nature; however, the range of sensitivity appears to be wide since not all freshwater species were impacted when exposed to picoxystrobin. Results of the exploratory study are provided below in Table IV.18.

84 Table IV.18. Effect of Picoxystrobin on Mortality/Immobilization of Aquatic Invertebrates. Test Organism 48-hour LC50 (µg a.i./L) Dugesia sp. – planarian 200-1000 Polycelis sp. – planarian 200-1000 Brachionus calcyciflorus – freshwater rotifer >4000 (24-hour LC50) Limnea stagnalis – freshwater snail >1000 Tubificidae (a mixture of Limnodrilus hofmeisteri and Tubifex sp.) 299 Erpobdella octoculata – leech 200-1000 Cloeon dipterum – mayfly, nymph 194 Coenagrion puella – damselfly, nymph >1000 Agrypnia varia – cased caddisfly larvae 158 Chaoborus crystallinus – phantom midge larva 332 Chironomus riparius – midge, 2nd instar larva 326 Notonecta sp. – water-boatman, adult >1000 Naucoridae – creeping water bug, adult >1000 Daphnia magna – water flea, first instar 18 Daphnia pulex – pond water flea >50 Macrocyclops fuscus – cyclopoid copepods, adults 5 Diaptomus sp. – calanoid copepods, adults 87 Asellus aquaticus – water louse, juvenile 152 Crangonyx pseudogracilis – freshwater shrimp, juvenile 63

An outdoor pond microcosm OECD-guideline study (MRID 48073779) to observe the effect of the Picoxystrobin 250 g/L SC formulation on communities of freshwater organisms (phytoplankton, zooplankton, and macroinvertebrates) for three months after the final application resulted in no adverse effects on zooplankton and macroinvertebrate communities at rates up to 100 g a.i./ha (0.044 lb a.i./A) and no effects to phytoplankton at the maximum labeled rate at 250 g a.i./ha (0.195 lb a.i./A). Four picoxystrobin treatments consisted 5, 30, 100 and 250 g a.i./ha representing spray drift rates of 2, 10, 40 and 100% of maximum field rate. Three direct applications of each treatment were made at two week intervals. A reduction in numbers of daphnia spp. were observed at 100 g a.i./ha but recovered rapidly within three weeks after the third application. Macroinvertebrates were adversely affected at 250 g a.i./ha, mostly notably after the third application, which included reductions in gammarids, dipteran larvae and mollusks, and increases in turbellarians that did not recovered during the study period. Following the third and final application, the reviewer-calculated depth integrated mean-measured concentrations were 0.54, 3.2, 12 and 29 µg a.i./L for the 5, 30, 100 and 250 g a.i./ha test rates, respectively. Therefore, with no effects observed up to 100 g a.i./ha, the NOAEC is determined to be 12 µg a.i./L based on the amount of picoxystrobin applied to microcosms for the 100 g a.i./ha treatment. The NOAEC in this study is also consistent with results of acute and chronic laboratory studies on daphnids, conducted with the TGAI or the formulated product. The 21-day NOAEC for Daphnia magna was 1 µg a.i./L (MRID 48073772; Kent and Shallabeer, 1996). The 48-h EC50 for Daphnia magna was 24 µg a.i./L for the TGAI (MRID 48073764; Kent and Shallabeer, 1997a), and 86 µg product/L for a 250 g/L SC formulation (equivalent to 20 µg a.i./L; MRID 48073765; Kent and Shallabeer, 1997b). However, according to the labels for the proposed uses, picoxystrobin is to be applied three times at a higher application rate of 250 g a.i./ha (corresponds to 0.195 lb a.i./A); it is anticipated that adverse effects to zooplankton and macroinvertebrates, the two of three communities reported in the microcosm study, would occur

85 following three picoxystrobin applications. Thus, the risk to freshwater invertebrates communities exposed to picoxystrobin may be mitigated following three applications at lower rates up to 100 g a.i./ha (corresponds to 0.044 lb a.i./A).

In a 25 day OECD-guideline static study (MRID 48073778) to observe the toxicity of picoxystrobin to sediment-dwelling chironomids (Chironomus riparius) exposed via overlying (spiked; not equilibrated) water resulted in a total emergence of 96%, 93%, 64%, 15%, 1.3%, 0% and 0% of introduced larvae in the blank control, solvent control, and 31.25, 62.5, 125, 250, 500, 1000, 2000 μg a.i./L (nominal) treatments, respectively. Even though the study does not meet EPA guidelines, results suggest the concentrations declined over the duration of the static study to 1-46% of nominal values and were likely from sorbing to the sediment as reported in a similar study with the fathead minnow in the presence of sediment (MRID 48258009).

In a 28 day OECD-guideline static study (MRID 48073777) to observe the toxicity of picoxystrobin to sediment-dwelling chironomids (Chironomus riparius) exposed via water- sediment system (spiked; not equilibrated) resulted in a total emergence of 90%, 93%, 93%, 93%, 87%, 73%, 50%, 0% and 0% of introduced larvae in the blank control, solvent control, and mean measured 1.2, 2.2, 5, 9.1, 20, 40 and 77 mg a.i./kg test concentrations, respectively. No emergence was observed in the two highest test concentrations (40 and 77 mg a.i./kg). No live larvae were found in sediments at study termination in any treatment. Last day of emergence in the control, solvent control, 1.2, 2.2, 5.0, 9.1 and 20 mg a.i./kg treatments was day 26, 25, 20, 23, 20, 24, and 20, respectively. While the study does not conform to EPA guidelines, it is worthwhile to note that the concentrations in the sediment at test termination were constant during the entire study (76-90% of nominal) and did not decline as observed in the spiked water studies, in addition to no live larvae in any treatment levels at test termination; data indicate picoxystrobin has the potential to bind to sediment and cause potential effects to sediment- dwelling organisms.

(3) Risk Summary for Invertebrates

Based on the available information, this ecological risk assessment for freshwater and estuarine/marine invertebrates, including Federally-listed endangered and threatened species, suggests potential risk for adverse effects on survival, reproduction and growth to freshwater and estuarine/marine invertebrates from acute and chronic exposure to picoxystrobin as a result of the proposed label uses. Risks to benthic invertebrates are assumed and cannot be precluded until available data indicate otherwise. Until the final OSCPP guidelines for chronic sediment toxicity tests are published, the registrant should submit a protocol to EFED for approval prior to test initiation. The data requested are as follow:

• Test Method 100.4: Hyalella azteca 42-d Test for Measuring the Effects of Sediment-associated Contaminants on Survival, Growth, and Reproduction in USEPA 2000 Methods for Measuring the Toxicity and Bioaccumulation of Sediment-associated contaminants with Freshwater Invertebrates EPA 600/R- 99/064 (OSCPP 850.1770, in prep.); • Test Method 100.5: Life-cycle Test for Measuring the Effects of Sediment- associated Contaminants on Chironomus dilates (formerly known as C. tentans)

86 in USEPA 2000 Methods for Measuring the Toxicity and bioaccumulation of Sediment-associated Contaminants with Freshwater Invertebrates EPA 600/R- 99/064 (OSCPP 850.1760, in prep.); and • Leptocheirus plumulosus in USEPA 2001 Method for Assessing the Chronic toxicity of Marine and Estuarine Sediment-associated Contaminants with the Amphipod Leptocheirus plumulosus EPA 600/R-01/020 (OCSPP 850.1780, in prep.)

There are no concerns for adverse effect on survival to freshwater invertebrates from acute exposure to the transformation products (degradates).

Supplemental data (MRID 48073779) indicate the risk to freshwater invertebrates could be mitigated following three picoxystrobin applications at a lower rate of 0.044 lb a.i./A than the proposed rate of 0.195 lb a.i./A. The range of sensitivity (MRID 48258013) for the nineteen different organisms representing most of the major taxa present in freshwater habitats appears to be wide (EC50s range: 5 - >4000 µg a.i./L) indicating not all freshwater invertebrate species were impacted when exposed to picoxystrobin.

Risk to Aquatic Vascular and Non-Vascular Plants

(1) Risk to Aquatic Plants Exposed to Picoxystrobin

The most sensitive EC50 derived from the duckweed study for aquatic vascular plants and from available studies for aquatic non-vascular plants (marine diatom) were compared to several PRZM exposure scenarios for plants inhabiting bodies of water adjacent to crops treated with picoxystrobin. Non-listed plant RQs for aquatic non-vascular plants using the marine diatom exceeded the Non-listed Plant Species LOC of 1 following multiple treatment on soybean, sorghum and corn (RQ = 2.2) but was not exceeded following applications on canola, cereal grains, legume vegetable, dried shelled bean and peas (RQ = 0.9). Non-listed plant RQs for aquatic vascular plants using the duckweed were all <0.1 which resulted in no LOC exceedance for risk to non-target (non-listed) aquatic vascular plants.

The most sensitive NOAEC derived from the duckweed study for aquatic vascular plants and from available studies for aquatic non-vascular plants (marine diatom) were compared to several PRZM exposure scenarios for plants inhabiting bodies of water adjacent to crops treated with picoxystrobin. Listed plant RQs for aquatic non-vascular plants using the marine diatom all exceeded the Listed Plant Species LOC of 1 following picoxystrobin applications on soybean, sorghum and corn (RQ = 3.9) and canola, cereal grains, legume vegetables, dried shelled bean, pea (RQ = 1.6). Listed plant RQs for aquatic vascular plants using the duckweed were all <0.4 which resulted in no LOC exceedance for risk to endangered (listed) aquatic vascular plants.

Of the acceptable algae/diatom studies submitted for aquatic non-vascular plants, the freshwater blue-green algae was the least sensitive (EC50 >3000 µg a.i./L) and the freshwater green algae (EC50 = 26 µg a.i./L) as sensitive as the marine diatom; the range of sensitivity is wide (toxicity range: 4 – >3000 µg a.i./L). To assess the range of aquatic non-vascular species affected when

87 exposed to picoxystrobin, a comparison of the least sensitive species (blue-green algae EC50 of >3000 µg a.i./L) and the most conservative PRZM/EXAMS EEC using the MS soybean scenario (8.9 µg a.i./L), the RQ is <0.003 and does not exceeds the acute LOC. Thus it is anticipated that the freshwater blue-algae would not be adversely affected and the freshwater green algae and marine diatom adversely affected when exposed to picoxystrobin. However, an uncertainty exists for aquatic non-vascular plants with the freshwater diatom, Navicula pelliculosa, study invalidated, it is uncertain if the marine diatom is the most sensitive species or whether freshwater diatoms as the one of the primary producers through the food chain are as sensitive to picoxystrobin as the freshwater green algae and marine diatom or least sensitive as the freshwater blue-green algae. Aquatic vascular plants data were limited to the duckweed study, the range of aquatic vascular plants adversely affected to picoxystrobin applications could not be assessed.

(2) Formulated Product, Transformation Products, Non-Guideline Studies, Etc.

RQs for aquatic plants exposed to the formulated product are not calculated. Picoxystrobin 250 g/L SC data indicates the formulated product is as toxic as the TGAI to the freshwater green algae, P. subcapitata, on an acute basis. The toxicity of the formulated product appears to be from picoxystrobin in the formulation, since the toxicity of the product is similar to the TGAI. Five transformation product studies with P. subcapitata observed no significant mortality at doses up to 10 mg/L, which indicate the transformation products are at least 154 times less toxic than the TGAI. Effects of Picoxystrobin 250 g/L SC and transformation products to marine diatom, the most sensitive aquatic plant, or to other submitted species were not available.

(3) Risk Summary for Aquatic Plants

This ecological risk assessment for aquatic plants, including Federally-listed endangered and threatened species, suggests potential risk for adverse effects on survival and growth to non- listed and listed non-vascular (algae and diatom species) plants from exposure to picoxystrobin as a result of proposed label uses. Additionally, there are no concerns for adverse effect on survival and growth to vascular (duckweed) plants from exposure to picoxystrobin and to both vascular and non-vascular plants from exposure to the transformation products.

There is uncertainty regarding the most sensitive endpoint used for non-vascular species due to lack of data on Navicula pelliculosa. If an acceptable Navicula study is submitted and is more sensitive than the endpoint used to assess risk, then risks may be underestimated for this taxonomic group. The submission of acceptable toxicity data with the freshwater diatom, N. pelliculosa would be useful in reducing the uncertainty. While the absence of this study represents an uncertainty in the risk assessment, requiring the data is low since it is unlikely to affect the risk conclusions for the proposed uses (e.g., risk to this taxa is already predicted for the proposed uses).

88 IV.2.2. Risks to Terrestrial Animals and Plants

In the conceptual model, dietary ingestion of picoxystrobin residues on vegetative matter and insects on treated areas are predicted as the most likely sources of picoxystrobin exposure to terrestrial animals. Spray drift, runoff and wind erosion of soil particles with resulting residues on upland and/or wetland foliage and soil are the most likely sources of picoxystrobin exposure to non-target terrestrial plants, including Federally-listed endangered and threatened species. Risks to terrestrial species (i.e. birds, mammals and plants) are assessed based on modeled estimated environmental concentrations (EECs) and available toxicity data. Terrestrial EECs for the ecological exposure to the acute and chronic toxicity values of the TGAI are estimated using T-REX (Tables III.9, III.10, and III.11) and TerrPlant (Table III.12).

Risk to Birds (1) Risk to Birds Exposed to Picoxystrobin

Available avian acute toxicity data indicates that picoxystrobin is practically nontoxic to upland game birds and waterfowls on an acute basis via either or both oral and dietary routes; however, uncertain for passerine birds. Acute RQs were not derived for birds in the Risk Estimation section of this assessment due to the non-definitive endpoints observed in the acute oral and dietary avian studies (e.g., >486 mg a.i./kg-bw, finch; >2250 mg a.i./kg-bw, quail; and >5200 mg a.i./kg-diet, both quail and duck).

The risk conclusion on the potential acute risk to birds is uncertain; additional passerine acute data is needed to address the uncertainty to fully assess the potential acute risk to all birds, including the smaller, passerines, species. In order to evaluate the potential acute risk to birds, the lowest acute toxicological endpoint of >486 mg a.i./kg-bw (the passerine study with zebra finch) selected from the submitted toxicological studies was compared to the highest EEC of 140.1 mg a.i./kg (residue on short grass following picoxystrobin application on soybean and sorghum). Calculations determined the acute endpoint to be greater than 0.1 of the acute ratio (acute listed species LOC = 0.1) indicating there is a potential risk to 20 g and 100 g birds consuming short grass and 20 g birds consuming tall grass, broadleaf plants and arthropods (Table IV.19). However, the uncertainty is that a definitive oral LD50 was not established in the passerine study with zebra finch due to regurgitation in 10%, 40%, 70% of passerines at the three highest doses (≥810 mg a.i./kg bw) and frank sub-lethal effects of lethargy, ruffled appearance, prostrate posture and loss of righting reflex on day of dosing occurred in 50% and 70% of the passerines dosed at the two highest doses and because of the problem with regurgitation at ≥810 mg a.i./kg bw, >486 mg a.i./kg-bw was used as an acute screening-level endpoint for passerines and in addition used as the lowest acute toxicological endpoint for all birds. Since the acute endpoint was calculated to be above the maximum expected exposure level, observation of >50% frank sub-lethal effects at environmentally relevant concentrations, and one incident report of probable azoxystrobin (a strobilurin) effects on a bald eagle (Incident No. I018723-002) suggest there is a potential risk for adverse effects on survival in addition to sub-lethal effects of ecological significance to passerines from the use of this pesticide. Therefore, the risk to all federally listed birds including the smaller, passerine, species and terrestrial-phase amphibians and reptiles from the use of picoxystrobin cannot be precluded until the uncertainty is addressed. In order to fully evaluate the potential risk to all birds including passerines, additional data are

89 needed on either an avian acute oral study with a passerine species if regurgitation does not occur up to or greater than 1400 mg a.i./kg or 10x the highest EEC (140 mg a.i./kg); or an modified subacute avian dietary LC50 toxicty test protocol for passerines where food consumption is monitored closely to generate an LD50, in addition to an LC50. In the absence of such data, risks to listed all birds including passerines and terrestrial-phase amphibians and reptiles will be assumed.

Table IV.19. Upper Bound Kenaga, Acute Avian Dose-Based Risk Quotients* EECs and RQs Size Adjusted Short Broadleaf Class Tall Grass Fruits/Pods Arthropods Seeds LD50 Grass Plants (grams) EEC RQ EEC RQ EEC RQ EEC RQ EEC RQ EEC RQ 20 512.71 140.1 0.27 64.21 0.13 78.8 0.15 8.76 0.02 54.9 0.11 1.95 <0.01 100 652.71 79.89 0.12 36.62 0.06 44.94 0.07 4.99 0.01 31.3 0.05 1.11 <0.01 1000 921.97 35.77 0.04 16.39 0.02 20.12 0.02 2.24 <0.01 14.0 0.02 0.5 <0.01 *Value in bold indicates RQ greater than acute listed species LOC of 0.1

Meanwhile, the non-definitive dietary value of >5200 mg a.i./kg-diet where no mortality or sub- lethal effects were observed at doses 30x the environmentally relevant concentrations, the risk to birds through the dietary route appears to be minimal.

Chronic avian RQs for all applications of picoxystrobin were below the Agency’s Chronic Risk LOC of 1.0, with a calculated maximum RQ of 0.98.

Based on results of the screening model SIP, drinking water exposure alone is not a concern for birds. Picoxystrobin has a relatively low solubility, which is the only parameter used in estimating potential exposure, and birds are not particularly sensitive to picoxystrobin on either an acute or chronic basis.

(2) Risk Summary for Birds Exposed to Picoxystrobin

Based on the available information, this ecological risk assessment for avian and terrestrial-phase amphibians and reptiles, including Federally-listed endangered and threatened species, suggests there is no indication of risk for adverse chronic effects on reproduction and growth to birds and terrestrial-phase amphibians and reptiles foraging on or near picoxystrobin-treated fields as a result of the label uses. However, the potential risk for adverse acute effects on survival to birds and terrestrial-phase amphibians and reptiles is uncertain since minimal effects were observed with the Northern bobwhite quail and mallard duck while >50% frank sublethal effects were observed with the passerine. Thus, the risk to birds cannot be completely precluded until additional data on the passerines are available to address the uncertainty. After an acute oral or subacute dietary toxicity test with the passerine bird is chosen, the registrant should submit a protocol to EFED for approval prior to test initiation. The data requested is as follows:

• OSCPP Guideline 850.2100: Avian Acute Oral Toxicity Test (with a passerine bird if regurgitation does not occur up to or greater than 1400 mg a.i./kg bw) or • OSCPP Guideline 850.2200: Avian Subacute Dietary Toxicity Test (a modified

90 protocol with a passerine bird to closely document food consumption and calculation of an oral LD50 value)

Risk to Mammals

(1) Risk to Mammals Exposed to Picoxystrobin

Available mammalian acute toxicity data indicates that picoxystrobin is practically nontoxic to mammals on an acute oral basis. Acute RQs were not derived for mammals in the Risk Estimation section of this assessment due to the non-definitive endpoint (>5000 mg a.i./kg-bw) where no mortality or sub-lethal effects occurred at the maximum dose tested. A comparison of the highest dose tested (rat LD50 >5000 mg a.i./kg-bw) and the most conservative T-REX EEC for a 15-gram mammal ingesting short grass (117 mg a.i./kg-bw), the highest RQ value is 0.01 or less than a dime of the Acute Listed Species LOC of 0.1. Given that the 15 g mammal is considered the most vulnerable, the potential for risk to mammals from acute exposure appears to be minimal.

Based on the most sensitive mammalian 2-generation NOAEL and upper bound T-REX EECs, the dose-based RQs of 1.26-9.8 exceed the Chronic Risk LOC for 15 g, 35 g and 1000 g mammals foraging on short grass, tall grass, broadleaves and arthropods following multiple picoxystrobin applications as proposed. For the dietary-based risk estimations, the results were similar; however, no LOC exceedances for mammals foraging on arthropods following multiple applications; and for applications on peas, dried shelled beans and canola, the LOC is marginally exceeded for short grass (RQ = 1.8) but not for tall grass (RQ = 0.8) and broadleaves (RQ = 0.98). There were no chronic LOC exceedances for mammals consuming fruits/seeds/pods. Thus, these exceedances indicate that mammals may be at risk for adverse effects on reproduction and growth from chronic exposure to picoxystrobin as a result of the labeled uses of the fungicide.

Considering the maximum single picoxystrobin application at 0.195 lbs a.i./A, the potential risk to adversely effect the reproduction and growth of mammals is unlikely; thus, reducing the number of applications would mitigate the risks to mammals. Graphs IV-1 through IV-3 illustrate the number of applications and days needed to exceed the chronic LOC for adverse effects to mammals foraging on its food resources in these proposed use fields. Graph IV-1 can be used to represent soyghum, soybean, canola, legume vegetables, dried shelled beans, and pea uses; Graph IV-2 for corn uses; and Graph IV-3 for cereal grains (excluding rice) uses.

Graph IV-1 below illustrates picoxystrobin applications on soybean and sorghum and canola, legume vegetables, dried shelled beans, and peas as directed on the labels. Pictured is the EECs following three applications of picoxystrobin at the maximum application rate of 0.195 lb a.i./A and since the soybean and sorghum uses and canola, legume vegetables, bean, and pea uses are applied at the maximum application rate of 0.195 lb a.i./A with the shortest reapplication interval of 7-days, they are grouped together in this graph; however, only a maximum of two picoxystrobin application is proposed for canola, legume vegetables, bean, and peas uses. Based on the graph, the upper-bound Kenaga dietary-based EECs exceed the LOC of 1 (NOAEC = 50 mg a.i./kg diet) for mammals foraging on short grass after the second application and on

91 broadleaves, arthropods and tall grass following three applications. Likewise, the number of days in exceedance of the LOC for chronic effects to mammals that forage on short grass in picoxystrobin-treated soybean and sorghum sites lasts for 46 days, 17 days on broadleaves and 7 days on tall grass. For picoxytrobin-treated canola, legume vegetables, bean, pea sites (not illustrated), the lethal concentration on short grass lasts 29 days. Graph for dose-based EECs is not available.

Graph IV-1. Number of applications and days needed to exceed the LOC of 1 for adverse effects of growth and reproduction to mammals following picoxystrobin applications on soybean, sorghum, legume vegetables, canola, bean, and peas per label directions.

92 Graph IV-2 below illustrates picoxystrobin applications on cereal grains excluding rice as directed on the labels. Based on the graph, the upper-bound Kenaga dietary-based EECs exceed the LOC of 1 (NOAEC = 50 mg a.i./kg diet) for mammals foraging on short grass after the second application and on broadleaves after the third and on tall grass following four applications as directed for cereal grains. Likewise, the number of days in exceedance of the LOC for chronic effects to mammals that forage on short grass in picoxystrobin-treated cereal grain sites lasts for 50 days, 12 days on broadleaves and 3 days on tall grass. Graph for dose- based EECs is not available.

Terrestrial Residues (upper bound estimates) vs 140.0 Mammalian Herbivore/Insectivore LOCs (as dietary concentrations

120.0

100.0

80.0

60.0

40.0

20.0

0.0Concentration (mg ai/kg dietary item) 0 Time (days) Short Grass Tall Grass Broadleaf plants Days Fruits/pods/seeds Arthropods Chronic LOC

Graph IV-2. Number of applications and days needed to exceed the LOC of 1 for adverse effects of growth and reproduction to mammals following picoxystrobin applications on cereal grains (excluding rice).

93 Graph IV-3 below illustrates picoxystrobin application as directed on the labels for corn use. Based on the graph, the EECs exceed the LOC for mammals foraging on short grass after the second application and on broadleaves after third and on tall grass following four applications. Likewise, the number of days in exceedance of the LOC for chronic effects to mammals that forage on short grass lasts for 52 days, 15 days on broadleaves and small insects and 2 days on tall grass. Graph for dose-based EECs is not available.

Terrestrial Residues (upper bound estimates) vs 120.0 Mammalian LOCs (as dietary concentrations)

100.0

80.0

60.0

40.0

20.0

0.0Concentration (mg ai/kg dietary item) 0 15 30 45 60 75 90 105 120 135 150 Time (days) Short Grass Tall Grass Broadleaf plants Days Fruits/pods/seeds Arthropods Chronic LOC

Graph IV-3. Number of applications and days needed to exceed the LOC of 1 for adverse effects of growth and reproduction to mammals following picoxystrobin applications on corn.

Based on results of the screening model SIP, drinking water exposure alone is not a concern for mammals. Picoxystrobin has a relatively low solubility, which is the only parameter used in estimating potential exposure, and mammals are not particularly sensitive to picoxystrobin on either an acute or chronic basis.

94 (2) Formulated Product, Transformation Products, Non-Guideline Studies, Etc.

Acute RQs for mammals exposed to the formulated product are not calculated. Picoxystrobin 250 g/L SC data indicates the formulated product is as toxic as the TGAI to mammals on an acute oral basis. The toxicity of the formulated product appears to be from picoxystrobin in the formulation, since the toxicity of the product is similar to the TGAI.

(3) Risk Summary for Mammals Exposed to Picoxystrobin

Based on the available information, this ecological risk assessment for mammals, including Federally-listed endangered and threatened species, suggests there is a potential chronic risk for adverse effects on reproduction and growth to mammals foraging on or near picoxystrobin- treated sites as a result of the label uses. There were no concerns for adverse effect on survival to mammals from acute exposure to picoxystrobin.

Risk to Terrestrial Monocots and Dicots

Based on the toxicity data presented in Ecological Effects section, the results indicate that for proposed uses, the Non-listed Plant Species and Listed Plant Species LOCs were not exceeded for terrestrial monocots and dicots located adjacent to treated areas, inhabiting semi-aquatic areas, and as a result of a combination of runoff and/or spray drift.

Even though an uncertainty exists in the terrestrial plant assessment because data was not available to evaluate the risk of picoxystrobin to listed dicots; the listed toxicity value (NOAEC) was <0.45 lbs a.i./A in the seedling emergence soybean and vegetative vigor cucumber limit- dose tests which a definitive screening-level endpoint cannot be used to evaluate risk to listed dicots. In order to draw a conclusion for listed dicots, TERRPLANT indicates a NOAEC would need to be ≤0.029 lb a.i./A to yield an RQ that exceeds the Listed Plant Species LOC of 1.0 or 16 times less than the limit dose tested. Although uncertainty exists regarding the potential risk to listed dicots given the significant effect observed at the limit dose in the seedling emergence soybean and vegetative vigor cucumber, the potential for risk to listed dicots from exposure to picoxystrobin appears to be minimal.

Based on the available information for terrestrial monocots and dicots, including Federally-listed endangered and threatened species, there is no indication of risk for adverse effects on survival and growth to terrestrial plants that inhabit dry and semi-aquatic areas adjacent to picoxystrobin- treated fields.

Risk to Terrestrial Invertebrates

a. Beneficial Insects

The available terrestrial insect toxicity data, based on tests with honeybees, suggest that the TGAI and its formulation product are practically non-toxic to bees on an acute contact basis. The LD50 values were all >200 µg a.i./bee. Risk to beneficial insects in the direct treatment area

95 exposed to picoxystrobin is expected to be minimal; consequently, precautionary labeling for honeybee protections is not required at this time.

b. Soil-dwelling Invertebrates

EFED does not regularly assess risk to non-target soil-dwelling invertebrates; however, the registrant submitted a subchronic earthworm toxicity test (MRID 48073811) to support the results that the risks to non-target terrestrial invertebrates are not expected. To assess the toxicity at environmentally relevant concentrations, the 28-day earthworm LC50 of >5.0 mg a.i./kg soil and 56-day NOAEC of 2.55 mg a.i./kg soil were compared with the estimated soil concentration for earthworms. To allow this type of assessment, the soil EEC is estimated by converting lb/A to mg/kg soil, the resulting EEC is 0.11 mg/kg soil assuming a soil depth of 15 cm and bulk density of 1.3 g/cm3. Using the estimated soil EEC of 0.11 mg/kg soil and the earthworm endpoints, the acute and chronic RQs were <0.02 and 0.04, respectively, which do not exceed the acute listed species LOC of 0.05 and the chronic risk LOC of 1.0, respectively. Thus, picoxystrobin is not expected to adversely affect non-target soil-dwelling invertebrates.

Field toxicity data on earthworms in United Kingdom, Germany, France, and Sweden indicate that picoxystrobin caused no significant effects at the relevant proposed rates. Some effects were observed such as the inconclusive analysis that showed significant (5/m2) surface earthworm mortality that received significant rainfall both before and after application of picoxystrobin; other studies had population recovery within the year after exposure to the compound.

c. Mites and Wasps

Supplemental acute data on the parasitoid wasp and mites exposed to picoxystrobin 250 g/L SC indicated mortality was high in wasp (100%) and moderate in mites (59-64%) in the 0.45 lb a.i./A and 0.9 lb a.i./A treatments. However, aged residue tests reported minimal effect on the fecundity of these parasitoid species. It is anticipated that picoxystrobin would have an initial effect on the mortality and fecundity of these species with a recovery in its populations immediately after picoxystrobin degrades over time. Thus, with a maximum annual rate of 0.585 lb a.i./A proposed for picoxystrobin, it is anticipated that the parasitoid species may be directly impacted when exposed to fresh residues of the test material following application; however, unlikely to be impacted when returning to 12-day aged residues.

96 V. FEDERALLY THREATENED AND ENDANGERED (LISTED) SPECIES CONCERNS

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 (USFWS) 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 reduce 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 Species 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 indirect 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 species 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 picoxystrobin on agricultural use sites it is expected that its use could occur nationwide.

V.1. Action Area

For listed species assessment purposes, the action area is considered to be the area affected directly or indirectly by picoxystrobin use and not merely the immediate area where picoxystrobin is applied. At the initial baseline, the risk assessment 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 located 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 relatively highest potential exposure to the pesticide, and that exposures are likely to decrease with distance from the treatment area. Section III.1 of this risk assessment presents the proposed pesticide use sites that are used to establish initial co-location of species with treatment areas.

97 V.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 taxon, and no further refinement of the action area is necessary. Furthermore, RQs below the listed species 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 listed 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 upon 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 an 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 downstream of the pesticide use site.

Assessment endpoints, exposure pathways, and the conceptual models addressing proposed new picoxystrobin uses, and the associated exposure and effects analyses conducted for the picoxystrobin baseline risk assessment are in Sections II to III. The assessment endpoints used in the baseline risk assessment include those defined operationally as reduced survival, growth and reproductive impairment for both aquatic and terrestrial animal species and survival and growth 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 authorize 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 IV.

Both acute listed species and chronic risk LOCs are considered in the baseline risk assessment to identify direct and indirect effects to taxa of listed species. This section identifies direct effect concerns, by taxon, 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 at the established listed 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 picoxystrobin, risk from chronic exposure is presumed for aquatic invertebrates and mammals. Potential acute risk to listed freshwater fish and aquatic-phase amphibians, freshwater and estuarine/marine invertebrates, alga/diatoms, and mammals is indicated based on exceedances of the LOC. However, the potential risk for acute effects to birds and terrestrial-phase amphibians and reptiles and for chronic effects to benthic invertebrates cannot be precluded until available data suggest otherwise.

Additionally, the results of the screen for indirect effects to listed species, using direct effect

98 acute and chronic LOCs for each taxonomic group, is presented and evaluated. For plants, if plant RQs fall between the listed plant species and non-listed plant species LOCs, the Agency concludes a no effect determination for listed species that rely on multiple plants species to successfully complete their life cycle (termed plant dependent species); alternatively, the Agency assumes a potential for adverse effects to those listed species that rely on a specific plant species in their life cycle (termed plant species obligates). If plant RQs for listed plant species are above the risk to plant LOCs (i.e., aquatic nonvascular plants), the Agency considered this to be indicative of a potential for adverse effects to those listed species that rely either on a specific plant species (plant species obligate) or multiple plant species (plant dependent) for some important aspect of their life cycle.

Table V.1. Listed Taxonomic Groups Potentially at Risks associated with Direct or Indirect Effects as a Result of the Proposed Uses of Picoxystrobin. Listed Taxon Direct Effects from Direct Effects from Indirect Effects a Acute Exposures Chronic Exposures

Aquatic Aquatic non-vascular plants Yes N/A Yes Aquatic vascular plants No N/A Yes Freshwater invertebrates Yes Yes Yes Marine/estuarine invertebrates Yes Yes Yes Benthic invertebrates Yes Cannot be precluded Yes Freshwater fish Yes No Yes Marine/estuarine fish No No Yes Aquatic-phase amphibians Yes No Yes Terrestrial Semi-aquatic plants - monocots No N/A Yes Semi-aquatic plants - dicots No N/A Yes Terrestrial plants – monocots No N/A Yes Terrestrial plants - dicots No N/A Yes Soil-dwelling invertebrates No No Yes Birds Cannot be precluded No Yes Terrestrial-phase amphibians Cannot be precluded No Yes Reptiles Cannot be precluded No Yes Mammals No Yes Yes N/A - indicates that this exposure route is not assessed. a until an endangered species assessment is complete, indirect effects to all species cannot be precluded

V.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

99 chance of an individual event (i.e., mortality or immobilization) should exposure at the EEC actually occur for a species with sensitivity to picoxystrobin on par with the acute toxicity endpoint selected for RQ calculation. To accomplish this interpretation, 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 probability 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 probability are also provided to account for variance in the slope, if available. Based on the available acute toxicity for picoxystrobin, a summary of the probit dose-response analysis is provided in Table V.2. If no dose response information is available to 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 Chance 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 parameter 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 highest calculated acute RQ following three, two and one application(s), if available.

Table V.2. Summary of Picoxystrobin Probit Dose Response Analysis for Listed Species Chance of Individual Effect Chance of Individual Effect at Acute Effect Taxa (study type) at Listed Species LOC Derived Acute RQ (95% Slope (95% C.I.) (95% C.I.) C.I.)1,2,3 No mortality observed for Not calculated; no mortality Not calculated; no mortality Bird oral dose upland game birds; observed observed uncertain for passerines Not calculated; no mortality Not calculated; no mortality Bird dietary No mortality observed observed observed 1 in 2.94E+5 Mortality A 1 in 4.18E+08 (1 in 44 to 1 in 8.86E+18) Fish Default Slope = 4.5 (1 in 216 to 1 in 1.75E+31) (2 – 9) 1 in 5.22E+7 (1 in 138 to 1 in 5.04E+27)B 1 in 27.3 Immobilization C Freshwater 1 in 4.18E+08 (1 in 5 to 1 in 5850) Default Slope = 4.5 Invertebrates (1 in 216 to 1 in 1.75E+31) 1 in 121 (2 – 9) (1 in 12.3 to 1 in 6.33E+8)D 1 in 1.22 Shell deposition E Estuarine/marine 1 in 4.18E+08 (1 in 1.52 to 1 in 1.03) Default Slope = 4.5 Invertebrates (1 in 216 to 1 in 1.75E+31) 1 in 6.29 (2 – 9) (1 in 3.04 to 1 in 43.6)F 1 Highest acute RQ for fish = A 0.1 (soybean, sorghum, corn uses); B 0.06 (cereal grains and legume veg., canola, pea, bean). 2 Highest acute RQ for freshwater invertebrates = C 0.4 (soybean, sorghum, corn uses); D 0.2 (cereal grains and legume veg., canola, pea, bean). 3 Highest acute RQ for estuarine/marine invertebrate = E 1.6 (soybean, sorghum, corn uses); F 0.6 (cereal grains and legume veg., canola, pea, bean).

As shown in Table V.2, the probability for acute direct effects (i.e., mortality) to individual

100 listed fish (based on the most sensitive species, fathead minnow) and the highest derived RQ value is 1 in 294,000 following applications on soybean, sorghum and cornfields. This reflects an average slope of 4.5. If the true dose response curve were shallow, the chance of an individual increases (e.g. slope of 2, chance is 1 in 44). The chance of an individual effect for freshwater invertebrates, based on the daphnid, is 1 in 121. For estuarine/marine invertebrate, the highest derived RQ is greater than 1 (acute RQ = 1.6), the chance for acute effects to an individual effect increases if the true dose response curve was steeper.

V.2.2. Listed Species Occurrence Associated with Picoxystrobin Use

The goal of the co-location analysis is 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 Significant 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) for 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 affected species associated with the proposed new uses of picoxystrobin is provided in Appendix J. Based the results of the LOCATES database query, there are a total of 310 listed species from all taxa nationwide.

This preliminary analysis indicates that there is a potential for picoxystrobin use to overlap 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 picoxystrobin and the best available information on the temporal and spatial co-location of listed species with respect to the action area. This analysis has not been conducted for this assessment.

REFERENCES

1. Farm Chemicals International. Product Profile: Picoxystrobin. Accessed on December 5, 2011 @ http://www.farmchemicalsinternational.com/cropprotection/productfocus/?storyid=307 5.

2. The Strobilurin Fungicides: Review.Pest Management Science.58:649-662.Accessed on Dec 2, 2011@ http://onlinelibrary.wiley.com/doi/10.1002/ps.520/pdf.

3. Guidance for Selecting Input Parameters in Modeling the Environmental Fate and Transport of Pesticides Version 2.1 October 22, 2009. U.S. Environmental Protection Agency Office of Pesticide Programs, Environmental Fate and Effects Division.

4. USEPA 1998. Guidelines for Ecological Risk Assessment. EPA/630/R-95/002F. Published in 63 FR 26846; May 14, 1998. U.S. Environmental Protection Agency, Washington, DC. April, 1998.

101 5. USEPA. 2004. Overview of the Ecological Risk Assessment Process in the Office of Pesticide Programs, U.S. Environmental Protection Agency. Endangered and Threatened Species Effects Determinations. Office of Prevention, Pesticides and Toxic Substances, Office of Pesticide Programs, Washington, D.C. January 23, 2004. Online at: http://www.epa.gov/oppfead1/endanger/consultation/ecorisk-overview.pdf

6. USEPA. 2006b. User’s Guide: TerrPlant Version 1.2.2 (Terrestrial Residue Exposure model). United States Environmental Protection Agency. Environmental Fate and Effects Division. Office of Pesticide Programs. U.S. Environmental protection Agency. Washington, D.C. December 26, 2006.

7. USEPA 2008. White Paper on Methods for Assessing Ecological Risks of Pesticides with Persistent, Bioaccumulative and Toxic Characteristics. Submitted to the FIFRA Scientific Advisory Panel. October 28-31, 2008. Office of Pesticide Programs, Environmental Fate and Effects Division, Washington, D.C.

8. USEPA. 2011b. 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/

9. USFWS/NMFS. 2004. 50 CFR Part 402. Joint Counterpart Endangered Species Act Section 7 Consultation Regulations; Final Rule. FR 47732-47762.

10. Urban, D.J. and N.J. Cook, 1986. Hazard Evaluation Division Standard Evaluation Procedure Ecological Risk Assessment. EPA 540/9-85-001. U.S. Environmental Protection Agency, Office of Pesticide Programs, Washington D.C.

11. North Dakota State University Extension Service. 2008. Identifying Leaf Stages in Small Grain. http://www.ag.ndsu.edu/pubs/plantsci/smgrains/w564.pdf.

102

103 Appendix A

Major degradates of picoxystrobin (constituting greater than 10% of the applied radiation from environmental fate studies, or of toxicological concern)

F F N O F HO O CH3 O

Compound 2 (IN-QDY62 R403092)

F H F N O F

Compound 3 (IN-QDK50 R403814)

F F N O F O H3C O O CH 3 Compound 4

104 F F N O F HO

O Compound 7 (IN-QFA35)

F F N O F O H3C OH O Compound 12

F F N O F O OH

Compound 8 (IN-QDY63)

105 Appendix B. Ecological Effects Data

In this risk assessment, surrogate test species of birds, mammals, fish, aquatic and terrestrial invertebrates and plants are used to estimate treatment-related direct effects on acute mortality or immobility and chronic reproduction, growth, and survival of non-target species. Toxicity test values (i.e., measures of effect) are derived from the results of registrant-required animal toxicity studies that are consistent with and meet toxicity testing guidelines (FIFRA 40 CFR Part 158 and 160). Toxicity tests include short-term acute, subacute, and reproduction/chronic studies that progress from basic laboratory tests to applied field studies. In addition, avian species are used as surrogates for reptiles while freshwater fish species are used as surrogates for aquatic-phase amphibians. Summaries of the studies are provided below.

Toxicity to Aquatic Animals Freshwater Fish, Acute (OPPTS 850.1075 Freshwater Fish Acute)

MRID: 48073769 In an acceptable 96-h acute toxicity study under static conditions, rainbow trout (Oncorhynchus mykiss) were exposed to ZA1963 at nominal concentrations of 0 (dilution water control), 0 (solvent control), 10, 18, 32, 56, 100 and 180 µg a.i./L. Mean measured concentrations were <0.40 (

MRID: 48073770 In an acceptable 96-h acute toxicity study under static conditions, bluegill sunfish (Lepomis macrochirus) were exposed to ZA1963 at nominal concentrations of 0 (dilution water control), 0 (solvent control), 18, 32, 56, 100 and 180 µg a.i./L. Mean measured concentrations were <1.0 (

106 measured concentrations were 77 μg a.i./L and 46 μg a.i./L, respectively. No sublethal symptoms of toxicity were noted throughout the study period, the EPA reviewer determined the EC50 and NOAEC for sub-lethal effects to be 170 µg a.i./L, the highest concentration tested.

MRID: 48258008 In an acceptable 96-h acute toxicity study under static conditions, fathead minnow (Pimephales promelas) were exposed to ZA1963 at nominal concentrations of 0 (dilution water control), 0 (solvent control), 18, 32, 56, 100 and 180 µg a.i./L. Mean measured concentrations were <1.2 (180 μg a.i./L and 180 μg a.i./L (EPA reviewer-estimated), respectively.

MRID: 48258010 In an acceptable 96-h acute toxicity study under static conditions, mirror carp (Cyprinus carpio) were exposed to ZA1963 at nominal concentrations of 0 (dilution water control), 0 (solvent control), 18, 32, 56, 100, 180 and 320 µg a.i./L. Mean measured concentrations were <1.2 (

MRID: 48258012 In an acceptable 96-h acute toxicity study under static conditions, three-spined stickleback (Gasterosteus aculeatus) were exposed to ZA1963 at nominal concentrations of 0 (dilution water control), 0 (solvent control), 18, 32, 56, 100 and 180 µg a.i./L. Mean measured concentrations were <0.75 (

107 nominal concentrations were 100 μg a.i./L and 56 μg a.i./L, respectively.

The general signs of toxicity noted in the study were sounding, loss of balance, quiescence and dark discoloration. Some signs of toxicity were observed in 1-3 fish of the 56 μg a.i./L group and in more than 3 fish of the 100 μg a.i./L group. The NOAEC for symptoms of toxicity observed was 32 μg a.i./L, based on nominal concentrations.

Additional Freshwater Fish Acute Studies Tested with Transformation Products of Picoxystrobin

MRID: 48258014 In an acceptable 96-h acute toxicity study under static conditions, fathead minnow (Pimephales promelas), were exposed to R408631, a transformation product of picoxystrobin, at nominal concentrations of 0 (dilution water control) and 10 mg/L. The test solution was observed to have some insoluble white particles on the surface. Mean measured concentrations prior to centrifugation were <0.016 (10 mg/L. The NOAEC based on mortality and sublethal effects was 10 mg/L, the highest concentration tested.

MRID: 48258016 In an acceptable 96-h acute toxicity study under static conditions, fathead minnow (Pimephales promelas), were exposed to R403814, a transformation product of picoxystrobin, at nominal concentrations of 0 (dilution water control) and 10 mg/L. Mean measured concentrations (pre- and post centrifugation) were <0.022 (10 mg/L (nominal). The NOAEC based on mortality and sublethal effects was 10 mg/L, the highest concentration tested (nominal).

MRID: 48258018 In a 96-h acute toxicity study under static conditions, fathead minnow (Pimephales promelas), were exposed to R403092, a transformation product of picoxystrobin, at nominal concentrations of 0 (dilution water control) and 10 mg/L. The test solution was observed to have some insoluble white particles on the surface. Mean measured concentrations prior to centrifugation were <0.058 (10 mg/L (nominal). The NOAEC based on mortality and sublethal effects was 10 mg/L, the highest concentration tested (nominal).

MRID: 48258020 In an acceptable 96-h acute toxicity study under static conditions, fathead minnow (Pimephales promelas), were exposed to R408509, a transformation product of picoxystrobin, at nominal concentrations of 0 (dilution water control) and 10 mg/L. The test solution was observed to have a powdery film on the surface. Mean measured concentrations prior to centrifugation were <0.038 (

108 throughout the study. The 96-hour LC50 was >10 mg/L (nominal). The NOAEC based on mortality and sublethal effects was 10 mg/L, the highest concentration tested (nominal).

MRID: 48258022 In an acceptable 96-h acute toxicity study under static conditions, rainbow trout (Oncorhynchus mykiss), were exposed to R413834, a transformation product of picoxystrobin, at nominal concentrations of 0 (dilution water control) and 10 mg/L. Mean measured concentrations were <0.093 (10 mg/L (nominal). The NOAEC based on mortality and sublethal effects was 10 mg/L, the highest concentration tested (nominal).

Additional Freshwater Fish Acute Study Tested with Formulated Product of Picoxystrobin

MRID: 48073771 In an acceptable 96-h acute toxicity study under static conditions, rainbow trout (Oncorhynchus mykiss) were exposed to a 250 g/L SC formulation of ZA1963 (picoxystrobin) at nominal concentrations of 0 (dilution water control), 0.10, 0.18, 0.32, 0.56, 1.0 and 1.8 mg formulation/L (equivalent to 0, 0.023, 0.041, 0.074, 0.13, 0.23 and 0.41 mg a.i./L). Mean measured concentrations of the formulation were <0.0056, 0.078, 0.15, 0.33, 0.61, 1.0 and 1.7 mg formulation/L (corresponding to <0.0013, 0.018, 0.034, 0.075, 0.14, 0.23 and 0.38 mg a.i./L). Mean measured concentrations ranged from 78 to 108% of nominal values. Results are based on mean measured concentrations. At 72 hours, one fish died as a result of jumping out of the mean measured 0.15 mg formulation/L test tank. This mortality was deemed not to be treatment- related. There were no treatment-related mortalities throughout the study in the control and the mean measured 0.078 and 0.15 mg formulation/L test concentrations. All fish died after 24 hours of exposure in the higher mean measured test concentrations (0.33, 0.61, 1.0 and 1.7 mg formulation/L). The reviewer-calculated 96-hour LC50 based on mean measured concentrations was 0.22 mg formulation/L. No symptoms of toxicity were noted in the control and the nominal 0.1 and 0.18 mg formulation/L test concentrations. There were no surviving fish in the higher test concentrations, thus symptoms of toxicity could not be observed in those treatments. The 96- hour NOAEC based on mortality and sublethal effects was 0.15 mg formulation/L, based on mean measured concentrations.

Freshwater Fish, Chronic (OPPTS 850.1400 Freshwater Fish Early Life Stage)

MRID: 48073775 The acceptable 36-day chronic toxicity of ZA1963 (picoxystrobin) to early-life stages of fathead minnow (Pimephales promelas) was studied under flow-through conditions. Fertilized eggs/embryos (80 per treatment level, <24 hours old) of fathead minnow were exposed to ZA1963 at nominal concentrations of 0 (dilution water control), solvent control (triethylene glycol), 5.0, 10, 20, 30, 40 and 80 µg a.i./L. The mean measured concentrations were <0.58 (

109 The percent hatching success was 90, 85, 86, 89, 90, 90 and 70% in the pooled controls, 4.8, 10, 19, 27, 36 and 73 µg a.i./L test concentrations, respectively. Larval survival at 32 days post hatch was 78% in the pooled controls, and 78, 78, 82, 72, 68 and 0% in the 4.8, 10, 19, 27, 36 and 73 µg a.i./L test concentrations, respectively. Mean total length of larvae at 32 days post hatch was 21.2, 21.6, 20.7, 21.5, 21.4 and 19.9 mm in the pooled controls, 4.8, 10, 19, 27 and 36 µg a.i./L test concentrations, respectively. Mean larval weight at 32 days post hatch was 155, 172, 151, 165, 163 and 134 g in the pooled controls, 4.8, 10, 19, 27 and 36 µg a.i./L test concentrations, respectively. A significant difference in embryo hatching success, larval survival at 32 days post hatch and larval growth – total length and wet weight at test termination was observed at the mean measured 73 µg a.i./L test concentration, relative to the pooled controls. The 36-day NOAEC and LOAEC (based on mean measured concentrations) were 36 and 73 µg a.i./L, respectively, based on effects on embryo hatching success, larval survival at 32 days post hatch and larval growth – total length and wet weight at test termination. No sub-lethal clinical signs of toxicity were observed and reported.

Freshwater Invertebrates, Acute (OPPTS 850.1010 Freshwater Invertebrate Acute)

MRID: 48073764 In an acceptable 48-hr-acute toxicity of ZA1963 technical (picoxystrobin) to Daphnia magna was studied under static conditions. Daphnids were exposed to 0 (control), 0 (solvent control), and nominal concentrations of 3.2, 5.6, 10, 18, 32, 56 and 100 μg a.i./L for 48 hours. Mean measured concentrations were <0.19 (LOD), <0.19, 3.2, 5.7, 10, 19, 32, 58 and 99 μg a.i./L. Immobilization was observed daily. After 48 hours of exposure, no immobility was observed in the controls or in the nominal 3.2, 5.6, 10, and 18 μg a.i./L test concentrations, while 100% immobility was observed in the 32, 56 and 100 μg a.i./L test concentrations. The 48-hour EC50 and NOAEC were 24 and 18 μg a.i./L, respectively.

Additional Freshwater Invertebrate Acute Studies with Transformation Products of Picoxystrobin

MRID: 48258015 The acceptable 48-hr-acute toxicity of R408631 (picoxystrobin transformation product) to Daphnia magna was studied under static conditions. Daphnids were exposed to 0 (control) and the nominal concentration of 10 mg R408631/L for 48 hours. Mean measured concentrations were <0.016 (LOD) and 10 mg R408631/L. Immobilization was observed daily. After 48 hours of exposure, no immobilization was observed in the control and the concentration tested. The 48- hour EC50 was >10 mg R408631/L. The 48-hour NOAEC was 10 mg R408631/L, the highest concentration tested.

MRID: 48258017 The acceptable 48-hr acute toxicity of R403814 (picoxystrobin transformation product) to Daphnia magna was studied under static conditions. Daphnids were exposed to 0 (control) and the nominal concentration of 10 mg R403814/L for 48 hours. Mean measured concentrations were <0.022 (LOD) and 10 mg R403814/L. Immobilization was observed daily. After 48 hours of exposure, no immobilization was observed in the control and the concentration tested. The 48- hour EC50 was >10 mg R403814/L. The 48-hour NOAEC was 10 mg R403814/L, the highest

110 concentration tested.

MRID: 48258019 The acceptable 48-hr acute toxicity of R403092 (picoxystrobin transformation product) to Daphnia magna was studied under static conditions. Daphnids were exposed to 0 (dilution water control) and a single nominal concentration of 10 mg R403092/L for 48 hours. Mean measured concentrations were <0.056 (LOD) and 11 mg R403092/L. Results are based on nominal concentrations. Immobilization was observed daily. After 48 hours of exposure, no immobilization was observed in the control and the nominal 10 mg R403092/L concentration tested. The 48-hour EC50 was >10 mg R403092/L. The 48-hour NOAEC was 10 mg R403092/L, the highest concentration tested.

MRID 4825021 The 48-hr acute toxicity of R408509 (picoxystrobin transformation product) to Daphnia magna was studied under static conditions. Daphnids were exposed to 0 (control) and a single nominal concentration of 10 mg R408509/L for 48 hours. Mean measured concentrations were <0.036 (LOD) and 11 mg R408509/L. Results are based on nominal concentrations. Immobilization was observed daily. After 48 hours of exposure, no immobilization was observed in the control or in the nominal 10 mg R408509/L concentration tested. The 48-hour EC50 was >10 mg R408509/L. The 48-hour NOAEC was 10 mg R408509/L, the highest concentration tested.

MRID: 48258023 The acceptable 48-hr acute toxicity of R413834 (picoxystrobin transformation product) to Daphnia magna was studied under static conditions. Daphnids were exposed to 0 (control), and nominal concentrations of 1.8, 3.2, 5.6, 10, and 18 mg R413834/L for 48 hours. Mean measured concentrations were <0.060 (LOD), 3.4, 3.8, 7.9, 11, and 21 mg R413834/L. Immobilization was observed daily. After 48 hours of exposure, no immobilization was observed in the controls or in the mean measured 3.4 and 3.8 mg R413834/L test concentrations, while 55, 75, and 100% immobilization was observed in the 7.9, 11, and 21 mg R413834/L test concentrations. The 48- hour EC50 and NOAEC were 8.0 and 3.8 mg R413834/L, respectively, based on mean measured concentrations.

Additional Freshwater Invertebrate Acute Study with Formulated Product of Picoxystrobin

MRID: 48073765 The acceptable 48-hr acute toxicity of a 250 g/L SC formulation of ZA1963 (picoxystrobin) to Daphnia magna was studied under static conditions. Daphnids were exposed to 0 (control) and nominal concentrations of 0.056, 0.10, 0.18, 0.32, 0.56 and 1.0 mg formulation/L (equivalent to 0, 0.013, 0.023, 0.041, 0.074, 0.13 and 0.23 mg a.i./L) for 48 hours. Mean measured concentrations of the formulation were <0.0056, 0.061, 0.11, 0.19, 0.42, 0.56 and 0.91 mg formulation/L (corresponding to <0.0013, 0.014, 0.025, 0.044, 0.096, 0.13 and 0.21 mg a.i./L). Immobilization was observed daily. No immobilization was observed in the dilution control, and nominal test concentration of 0.056 mg formulation/L throughout the study. After 48 hours of exposure, 85% of daphnids were immobile in the nominal 0.10 mg formulation/L test concentration, and all daphnids were immobile at the higher concentrations (0.18, 0.32, 0.56 and

111 1.0 mg formulation/L). The 48-hour EC50 and NOAEC are 0.086 and 0.056 mg formulation/L, respectively, based on nominal concentrations.

Freshwater Invertebrate, Chronic (OPPTS 850.1300 Freshwater Invertebrate Life Cycle)

MRID: 48073772 The acceptable 21-day chronic toxicity of ZA1963 (picoxystrobin; 96.6% purity) to Daphnia magna was studied under static renewal conditions. Daphnids were exposed to 0 (dilution water control), 0, (solvent control), and test chemical at nominal concentrations of 1, 2, 4, 8, 16 and 32 µg a.i./L. Mean measured concentrations were <0.033 (LOD), <0.033 (LOD), 1, 2, 4, 8.2, 16 and 32 µg a.i./L (100-103% of nominal). Results are reported based on nominal concentrations. No mortalities were observed in the dilution control, and the 2 and 8 µg a.i/L test concentrations. One mortality (10%) was observed in the solvent control, 1, 4, and 16 µg a.i/L test concentrations, while 7 mortalities (70%) were observed in the 32 µg a.i/L test concentration by study termination. The mortalities in all but the highest test concentration were deemed to be random and not attributed to picoxystrobin. The 21-day LC50 was 26 µg a.i/L. The length of parent daphnids was significantly reduced at the 32 µg a.i/L test concentration compared to pooled controls. The 21-day NOAEC based on the length of parent daphnids was 16 µg a.i/L. A significant reduction in the number of alive offspring per surviving adult was detected in the 16 and 32 µg a.i./L test concentrations, compared to pooled controls. The 21-day NOAEC based on the number of alive offspring per surviving adult was 8 µg a.i/L (most sensitive endpoint). The EPA reviewer’s conclusions agreed with most of the study authors’ except for reproduction. Number of young per adults in the 2, 4, 8, 16, and 32 µg a.i./L levels had a mean value of 49, 48, 48, 48, 47 and 42, respectively, compared to 51 for the blank control level. The EPA reviewer’s analyses with blank control detected a significant effect at the ≥2 µg a.i./L levels for that parameter; the EPA reviewer concluded the NOAEC was 1 µg a.i./L, which differed from the author’s analyses with pooled control that detected a significant difference only at the highest level tested (32 µg a.i./L). The NOAEC was 1 µg a.i./L, which was several levels below the author’s results.

Estuarine/Marine Fish, Acute (OPPTS 850.1075 Estuarine/Marine Fish Acute)

MRID: 48073768 In an acceptable 96-h acute toxicity study under static conditions, sheepshead minnow (Cyprinodon variegatus) were exposed to picoxystrobin at nominal concentrations of 0 (dilution water control), 0 (solvent control), 100, 150, 220, 330 and 500 µg a.i./L. Mean measured concentrations were <1.71 (

112 all fish in the 310 µg a.i./L test concentration recovered throughout the study. After 72 hours, all fish in the 520 µg a.i./L test concentration were observed to be lethargic and were dead at test termination. An EC50 and NOAEC for sublethal effects was not determined by the study author; however, the EPA reviewer determined the NOAEC to be 310 µg a.i./L by visual observation.

Estuarine/Marine Fish, Chronic (OPPTS 850.1400 Estuarine/Marine Fish Life-Cycle)

MRID: 48073774 The acceptable 33-day chronic toxicity of DPX-YT669 (picoxystrobin) to the early life stage of sheepshead minnow (Cyprinodon variegatus) was studied under flow-through conditions. Embryos (fertilized eggs, 120 per test level, <30 hours old) of sheepshead minnow were exposed to nominal concentrations of 0 (negative control), 0 (solvent control, DMF), 6.3, 13, 25, 50 and 100 µg a.i./L. The mean measured concentrations were <0.06 (

Estuarine/Marine Invertebrates, Acute (OPPTS 850.1025 and 850.1035 Estuarine/Marine Invertebrate Acute)

MRID: 48073766 The acceptable 96-hour acute toxicity of DPX-YT669 (picoxystrobin) to the Eastern oyster, Crassostrea virginica, was studied under flow-through conditions. Oysters were exposed to the test material at nominal concentrations of 0 (blank control and solvent control), 1.5, 2.7, 4.8, 8.8 and 16 μg a.i./L. Mean-measured concentrations were

113 measured concentrations was <1.4 μg a.i./L (PMRA reviewer-calculated based on pooled controls) or 1.4 µg a.i./L (EPA reviewer-calculated based on the blank control).

MRID: 48073767 The 96-hour acute toxicity of DPX-YT669 (picoxystrobin) to mysids, Americamysis bahia, was studied under static-renewal conditions. Mysids were exposed to the test material at nominal concentrations of 0 (blank and solvent controls), 13, 25, 50, 100, and 200 µg a.i./L; mean- measured concentrations were 12, 24, 46, 110 and 190 µg a.i./L. Mortality and sublethal effects were observed daily. No mortality was observed in the dilution water and solvent controls. Mortality was 10, 0, 100, 100 and 100% in the 12, 24, 46, 110 and 190 μg a.i./L treatment groups, respectively. The 96-hour LC50, based on measured concentrations was 33 μg a.i./L. The 96-hour NOAEC based on mortality was 24 μg a.i./L. No sublethal effects were observed in controls and in concentrations of 0, 12 and 24 μg a.i./L treatment groups. In the 46 µg a.i./L test concentration, two of the five surviving mysids were lethargic while the other three were on the bottom of the test vessel after 48 hours. After 72 hours, the single surviving mysid was observed to be lethargic at that concentration. All surviving mysids in the 110 µg a.i./L test concentration were observed to be lethargic after 24 hours.

Estuarine/Marine Invertebrate, Chronic (OPPTS 850.1350 Estuarine/Marine Invertebrate Life-Cycle)

MRID: 48073773 The acceptable 29-day chronic toxicity of picoxystrobin to mysids, Americamysis bahia, was studied under flow-through conditions. Mysids were exposed to dilution water control, solvent control, and test chemical at measured concentrations of 0.92, 1.8, 3.6, 7.6, 14 μg a.i./L. A significant reduction in the number of offspring was observed at the two highest test concentrations when compared with pooled controls or blank control alone. No other statistically significant treatment-related effects were observed. The NOAECs for F0 survival, male and female body length and male and female body weight were all 14 μg a.i./L (highest concentration tested). The LOAECs for these endpoints could not be determined because 14 μg a.i./L was the highest dose tested. The NOAEC for mean number of offspring was 3.6 μg a.i./L and the LOAEC was 7.6 μg a.i./L. The NOAEC and LOAEC for F1 survival were 14 μg a.i./L (highest concentration tested) and >14 μg a.i./L, respectively. The most sensitive end point was mean number of offspring per female.

Toxicity to Aquatic Plants Aquatic Plants (OPPTS 850.4400 and 850.5400 Vascular and Non-Vascular Plants)

MRID: 48073803 In an acceptable 7-day acute toxicity study, freshwater aquatic vascular plants, duckweed (Lemna gibba), were exposed to picoxystrobin at mean measured concentrations of <0.06 (

114 percent inhibition of growth rate, calculated from frond density compared to pooled controls from 0-7 days ranged from -2% at 7.9 µg a.i./L to 37% in the 1000 µg a.i./L test concentration. The percent inhibition of frond dry weight (biomass) compared to pooled controls from 0-7 days ranged from 0% at 7.9 µg a.i./L to 43% in the 340 µg a.i./L test concentration. The percent inhibition of yield, calculated from frond dry weight, compared to pooled controls after 7 days ranged from -2% at 7.9 µg a.i./L to 44% in the 340 µg a.i./L test concentrations. The percent inhibition of growth rate, calculated from frond dry weight, compared to pooled controls from 0- 7 days ranged from 0% at 7.9 µg a.i./L to 20% at 340 µg a.i./L. The 7-day EC50 for frond density, yield based on frond density, growth rate based on frond density, dry frond weight, yield based on dry weight and growth rate based on dry weight was 260, 230, >1000, >1000, >1000 and >1000 µg a.i./L, respectively. Significant differences between the pooled controls and the three highest test concentrations were detected for all endpoints. The 7-day NOAEC for all endpoints was 49 µg a.i./L when compared to pooled controls. The EPA reviewer’s conclusions agreed with most of the study authors’ except for frond production (% of frond density and yield of frond density). Number of frond density in the 49, 160, 340 and 1000 µg a.i./L levels had a mean value of 319, 202, 157 and 103, respectively, compared to 375 for the blank control level. Yield of frond density in the 49, 160, 340 and 1000 µg a.i./L levels had a mean value of 307, 190, 145 and 91, respectively, compared to 363 for the blank control level. The EPA reviewer’s analyses with blank control did detect a significant effect at 49 µg a.i./L for those parameters; the reviewer concluded the NOEC was at 20 µg a.i./L, which differed from the author’s analyses with pooled control that did not detect a significant difference. The NOAEC was 20 µg a.i./L, which was lower than author’s results. Frond density after 7 days of recovery ranged from 10 to 18 times the frond density at the initiation of the recovery period in all test concentrations. These results indicated that picoxystrobin was phytostatic within a 7-day recovery phase at mean measured concentrations ≤1000 µg a.i./L.

MRID: 48073804 In an acceptable 96-hour acute toxicity study, cultures of the marine diatom, Skeletonema costatum, strain CCMP 1332, were exposed to DPX-YT669 (picoxystrobin) mean measured concentrations of 0 (blank control), 0 (solvent control), 0.0009, 0.0023, 0.0053, 0.013, 0.035 and 0.096 mg a.i./L under static conditions. After 96-hours, the percent inhibition in cell density relative to the blank control ranged from 8% at 0.009 mg a.i./L (0% relative to pooled controls; reviewer-calculated) to 96% in the 0.096 mg a.i./L test concentration. The percent inhibition in yield (0-96 hours) relative to the blank control ranged from 8% at 0.009 mg a.i./L (0% relative to pooled controls; reviewer-calculated) to 102% in the 0.096 mg a.i./L test concentration. The percent inhibition in growth rate (0-96 hours) relative to the blank control ranged from 3% at 0.009 mg a.i./L (-4% relative to pooled controls; reviewer-calculated) to 116% in the 0.096 mg a.i./L test concentration. The 96-hour NOAEC for all endpoints was 0.0023 mg a.i./L. The 96- hour EC50 for cell density, yield (0-96 hours) and growth rate (0-96 hours) was 0.0042, 0.0040 and 0.0063 mg a.i./L, respectively. Cell density after 4 days of recovery was >10X the cell density at initiation of the recovery period. Picoxystrobin was algistatic to S. costatum at nominal concentrations less than or equal to 0.10 mg a.i./L within a 4-day recovery phase.

MRID: 48073805 In an acceptable 96-hour acute limit toxicity study, cultures of the freshwater blue-green alga, Anabaena flos-aquae, were exposed to picoxystrobin (DPX-YT669) mean measured

115 concentrations of 0 (blank control) and 3 mg/L under static conditions. No toxicant-related effects were observed on cell density, yield or growth rate. The percent inhibition in the treated algal culture as compared to the control was 3.87%, 3.87% and 0.82% for cell density, yield and growth rate. The 96-hour EC50 based on all endpoints was >3 mg a.i./L, and the corresponding NOAEC was 3 mg a.i./L, the highest concentration tested.

MRID: 48073806 In an invalidated 96-hour acute toxicity study, cultures of the freshwater diatom, Navicula pelliculosa, strain B664, were exposed to DPX-YT669 (picoxystrobin) mean measured concentrations of 0 (blank control), 0 (solvent control), 1.4, 3.7, 13, 40, 130, 400 and 1200 µg a.i./L under static conditions. After 96-hours, the PMRA reviewer-calculated percent inhibition in cell density relative to the solvent control ranged from 20% at 1.4 µg a.i./L to 82% in the 1200 µg a.i./L mean measured test concentration. The PMRA reviewer-calculated percent inhibition in yield (0-96 hours) relative to the solvent control ranged from 20% at 1.4 µg a.i./L to 83% in the 1200 µg a.i./L mean measured test concentration. The PMRA reviewer-calculated percent inhibition in growth rate (0-96 hours) relative to the solvent control ranged from 4% at 1.4 µg a.i./L to 33% in the 1200 µg a.i./L mean measured test concentration. The following major problems were noted: significant differences between the blank and solvent controls (for the EPA), high coefficients of variation in blank and solvent controls, unsound statistical results with the blank control and potential hormesis. These problems impacted the validity of the study as per EPA and OECD guidelines; the PMRA and EPA reviewers cannot accept this study.

MRID: 48258024 In an acceptable 3-day acute toxicity study, cultures of the freshwater green algae, Selenastrum capricornutum, strain ATCC 22662, were exposed to ZA1963 (picoxystrobin) nominal concentrations of 0 (blank control), 0 (solvent control), 4.0, 8.8, 19, 42, 92, 200, 440 and 970 µg a.i./L under static conditions. Mean measured concentrations were <0.93 (LOD), <0.93, 4.4, 9.4, 19, 43, 81, 210, 450 and 940 µg a.i./L (88 to 110% of nominal concentrations). Results are based on reviewer calculations using mean measured concentrations. After 3 days, the percent inhibition in cell density relative to the pooled controls ranged from -3% (stimulation) at 4.4 µg a.i./L to 97% in the 940 µg a.i./L test concentration (-5% to 97% relative to blank control). The percent inhibition in biomass (0-3 days), expressed as area under the growth curve relative to the pooled controls ranged from -4% at 4.4 µg a.i./L to 96% in the 940 µg a.i./L test concentration (- 5% to 96% relative to blank control). The percent inhibition in biomass (0-3 days), expressed as yield relative to the pooled controls ranged from -3% at 4.4 µg a.i./L to 98% in the 940 µg a.i./L test concentration (-5% to 98% relative to blank control). The percent inhibition in growth rate (0-3 days) relative to the pooled controls ranged from -1% at 4.4 µg a.i./L to 65% in the 940 µg a.i./L test concentration (-1% to 65% relative to blank control). The 3-day NOAEC based on mean measured concentrations when compared to both the pooled controls and the blank control was 4.4 µg a.i./L for cell density and yield, when compared to the pooled controls alone was 9.4 µg a.i./L for area under the growth curve and growth rate, and when compared to the blank control alone was 4.4 µg a.i./L and 9.4 µg a.i./L for area under the growth curve and growth rate respectively. The 3-day EC50 based on mean measured concentrations for cell density, area under the growth curve (0-3 days), yield (0-3 days) and growth rate (0-96 hours) when compared both to the pooled controls and the blank control were 33.0, 32.8, 32.8 and 184.9 µg a.i./L and

116 26, 26, 26 and 240 µg a.i./L, respectively. Additional Aquatic Non-Vascular Plant Studies with Transformation Products of Picoxystrobin

MRID: 48258026 In a 3-day acute toxicity study, cultures of the freshwater green algae, Selenastrum capricornutum, were exposed to R403814 (a transformation product of picoxystrobin) at nominal concentrations of 0 (blank control) and 10 mg/L. Mean measured concentrations were <0.022 (10 mg R403814/L. This toxicity study is classified as acceptable to the PMRA [the study is scientifically sound and satisfies the guideline requirements] and supplemental to the USEPA [the study is scientifically sound but a NOAEC could not be established; other endpoints or a toxicity test with multiple levels to determine a NOAEC could be considered if the screening level risk assessment using this limit concentration indicates the level of concern is exceeded.] for an acute aquatic non-vascular plant toxicity study with R403814, a transformation product of picoxystrobin, on the freshwater green algae, Selenastrum capricornumtum.

MRID: 48258027 In a 3-day acute toxicity study, cultures of the freshwater green algae, Selenastrum capricornutum, were exposed to R408631 (a transformation product of picoxystrobin) at nominal concentrations of 0 (blank control) and 10 mg /L. Mean measured concentrations were <0.016 (10 mg R408631/L. This toxicity study is classified as acceptable to the PMRA [this study is scientifically sound and satisfies the guideline requirements] and supplemental to the USEPA [the study is scientifically sound but a NOAEC could not be established; other endpoints or a toxicity test with multiple levels to determine a NOAEC could be considered if the screening level risk assessment using this limit concentration indicates the level of concern is exceeded.] for an acute aquatic non-vascular toxicity study with the freshwater green algae, Selenastrum capricornumtum, using the picoxystrobin transformation product, R408631.

MRID: 48258028 In an acceptable 3-day acute toxicity study, cultures of the freshwater green algae, Selenastrum capricornutum, were exposed to R403092 (a transformation product of picoxystrobin) at nominal concentrations of 0 (blank control) and 10 mg R403092/L. Mean measured concentrations were

117 <0.058 (10 mg R403092/L.

MRID: 48258029 In a 3-day acute toxicity study, cultures of the freshwater green algae, Selenastrum capricornutum, were exposed to R408509 (a transformation product of picoxystrobin) at nominal concentrations of 0 (blank control) and 10 mg R408509/L. Mean measured concentrations were <0.038 (10 mg R408509/L. This toxicity study is classified as acceptable to the PMRA [this study is scientifically sound and satisfies the guideline requirements] and supplemental to the USEPA [the study is scientifically sound but a NOAEC could not be established; other endpoints or a toxicity test with multiple levels to determine a NOAEC could be considered if the screening level risk assessment using this limit concentration indicates the level of concern is exceeded.] for an acute aquatic non-vascular plant toxicity study with the freshwater green algae, Selenastrum capricornumtum, using the picoxystrobin transformation product, R408509.

MRID: 48258030 In a 3-day acute toxicity study, cultures of the freshwater green algae, Selenastrum capricornutum, were exposed to R413834 (a transformation product of picoxystrobin) at nominal concentrations of 0 (blank control) and 10 mg R413834/L. Mean measured concentrations were <0.095 (10 mg R413834/L. This toxicity study is classified as acceptable to the PMRA [the study is scientifically sound and satisfies the guideline requirements] and supplemental to the USEPA [the study is scientifically sound but a NOAEC could not be established; other endpoints or a toxicity test with multiple levels to determine a NOAEC could be considered if the screening level risk assessment using this limit concentration indicates the level of concern is exceeded.] for an acute aquatic non-vascular plant toxicity study with the freshwater green algae, Selenastrum capricornumtum, using the picoxystrobin transformation product, R413834.

Additional Aquatic Non-Vascular Plant Study with Formulated Product of Picoxystrobin

118

MRID: 48258025 In a supplemental 3-day acute toxicity study under static conditions, cultures of the freshwater green algae, Selenastrum capricornutum, strain ATCC 22662, were exposed to a 250 g/L SC formulation of ZA1963 (picoxystrobin) at nominal concentrations of 0 (control), 0.02, 0.045, 0.1, 0.23, 0.5, 1.1, 2.5 and 5.6 mg formulation/L (corresponding to 0, 0.0046, 0.01, 0.023, 0.053, 0.12, 0.25, 0.58 and 1.3 mg a.i./L). Mean measured concentration of picoxystrobin were <0.0013 (LOD), 0.005, 0.01, 0024, 0.052, 0.13, 0.26, 0.55 and 1.3 mg a.i./L (95 to 109% of nominal concentrations). Results are based on nominal concentrations. After 3 days, the percent inhibition in cell density and yield relative to the blank control ranged from 4% at 0.045 mg formulation/L to 98% in the 5.6 mg formulation/L test concentration. The percent inhibition in area under the growth curve (0-3 days) relative to the blank control ranged from 4% at 0.045 mg formulation/L to 97% in the 5.6 mg formulation/L test concentration. The percent inhibition in growth rate (0-3 days) relative to the blank control ranged from 1% at 0.045 mg formulation/L to 70% in the 5.6 mg formulation/L test concentration. The 3-day NOAEC for all endpoints was 0.045 mg formulation/L (corresponding to 0.01 mg a.i./L). The 3-day EC50 for cell density, area under the growth curve (0-3 days), yield (0-3 days) and growth rate (0-96 hours) was 0.16, 0.18, 0.16 and 1.2 mg formulation/L, respectively; corresponding to 0.04, 0.04, 0.04 and 0.28 mg a.i./L).

Toxicity to Terrestrial Animals Birds, Acute (OPPTS 850.2100 Avian Acute Oral)

MRID: 48073780 The acute oral toxicity of picoxystrobin to zebra finch (Poephila guttata) was assessed over 14 days. Five zebra finch/sex/dose received single oral nominal doses of 0, 292, 486, 810, 1350, and 2250 mg a.i./kg bw at a dose volume of 5 mL/kg bw in 1% carboxymethyl cellulose aqueous solution. Birds were observed for clinical signs of toxicity, body weight effects, and mortality for 14 days after dosing. Mortalities were examined for gross pathological changes. Given the nature of the feed presented and the hulling and wasteful behavior of the birds, no attempt was made to measure feed consumption. There were no mortalities in the control group or in the 292, 486 and 1350 mg a.i./kg bw treatment groups. Ten percent of birds died within one day of dosing in the 810 and 2250 mg a.i./kg bw dose levels. No apparent differences in body weight were observed between the control birds and those at all dose levels. Signs of toxicity including lethargy, ruffled appearance, prostrate posture and loss of righting reflex were observed on the day of dosing in 50% and 70% of birds dosed at 1350 and 2250 mg a.i./kg bw, respectively; all surviving birds were normal in appearance and behavior from Day 1 of the test until test termination. Regurgitation was observed in 10%, 40% and 70% of birds on the day of dosing at the 810, 1350 and 2250 mg a.i./kg bw dose levels, respectively. Excluding all doses at which regurgitation occurred, an initial conservative acute oral LD50 was set by the reviewer at >486 mg a.i./kg bw (dose with no regurgitation observed, no mortalities occurred and no clinical signs of toxicity were noted). Other endpoints or toxicity test could be considered if the initial screening level risk assessment indicates the level of concern is exceeded. The NOAEC was 486 mg a.i./kg bw, based on the incidence of sublethal effects. Despite noted problems with regurgitation, this toxicity study is classified by the EPA reviewer as supplemental and provides useful information for an acute oral toxicity study with zebra finch. The PMRA finds that the study provides useful information for an acute oral toxicity study with zebra finch.

119

MRID: 48073781 The acute oral toxicity of ZA1963 to 22 to 29-week-old bobwhite quail (Colinus virginianus) was assessed over 14 days. Technical ZA1963 was administered in corn oil to ten birds per treatment level by gavage at 2250 mg a.i./kg bw. A single mortality was observed after three days in the 2250 mg a.i./kg bw test group. No mortality was observed in the controls. The 14- day-acute oral LD50 was >2250 mg a.i/kg bw, while the 14-day NOAEC, based on mortality, was 2250 mg a.i./kg bw, the highest dose tested. Although not required, additional doses (1125, 562.5 and 100 mg a.i./kg bw) and associated controls were subsequently added in different phases to establish the no effect level based on sublethal effects. As a result, the in-life portion of the study was conducted in four phases from July 7, 1997 to February 20, 1998. Effects on body weight compared to concurrent controls occurred at doses of 562.5 mg a.i./kg bw, 1125 mg a.i./kg bw and 2250 mg a.i./kg bw. There were no apparent effects upon feed consumption in the 100 and 562.5 mg/kg bw dose groups and at feed consumption interval. A marked reduction in feed consumption was noted in the 1125 and 2250 mg/kg bw dose groups for the period from Day 0 to Day 3, but feed consumption was comparable to the control groups at all other feed consumption intervals. A NOAEC is not required by the PMRA for an acute oral toxicity study. The PMRA and EPA reviewers do not consider the NOAEC (based on sub-lethal endpoints) to be reliable, as the tests for the different doses were conducted at different times and the birds were from different sources and came from different hatches. However, the LD50 results and NOEL based on mortality from the initial portion of the study are acceptable.

Birds, Subacute (OPPTS 850.2200 Avian Subacute Dietary)

MRID: 48073782 The acceptable acute dietary toxicity of ZA 1963 (picoxystrobin) to 10-d old northern bobwhite quails (Colinus virginianus) was assessed over 8 days. ZA 1963 was administered in the diet at nominal concentrations of 0 (control), 325, 650, 1300, 2600 and 5200 mg a.i./kg diet. Mean measured concentrations ranged from 99 to 102% of nominal values. The study was conducted in two phases. At termination of the first test phase, birds from the control group and the highest treatment were not examined macroscopically. To determine if any gross pathological changes were associated with sub-chronic exposure to ZA 1963, the test was repeated with a control and a 5200 mg a.i./kg diet test level during a second phase to collect necropsy data. No mortalities were observed in any birds throughout either phases of the study. Similarly, no treatment-related sublethal effects were noted at any concentration. The 5-day acute dietary LC50 was >5200 mg a.i./kg diet (nominal). The 5-day NOAEC of ZA 1963 based on mortality and sublethal effects was 5200 mg a.i./kg diet (nominal), the highest concentration tested. The 5-day LC50 of >5200 mg a.i./kg diet was equivalent to a 5-day LD50 of >1830 mg a.i./kg body weight/day (reviewer- calculated). According to the US EPA classification, ZA 1963 would be classified as practically non-toxic to northern bobwhite quails on an acute dietary exposure basis using the nominal concentration.

MRID: 48073783 The acceptable acute dietary toxicity of ZA 1963 (picoxystrobin) to 10-d old mallard ducks (Anas platyrhynchos) was assessed over 8 days. ZA 1963 was administered in the diet at nominal concentrations of 0 (control), 325, 650, 1300, 2600 and 5200 mg a.i./kg diet. Mean measured

120 concentrations ranged from 99 to 102% of nominal values. The study was conducted in two phases. At termination of the first test phase, birds from the control group and the highest treatment were not examined macroscopically. To determine if any gross pathological changes were associated with sub-chronic exposure to ZA 1963, the test was repeated with a control and a 5200 mg a.i./kg diet test level during a second phase to collect necropsy data. No mortalities were observed in any birds throughout either phases of the study. The 5-day acute dietary LC50 was >5200 mg a.i./kg diet (nominal). Treatment-related reductions in weight gain relative to the control were observed at test concentrations of 2600 and 5200 mg a.i./kg diet during the exposure period. According to visual observation by the study authors, food consumption in the 5200 mg a.i./kg diet treatment group was reduced compared to the control during Phase I, but not during Phase II of the test. However, statistical analyses performed by the reviewer for food consumption determined there was no statistically significant difference in food consumption between any test group and the controls during Phase I of the test, but the birds in the 5200 mg a.i./kg diet group consumed significantly more food than the control birds in Phase II of the test. The 5-day NOAEC of ZA 1963 based on sublethal effects (reduction in weight gain) was 1300 mg a.i./kg diet (nominal). The 5-day LC50 of >5200 mg a.i./kg diet was equivalent to a 5-day LD50 of >2298 mg a.i./kg body weight/day (reviewer-calculated). According to the US EPA classification, ZA 1963 would be classified as practically non-toxic to mallard ducks on an acute dietary exposure basis using the nominal concentration.

Birds, Chronic (OPPTS 850.2300 Avian Reproduction)

MRID: 48073784 The acceptable one-generation reproductive toxicity of picoxystrobin to groups of 16 pairs of 42- week old northern bobwhite quail was assessed over 20 weeks. Picoxystrobin was administered to the birds in the diet at 0, 300, 600 and 1200 mg a.i./kg diet. Mean-measured concentrations were

MRID: 48073785 The acceptable one-generation reproductive toxicity of ZA 1963 (picoxystrobin; purity of 98.4%) to groups of 16 pairs of 23-week old mallard ducks was assessed over 21 weeks. ZA 1963 was administered to the birds in the diet at nominal concentrations of 0 (control), 150, 450 and 1350 mg a.i./kg diet, not adjusted for the purity of the test material. Mean-measured concentrations were

121 comparable to that for the control birds. The effects were not considered to have affected overall survival or reproductive performance of the birds. There were no statistically significant effects on adult mortality, signs of toxicity, behavior, reproductive performance, egg shell thickness or offspring body weight at any of the concentrations tested throughout the study. The NOAEC for mallard duck exposed to ZA 1963 in the diet was 1350 mg a.i./kg diet, the highest concentration tested. This is equivalent to 178 mg a.i./kg bw/day (PMRA reviewer-calculated). The EPA reviewer’s conclusions agreed with most of the study authors’ except for egg production (% eggs set of eggs laid). Percentage of eggs set of eggs laid in the 457 and 1430 mg ai/kg diet levels had a mean value of 76 and 81%, respectively, compared to 88% for the control level. The reviewer’s non-parametric analyses did detect a significant effect at the two highest levels for that parameter; the reviewer concluded that a NOAEC was the lowest level which differed from the author’s parametric analyses which did not detect a significant difference for any parameter. The NOAEC was 157 mg a.i./kg diet, the lowest mean-measured concentration tested, which was lower than author’s results.

Mammals, Acute and Chronic (OPPTS 870.1100 Acute Mammalian Oral and OPPTS 870.3800 Mammalian Reproduction)

MRID: 48073718 In an acute oral toxicity study, 3 female young adult rats were given a single oral dose of DPX- YT669 Technical (Purity: 99.66%; Reference No: DuPont-21522; off-white solid), suspended in deionized water, at a limit dose of 5000 mg/kg bw. Animals were observed at least once daily for the following 14 day study period. Bodyweights were recorded prior to fasting, immediately prior to dosing and again on study days 7 and 14. All animals were necropsied at study termination. Oral LD50 Females > 5000 mg/kg bw. No mortality occurred at the limit dose. Based on the oral LD50, DPX-YT669 Technical meets the criteria for EPA Toxicity Category IV. There was no mortality and all animals gained body weight throughout the study. Two of three animals exhibited diarrhea on the day of dosing only; no other signs of toxicity were observed at any point during the study period. No abnormalities were observed at necropsy. This acute oral study is classified acceptable. This study satisfies the guideline requirement for an acute oral study (OPPTS 870.1100; OECD 425) in the rat. According to the study author, “one rat was removed from the study because the entire amount of the dosing suspension was not administered. A fourth rat was dosed as a replacement.” This substitution had no effect on the overall acceptability or outcome of this study.

MRID: 48073739 In a two-generation reproduction toxicity study, Picoxystrobin (99.3%; Lot # DPX-YT669-028) was administered continuously in the diet to 30 Sprague-Dawley (Crl:CD[SD]) rats/sex/dose group for two consecutive generations at dietary levels of 0, 75, 300, 1000, or 2500 ppm (equivalent to 0/0, 4.2/5.4, 16.9/21.7, 55.5/70.3, and 137.5/173.4 mg/kg/day in males/females, respectively). The P generation animals (30/sex/dose group) were exposed to the test diets beginning at approximately 8-9 weeks of age, for at least 10 weeks prior to mating to produce the F1 litters. F1 offspring selected to be parents of the next generation (30/sex/dose group) were fed the same test diet concentrations as their parents. F1 parents were fed the test diets for at least 10 weeks prior to mating to produce the F2 generation. The F2 offspring were terminated after weaning. Parent animal toxicity: The treatment-related effects produced by picoxystrobin

122 were mainly seen in the 2500 ppm P and F1 parental rats. The effects were on body weights, body weight gains, food consumption, food efficiency changes, organ weight changes, and histopathology. The effects on body weights, body weight gains, food consumption, and food efficiency are tabulated below, and the details are shown in Tables 3a, 3b, 4 and 5.

Percent Change Relative to the Controls (%) in P & F1 Generation Rats at 2500 ppm Periods Body Weights Body Weight Food Food Efficiency Gains Consumption Males Females Males Females Males Females Males Females P Generation Pre-mating ↓4- ↓5-7% ↓18% ↓26% ↓7% ↓8% ↓11% ↓19 7% Gestation ↓7-8% ↓8% ↓10% − Lactation ↓7-8% ↑223% ↓16- − 20% F1 Parental Rats Pre-mating 10- 9-27%↓ ↓8% ↓5% ↓9% ↓9% − ↑5% 26%↓ Gestation ↓8% ↓9% ↓8% − Lactation ↓6-10% ↑304% ↓12% at ↑64% LD 11- 15

Additionally at 2500 ppm, the following differences in organ weights compared to controls were noted in the P generation females: (i) absolute and relative (to body and to brain weight) liver weights were increased by 6-10%; (ii) absolute and relative (to body and to brain weight) thymus weights were decreased by 29-32%; (iii) absolute and relative (to body and to brain weight) non- gravid uterus weights were decreased by 30-32%; (iv) absolute and relative (to body and to brain weight) pituitary weights were decreased by 13-20%; (v) absolute brain weight was decreased by 3%; and (vi) absolute and relative (to body weight) right ovary weights were decreased by 13% each. Findings in the P generation males were limited to increased relative (to body weight) liver weight (incr. 10%) at this dose. Microscopic findings were limited to minimal to moderate lymphoid atrophy in the thymus in the 2500 ppm females (11/30 treated vs. 0/30 controls). The LOAEL for parental toxicity is 2500 ppm (137.5/173.4 mg/kg/day in males/females, respectively) based on decreases in body weight, body weight gain, and food consumption in the P and F1 generation during pre-mating; increased body weight gains in the P and F1 females at the end of the lactation period; organ weight differences; and minimal to moderate lymphoid atrophy in the thymus in P generation females. The NOAEL is 1000 ppm (55.6/70.3 mg/kg/day in males/females, respectively). Offspring toxicity: There were no treatment-related effects on: mortality; clinical signs; live birth, viability, and lactation indices; or pup sex ratio for either generation. There were no treatment-related gross or microscopic findings in the F1 or F2 pups. At 2500 ppm, overall (PND 1-22) pup body weight gains (calculated by reviewers) were decreased in both the F1 and F2 generations by 17-26%. Mean pup body weights/litter at this dose were decreased by 13-23% on PND 8, 15, and 22 in the F1 generation and by 12-14% on PND 15 and 22 in the F2 generation. Organs weights such as

123 thymus, spleen, and thyroid were decreased in F1 and F2 pups. The LOAEL for offspring toxicity is 2500 ppm (137.5/173.4 mg/kg/day in males/females, respectively) based on decreased mean pup body weights/litter and body weight gains in the F1 and F2 generations and decreased organ weights including spleen, thymus, and thyroid. The NOAEL is 1000 ppm (55.6/70.3 mg/kg/day in males/females, respectively). Reproductive toxicity: There were no effects of treatment in either generation on: estrous cycle; sperm parameters; mating, fertility, litter sizes, sex ratio, pup birth weights, or gestation indices; pre- coital interval; or gestation duration. The LOAEL for reproductive toxicity was not observed. The NOAEL is 2500 ppm (137.5/173.4 mg/kg/day in males/females, respectively) (HDT). This study is classified as acceptable/guideline and satisfies the guideline requirements (OPPTS 870.3800; OECD 416) for a two-generation reproduction study in the rat.

MRID: 48073740 In a two-generation reproduction toxicity study, ZA1963 (Picoxystrobin; 93.3% a.i.; Batch No. P25) was administered in the diet to 26 Alpk:APfSD rats/sex/dose group at dietary levels of 0, 50, 200, or 750 ppm (equivalent to 0/0, 5.4/5.8, 21.5/23.4, and 80.0/87.2 mg/kg in males/females during pre-mating) for two successive generations with one litter per generation. The P generation animals were fed the test diets for ten weeks prior to mating to produce the F1 litters. On post-natal day (PND) 29, 26 pups/sex/dose group were selected and fed the same test diet concentration as their dam. These F1 parents were fed the test diets for at least ten weeks prior to mating to produce the F2 litters. No treatment-related effects were observed on mortality, clinical signs, organ weights, or macroscopic or microscopic findings. At 750 ppm, pre-mating body weights were decreased during Weeks 2-11 in the P and F1 parental males and during Weeks 4/5-11 in the P and F1 parental females. Body weight was also decreased during gestation and lactation at day 1 in males and females. Pre-mating (Weeks 1-11) body weight gains (calculated by reviewers) were also decreased, and food consumption was generally decreased during this period in both sexes and generations. There were also decreases in body weights and food consumption in 200 ppm F1 parental males. The LOAEL for parental toxicity is 200 ppm (21.5 mg/kg), based on decreased body weights, body weight gains, and food consumption in the F1 males. The NOAEL is 50 ppm (5.4 mg/kg). There were no effects of treatment on the survival indices, numbers of pups born or born live, numbers of litters or litters with all pups born live, mean litter size, litters with all pups live on PND 22, whole litter losses, or clinical observations, organ weights, or macroscopic or microscopic findings in either the F1 or F2 offspring. At 750 ppm, body weights were decreased in both the F1 males and females on PND 29, and in both the F2 males and females on PND 22 and 29. No treatment-related effect was seen in 200 ppm or lower. The LOAEL for offspring toxicity is 750 ppm (80 mg/kg ), based on decreased body weights in the F1 and F2 pups. The NOAEL is 200 ppm (21.5 mg/kg ). Reproductive performance was not affected by treatment at any dose level. All the reproductive parameters measured were comparable among the treated and control groups. The LOAEL for reproductive toxicity was not observed. The NOAEL is 750 ppm (equivalent to 87.2 mg/kg) (HDT). This study is classified as acceptable/guideline and satisfies the guideline requirements (OPPTS 870.3800; OECD 416) for a two-generation reproduction study in the rat.

Additional Mammalian Toxicity Study with Formulation Product of Picoxystrobin

MRID: 48073720

124 In an acute oral toxicity study (MRID 48073720), 5/sex young adult rats were given a single oral dose of ZA1963 250 g/L SC Formulation (%AI in formulation (w/w): 23.0%; Batch Reference No: J1251/158; cream liquid; density (at 20ºC): 1.09 g/mL) at a limit dose of 2000 mg/kg bw. Test animals were observed for signs of toxicity daily for the following 14 days. Bodyweights were recorded prior to fasting, immediately prior to dosing (study day 1) and again on study days 8 and 15. All animals were necropsied at study termination. Oral LD50 Males > 2000 mg/kg bw; Oral LD50 Females > 2000 mg/kg bw; Oral LD50 Combined > 2000 mg/kg bw. No mortality occurred at the limit dose. Based on the oral LD50, ZA1963 250 g/L SC Formulation meets the criteria for EPA Toxicity Category III. There was no mortality and all test animals gained body weight throughout the study. Apart from a few incidences of diarrhea, there were no significant signs of toxicity. No abnormalities were observed at necropsy. This acute oral study is classified acceptable. This study satisfies the guideline requirement for an acute oral study (OPPTS 870.1100; OECD 401) in the rat.

Non-target Beneficial Insects, Acute (OPPTS 850.3020 Honeybee Acute Contact)

MRID: 48073786 The acute contact and oral toxicity of technical ZA1963 to honey bees (Apis mellifera) was tested in the laboratory. In the 48-hour acute contact test, bees were exposed to technical ZA1963 administered topically to the thorax, at an application rate of 0 (solvent control), 5, 10, 20, 50, 100 and 200 µg a.i./bee. No compound related effects were noted throughout the study period. The 48-hour acute contact LD50 was >200 µg a.i./bee and the NOAEC was 200 µg a.i./bee, the highest dose tested. Dimethoate was used a reference chemical control, and results indicate the bees were reacting normally to pesticides during the study. Due to its low solubility in water, the technical ZA1963 could not be homogeneously dispersed in 50% w/v aqueous sucrose solution. Therefore, the acute oral toxicity of ZA1963 to honey bees could not be tested.

Additional Honeybee Toxicity Study with Formulation Product of Picoxystrobin

MRID: 48073787 The acute contact and oral toxicity of a 250 g/L SC formulation of ZA1963 (YF10267) to honey bees (Apis mellifera) was tested in the laboratory. In the 48-hour acute contact test, bees were exposed to the ZA1963 formulation administered topically to the thorax, at an application rate of 0 (formulation control), 5, 10, 20, 50, 100 and 200 µg a.i./bee. The formulation control consisted of deionized water containing the specific surfactant present in the formulation at the concentration present at the highest dose. In the 48-hour acute oral toxicity test, bees were exposed to the ZA1963 formulation at an application rate of 0 (formulation control), 5, 10, 20, 50, 100 and 200 µg a.i./bee. The formulation control in this acute oral study consisted of 50% w/v aqueous sucrose solution. No compound related effects were noted at any time interval in either the acute contact or oral test. The 48 hour acute contact LD50 was >200 µg a.i./bee, and the NOAEC was 200 µg a.i./bee, the highest dose tested. The 48 hour acute oral LD50 was >200 µg a.i./bee, and the NOAEC was 200 µg a.i./bee, the highest dose tested. Dimethoate was used a reference chemical control in both the acute contact and acute oral tests, and results indicate the bees were reacting normally to pesticides during the two tests. This study is classified as acceptable and satisfies the guideline requirement for an insect pollinator acute contact toxicity study with honey bees. The portion of the acute oral toxicity study with honey bees is classified

125 as supplemental to the USEPA (not a guideline study) and acceptable to PMRA.

Non-target Soil-dwelling Insects, Subchronic (OPPTS 850.6200)

MRID: 48073811 In an 8-week (4-weeks adult mortality; 4 weeks juvenile development) chronic toxicity study on growth and reproduction, earthworms (Eisenia fetida) were exposed to A12796B, a 250 g/L SC formulation of picoxystrobin (ZA1963) at 0 (control), 0.16, 0.31, 0.63, 1.25, 2.5 and 5 mg a.i./kg dry weight of artificial soil. The reference chemical used was benomyl with concentrations of 5 and 10 mg product/kg dry weight of soil. At 4 weeks after application, the picoxystrobin formulation (A12796B) caused 0% mortality at the test concentrations of 0.16, 0.31, 0.63, 1.25 and 2.5 mg a.i./kg soil and 12.5% mortality at the test concentration 5 mg a.i./kg soil. No mortality (0%) occurred in the control group. The 4-week LC50 and NOAEC for mortality of adult earthworm were >5 mg a.i./kg soil and 2.5 mg a.i./kg soil, respectively (reviewer- calculated).The test item caused no statistically significant decrease in adult worm growth (change in fresh weight after 4 weeks relative to initial fresh weight) relative to the control treatment at any concentration tested. A weight increase of 15.2%, 25.0%, 22.5%, 25%, 21.4% 12.8% and 17.4% was recorded in the control group and at the test concentrations of 0.16, 0.31, 0.63, 1.25, 2.5 and 5 mg a.i./kg soil, respectively. The 4-week LOAEC and NOAEC for fresh weight of adult earthworm were >5 mg a.i./kg and 5 mg a.i./kg soil, respectively (reviewer- calculated). At 4 weeks after application, there were no effects on the behavior and morphology of the adult earthworms. The feeding activity of adult earthworms was reduced at concentrations of 2.5 and 5 mg a.i./kg soil compared to the control group. At 8 weeks after application indicates no statistically significant effects on the number of juveniles compared to the control group could be recorded at concentrations of 0.16, 0.31 and 0.63 mg a.i./kg soil. At the test concentrations of 1.25, 2.5 and 5 mg a.i./kg soil, the number of juvenile earthworms was statistically significantly reduced by 20%, 39% and 93% in comparison with the control group. The results obtained from the toxic standard benomyl indicated that for test concentration of 5 and 10 mg product/kg soil, the number of juvenile earthworms was reduced by 62% and 100% in comparison with the control group; thus, the 8-week LC50 for the number of juvenile was 2.55 mg a.i./kg of artificial soil. The 8-week NOAEC, based on the number of juveniles was of 0.63 mg a.i./kg of artificial soil. The 8-week LOAEC was 1.25 mg a.i./kg soil.

Terrestrial Plants, Seedling Emergence and Vegetative Vigor (OPPTS 850.4100 and 850.4150)

MRID: 48073801 The effect of a 250 g/L SC formulation of picoxystrobin (DPX-YT669) on the seedling emergence of ten monocot and dicot crops (monocots: corn (Zea mays), oat (Avena sativa), onion (Allium cepa) and ryegrass (Lolium perenne); dicots: cucumber (Cucumis sativa), oilseed rape (Brassica napus), pea (Pisum sativum), soybean (Glycine max), sugar beet (Beta vulgaris), and tomato (Lycopersicon esculentum)) was assessed over 21 days. Effects on seedling emergence and early growth following soil surface application to planted seeds prior to emergence. Tests were conducted as a limit test at a nominal concentration of 2 L formulation/L (equivalent to 500 g a.i./ha or 0.45 lb a.i./A) in an artificial sandy loam soil mixture (pH 6.0, 1.5% organic matter) under greenhouse conditions. Controls consisted of a carrier control

126 (domestic well water purified by reverse osmosis) and a surfactant control (0.125% non-ionic surfactant). The 21-day emergence, shoot height, shoot dry weight, survival, and visual response data were analyzed and compared to pooled controls. Inhibition of all measured parameters for the ten species was less than 25% relative to the untreated control plants. The most sensitive monocot species in the seedling emergence test was ryegrass, with 15% reduction in shoot dry weight compared to the pooled controls. The most sensitive dicot species was soybean, with a 15% effect based on signs of toxicity. The 21-day EC25 and EC50 for all parameters measured were >2 L formulation/ha (equivalent to >500 g a.i./ha or >0.45 lb a.i./A) for all species tested when compared to the pooled controls. The study author did not establish an NOAEC. The PMRA and EPA reviewers’ conclusions were similar to the study author’s reported EC25 for the ten species. The % inhibition differences between EPA and author’s were mainly from comparing the treatment data to author’s pooled controls and to EPA reviewer’s blank control. Without an NOAEC established by the study authors, the EPA reviewer calculated the NOAEC. The 21-day NOAEC was ≥2 L formulation/ha (equivalent to ≥500 g a.i./ha or ≥0.45 lb a.i./A) for all species tested except oat, onion, cucumber, pea, soybean, and sugarbeet. Based on the p-value of <0.05, the EPA reviewer determined the NOAEC was <2 L formulation/ha (<500 g a.i./ha or <0.45 lb a.i./A) for those affected species. This seedling emergence toxicity study is classified as supplemental to the EPA [it is scientifically sound but deviates from guideline requirement for a tier I seedling emergence toxicity study] and acceptable to the PMRA.

MRID: 48073802 The effect of a 250 g/L SC formulation of picoxystrobin (DPX-YT669) on the vegetative vigour of ten monocot and dicot crops (monocots: corn (Zea mays), oat (Avena sativa), onion (Allium cepa) and ryegrass (Lolium perenne); dicots: cucumber (Cucumis sativa), oilseed rape (Brassica napus), pea (Pisum sativum), soybean (Glycine max), sugar beet (Beta vulgaris), and tomato (Lycopersicon esculentum)) was assessed over 21 days. Tests were conducted at a single nominal concentration of 2 L formulation/L (equivalent to 500 g a.i./ha or 0.45 lb a.i./A) in an artificial sandy loam soil mixture (pH 6.0, 1.5% organic matter) under greenhouse conditions. Controls consisted of a carrier control (domestic well water purified by reverse osmosis) and a surfactant control (0.125% non-ionic surfactant). The 21-day shoot height, shoot dry weight, and visual response data were analyzed and compared to pooled controls. Inhibition of all measured parameters for the ten species was less than 25% relative to the untreated control plants. The most sensitive monocot species in the vegetative test was onion, with 7% effect on visual rating. The most sensitive dicot species was cucumber, with a 20% effect based on visual rating. The 21-day EC25 and EC50 for all parameters measured were >2 L formulation/ha (equivalent to >500 g a.i./ha or >0.45 lb a.i./A) for all species tested when compared to pooled controls. The study author did not establish a NOAEC. The PMRA and EPA reviewers’ conclusions were similar to the study author’s reported EC25 for the ten species. The % inhibition differences between EPA and author’s were mainly from comparing the treatment data to author’s pooled controls and to EPA reviewer’s negative control. Without an NOAEC established by the study authors, the EPA reviewer calculated the NOAEC. The 21-day NOAEC was ≥2 L formulation/ha (equivalent to ≥500 g a.i./ha or ≥0.45 lb a.i./A) for all species tested except onion, cucumber, soybean, sugarbeet and tomato. Based on the p-value of <0.05, the EPA reviewer determined the NOAEC was <2 L formulation/ha (<500 g a.i./ha or <0.45 lb a.i./A) for those affected species. This vegetative vigor toxicity study is classified as acceptable to the PMRA and supplemental to the EPA [the study is scientifically sound but deviates from EPA guideline requirement for a

127 limit vegetative vigor toxicity study].

Non-EPA Guideline Studies

MRID: 48073777 In a 28-day toxicity study, chironomids (Chironomus riparius) were exposed to ZA1963 in laboratory water-sediment systems at 20±°2C using an artificial sediment with a measured organic content of 4.2%. Test systems were prepared by applying the chemical to a sediment- water slurry, shaking and then rolling for two hours. After allowing the system to settle for two days, first instar larvae were introduced into the systems. Test concentrations were 0 (control), 0 (solvent control), 1.25, 2.5, 5, 10, 20, 40, and 80 mg a.i./kg (dry weight) concentrations in a sandy loam sediment. Measured sediment concentrations were <0.1 (

MRID: 48073778 In a 25 day toxicity study, chironomids (Chironomus riparius) were exposed to ZA1963 at 31.25, 62.5, 125, 250, 500, 1000, 2000 μg a.i./L concentrations in the overlying water. On day 0, measured concentrations were

128 where 100% emergence had not occurred on day 25 showed no live larvae. The highest nominal concentrations tested, 1000 and 2000 μg a.i./L, showed zero emergence and were not included in the statistical analyses. No significant effect on emerged sex ratio was observed between the controls and any treatment levels. The reviewer-calculated 28-day EC50 for total emergence was 56.4 μg a.i./L based on mean measured water concentrations (135 μg a.i./L based on initial measured water concentrations as per OECD Guideline 219). The reviewer-calculated 28-day NOAEC and LOAEC, based on total emergence and day 0 measured water concentrations were 19.6 and 46.7 μg a.i./L, respectively, (54 and 118 μg a.i./L based on initial measured water concentrations as per OECD Guideline 219).

MRID: 48073779 The effect of a 250 g/L SC formulation of ZA1963 on communities of freshwater aquatic organisms was investigated in an outdoor pond microcosm study. Cylindrical tanks were used, each containing approximately 1230 litres of water at a depth of 1 metre over 10 cm of sediment, with established communities of plants and invertebrates. The study design consisted of three replicates each of four ZA1963 treatments (5, 30, 100 and 250 g a.i./ha) representing spray drift rates of 2, 10, 40 and 100% of maximum field rate and an unsprayed control. Three applications of each treatment were made at two week intervals in June and July of 1997. Phytoplankton, zooplankton and macroinvertebrates were studied for approximately three months after the final application. Multivariate and conventional univariate statistical methods were applied to the data. The ZA1963 applications were determined to be 93-115% of nominal rates. Depth integrated measured concentrations following the third and final application were <0.15 (

MRID: 48073807 The relationship between changes in picoxystrobin bioavailability and earthworm mortality in treated soil was investigated in a laboratory study. The main aims of the study were: to determine the effect of different moisture levels and ageing of the chemical in soil post application on the toxicity of picoxystrobin to Eisenia fetida in agricultural soil; and to analyze picoxystrobin soil

129 concentrations over time to quantify the potential bioavailable fractions and investigate correlations with the biological data. Two concentrations (4 and 10 mg a.i./kg dry soil) of a 250 g/L SC formulation containing picoxystrobin were evenly incorporated into ‘18 Acres’ agricultural soil (sandy clay loam; 55% sand, 21% silt, 24% clay, pH 5.7, 4.1% organic carbon) maintained at three moisture levels: 25, 40 and 50%. For each moisture level, at both picoxystrobin concentrations, separate aliquots of soil were aged for periods of 0, 1, 3, 7, 11 and 14 days to assess the aging effects on earthworm mortality. When the soil aging periods were completed, E. fetida were weighed and exposed to these soils for a period of 14 days. Samples of treated soil were removed after each incubation time and picoxystrobin residues were analyzed. Various extraction methods, ranging from mild to stringent, were used to extract picoxystrobin: separation of pore water, aqueous calcium chloride, hydroxyporpyl cyclodextrin (HPCD), propanol, and acetone: HCl (75:25) as used in the Residue Analytical method (RAM). A different RAM was used to extract picoxystrobin from the worms in the 4 mg a.i./kg treatments. Surface counts assessments were conducted after 1 and 3 days of earthworm exposure to the incubated soil and mortality assessments were conducted after 7 and 14 days. Surviving E. fetida were weighed after the mortality assessments and the mean weight per worm was calculated. The day 1 surface count assessments showed worms on the soil surface at 50% moisture for all soil aging periods in the control, 4 and 10 mg a.i./kg treatments, although there appeared to be a decline in surface counts with increasing soil age for all three treatments. By the day 3 assessments, there was a clear trend of decreasing surface counts as soil age increased in the soil treated with 4 mg a.i./kg at 50% moisture and the control. The surface counts in the 10 mg a.i./kg, 50% moisture treatment remained high regardless of the soil age. The highest number of worms on the surface was observed in the 50% moisture treatments at 10 mg a.i./kg, suggesting that worms were more rapidly affected in soil treated with 10 mg a.i./kg at 50% moisture than in other treatments. The mortality assessments showed that 10 mg a.i./kg was highly toxic to earthworms. In the majority of cases 100% mortality occurred within 7 days at the 25%, 40% and 50% moisture levels regardless of soil ageing. This seems to indicate that there was sufficient bioavailable picoxystrobin in the 18 Acres soil type treated with 10 mg a.i./kg at moisture levels between 25% and 50% to give complete kill of earthworms even after fourteen days of aging. The 18 Acres soil treated with 4 mg picoxystrobin/kg was generally less toxic than soil treated with 10 mg a.i./kg. This was most apparent in soils with lower moisture levels. However, by assessment day 14, high levels (>67%) mortality were observed in all moisture level and age combinations. Mortality of E. fetida appeared to be higher in treatments were where residues of picoxystrobin were 0, 1 and 4 days old (days 0, -1, and -4) compared to those soils treated 7, 11 and 14 days prior to the introduction of earthworms. Recovery of “free” picoxystrobin from the extracted pore water of the treatments with 40 and 50% moisture indicated that more chemical was available in the wettest soil. This could explain the increased mortality observed in the 50% moisture treatments in the worm mortality bioassay. Recoveries of weakly bound picoxystrobin in the aqueous calcium chloride extracts of the 25, 40 and 50% moisture soils were very similar. This may suggest that the extraction technique is unlikely to prove a good indicator of bioavailability in this case. Recoveries of weakly bound picoxystrobin in the HPCD extracts of the 25 and 50% moisture soils were quite similar for the 4 mg a.i./kg treatments; the recoveries in the 40% moisture soil were slightly higher than in the other two moisture soils. At the 10 mg a.i./kg treatment, the recoveries of picoxystrobin in the extracts from the different soil moistures were all different from each other, with again the highest extraction from the 40% moisture level soil. The meaning of these differences is however

130 unclear. The propanol extraction extracted a large proportion of the tightly bound picoxystrobin remaining in the soil. In all but one case propanol extracted more than 65% of the applied picoxystrobin at 0 days after treatment. Thus, it is doubtful that this method reflects the amount of chemical available to worms, and it is also likely that this extractant was disrupting the soil structure. The RAM extraction was observed to remove picoxystrobin remaining in the soil after the mild and propanol extractions, which shows that these extraction systems were not removing total residues. During the 14-day course of the study there were clear trends in all extracts which showed that availability of picoxystrobin decreased over time. This decline exceeded the expected rate of degradation of picoxystrobin in this soil and also indicated that there was an increased level of strong adsorption occurring over time. Worm extract data showed that in the 4 mg a.i./kg application rate soils, levels of 1.4-6.0 ug/g picoxystrobin (wet weight) were found in the live worms. In conclusion, picoxystrobin was highly toxic to E.fetida at rates of 4 mg a.i./kg and above under the experimental conditions. Mortality of E. fetida appeared to be higher in soils treated with picoxystrobin at -4, -1 and 0 days compared to the soils treated at -14, -11 and -7 days. There was sufficient bioavailable picoxystrobin in soil treated with 10 mg a.i./kg at moisture levels between 25% and 50% to give complete kill of earthworms even after 14 days of aging. The highest level of mortality was observed in soils at 50% moisture, which was supported by the pore water recovery data where more picoxystrobin was available in the 50% moisture soil compared with the 40% moisture treatment. The bioavailability phase of the study suggested that the pore water technique appeared to show the best correlation with the worm mortality data. All the techniques showed that the availability of picoxystrobin decreased during the course of the 14-day study. This decline exceeds the expected rate of degradation of picoxystrobin in this soil and would indicate that there was also an increased level of strong adsorption over time.

MRID: 48073808 A field monitoring study was conducted in 99 fields across the major cereal growing areas of France (59 fields), U.K. (20 fields) and Germany (20 fields). The experiment was not conducted in compliance with Good Laboratory Practice Standards, nor according to the ISO guideline 11268-3 for field earthworm testing. Acanto 250 SC [A-12796B], a 250 g/L SC formulation of picoxystrobin, was applied to field plots of wheat or barley at rates of 0 (control), 75, 125, 175 and 250 g a.i./ha in France, the U.K. and Germany. An additional rate of 200 g a.i./ha (tank mixed with 360 g a.i./ha fenpropidin and 100 g a.i./ha propiconazole [formulation Agent 575 EC (A_7504) emulsifiable concentrate containing nominally 450 g a.i./L fenpropidin and 125 g a.i./L propiconazole]) was applied in Germany only. Two applications were made to represent realistic worst-case field use, based on the labelled growth stage application across Europe. The method of application was not reported. The first application (T1) was at Zadok’s growth stage 31-32, while the second application (T2) occurred 21 days after T1. Plots were a minimum of 2 m x 10 m in size. Treatments were allocated as a random block design. Soil pH ranged from 5.2 to 8.4 with percent organic matter ranging from 1.1 to 6.9%. The only exception was site M- UK16, where organic matter was 50%, as soil characteristic found in only a small proportion of the European cereal acreage. Monitoring of the soil surface for earthworm mortality was conducted 3 (± 1 day), 7 (± 1 day), and 14 (± 1 day) days after each application, giving a total of 6 assessment times. Four visual observations per plot, per assessment, were taken using 50 cm x 50 cm quadrats at preassigned locations in each plot. The number of dead and live earthworms noted on the soil surface was recorded. Thirty-eight of the 99 sites were subsequently visited to

131 estimate the earthworm populations present at those sites. Surface mortality was then compared to population estimates to give a percentage effect of the estimated population. In the majority of sites, earthworm populations were assessed by digging four 25 x 25 cm holes as far down as the soil cultivation would allow and sorting the soil by hand to count earthworms. Numbers were reported on a per square meter basis. No other technique was used (e.g. formalin) to optimize field population sampling. Taxonomic identification was conducted on all earthworms collected from both the soil surface monitoring and the earthworm population determinations. Local weather data (with a particular emphasis on rainfall) were collected and soil analyses were conducted on samples from all sites. Earthworm mortalities were totalled across the 6 assessment times. Mortalities ≥5 earthworms/m2 in any picoxystrobin treatment were deemed to be a significant effect. Using this criterion, significant effects were observed at 14 sites out of the 99 trials (14%). They were not evenly distributed across Europe, with significant effects observed at 11 out of 20 sites in Germany (55%), 1 out of 20 sites in the U.K. (5%) and 2 out of 59 sites in France (3%). Generally, the highest mortalities were associated with the highest application rate of 250 g a.i./ha, and a dose-response relationship was reported. However, no endpoint values were reported in the study. The magnitude of the effect varied, with 9 trials having an effect ranging from 5 and 40 earthworms/m2 and 5 trials having effects between 41 and 81 earthworms/m2. Comparing the number of dead earthworms against an estimate of the population for 12 of the 14 sites where significant effects were observed (the percentage effect at 2 sites where effects of ≥ 5 /m2 were observed was not determined) gave a spread in the percentage effect between 2 and 39%. Two sites had an effect of less than 5%, 5 sites between 10 and 20%, 3 sites between 20 and 30% and 2 sites between 30 and 40%. According to the authors this level of effect is unlikely to have a long term effect on earthworm populations. In all three countries (France, Germany and the UK), the most common taxonomic groups of the dead earthworms from the soil surface were juvenile Aporrectodea spp. and juvenile Lumbricus spp. Summed across all three countries the most abundant adult earthworms were Aporrectodea caliginosa caliginosa and Allolobophora chloratica. The most common taxonomic groups reported from the population sampling were also juvenile Aporrectodea spp. and juvenile Lumbricus spp. Overall when the species and taxonomic groups from the population sampling were compared to the dead earthworms collected, no species or group appeared to be more affected by the picoxystrobin applications. The earthworms that were affected were approximately proportional to those present in the population. More effects were observed at T1 (Zadok’s Growth Stage 31-32) than at T2 (approximately 21 days later). At the T1 application, significant (≥ 5 /m2) surface earthworm mortality was observed predominantly at sites which received significant rainfall both before and after applications of picoxystrobin. However, this observation is not conclusive, as not all sites fulfilling these criteria had significant surface earthworm mortality in the picoxystrobin treatments. In some cases this was due to very low earthworm populations at these sites, but there were a number of sites with large populations where this hypothesis did not hold true, indicating that there may be other factors involved. The relationship between rainfall and earthworm mortality on the soil surface which was evident at T1 does not apply to T2. Many sites received significant rainfall both before and after application of picoxystrobin, however there were only two sites with an earthworm mortality of 5 or more per m2 There was no apparent relationship between surface earthworm mortality and soil type. In their conclusion, the authors indicate that there was a low percentage (14%) of sites where surface earthworm mortality exceeded 5/m2. Most of these were following the T1 application and were linked to rainfall. Significant (5/m2) surface earthworm mortality was observed

132 predominantly at those sites that received significant rainfall both before and after application of picoxystrobin. In conclusion, the results of the study suggest that the earthworm LD50 would be greater than 250 g a.i./ha based on mortality of the population and in the different field trials.

MRID: 48073809 Nine field trials were conducted in Northern France to assess the impact of picoxystrobin application on earthworm populations and their subsequent recovery over the following year. Acanto 250 SC (nominal 250 g/L picoxystrobin) was applied twice, with approximately a 21-day interval, to field plots of wheat or barley at rates of 250 g and 125 g a.i./ha. Tap water was applied twice as a control, and Benomyl was applied once at 4 kg a.i./ha with the first picoxystrobin spray, as a toxic reference. This application regime was chosen to represent the maximum label rate and a realistic worst case field use in France. Earthworm populations were sampled prior to application and at approximately one, five to six and twelve months after the second application. Surface effects were assessed approximately 2-4, 6-8 and 12-15 days after each application. All earthworms were taxonomically determined and total earthworm numbers and weights, species and key “ecological” groupings (e.g., anecic and epigeic and adult and juvenile earthworms) were recorded. No more than 4 dead earthworms/m2 were found on the soil surface during the 125 days post application at any of the nine sites and any of the plots. In the benomyl sites, population sampling showed that there were statistically significant differences in total abundance of earthworms between the benomyl treatment and the control at 1 month at all but one site (Sarthe R-FR09) and in total biomass at five out of the nine sites (Champagne R- FR01, Lorraine R-FR02, Pas de Calais R-FR04, Picardie R-FR05 and Bretagne R-FR08), thus demonstrating the validity of the test system. In only one of the nine sites (Pas de Calais R- FR04) was there any statistically significant decrease in total earthworm abundance from picoxystrobin treatments at either rate or at any sampling period post-application. This effect was found only at the first post-treatment sampling (1 month) at 250 g a.i./ha. Three of the nine sites (Lorraine R-FR02 at 125 g a.i./ha, Pas de Calais R-FR04 and Picardie R-FR05 at 250 g a.i./ha) were reported showing a statistically significant decrease in earthworm biomass in the picoxystrobin treatments but no significant effects were evident later than 189 days after application (DAA). No dose-response relationship was apparent. By 12 months post-application, no significant effects were found on total earthworm abundance or biomass in either of the picoxystrobin treatments at any of the nine sites. There were no apparent trends in effects of picoxystrobin on total adults and total juveniles, though juvenile biomass may have been more sensitive than juvenile abundance. Total juvenile abundance decreased significantly at only one site (Lorraine R-FR02, 49 and 373 DAA) and total juvenile biomass in three (Lorraine R-FR02 49 and 189 DAA, Pas de Calais R-FR04 43 and 381 DAA and Picardie R-FR05 at 44 and 184 DAA). Total adult abundance decreased significantly at two sites (Pas de Calais R-FR04 at 43 DAA and Picardie R-FR05 at 184 DAA) and total adult biomass at two different sites (Lorraine R-FR02 at 189 DAA and Sarthe F-FR09 at 396 DAA). By 12 months post application only one site showed a statistically significant decrease in total juvenile abundance (Lorraine R-FR02, 250 g a.i./ha) although no effect on juvenile biomass; one showed a decrease in total juvenile biomass (Pas de Calais R-FR04, 125g a.i./ha) and one showed a decrease in total adult biomass (Sarthe R-FR09, 125 g a.i./ha). All other sites showed no significant decreases in total juvenile and total adult abundance at all of the nine sites and in total adult and total juvenile biomass at all sites except R-FR03 (Bourgogne) and F-FR06 (Beauce). No significant effect was found on any of the ecological groups in either of the picoxystrobin treatments later than 189 DAA at any of

133 the sites. On an individual taxon level, 19 taxonomic groups were identified across the nine sites. Of these 19 taxa only five showed any statistically significantly effect in the picoxystrobin treatments at any time post-application, at any site (Aporrectodea spp. sensu lato J, Apporrectodea caliginosa caliginosa A, Aporrectodea longa A, Lumbricus spp. J and Octolasion spp. J). There were no consistent trends in effects on individual taxa. A dose response was not always evident and in only 23 out of 1140 comparisons between individual taxa numbers and biomasses were there any significant differences from the control (P=5%). As such, the site at Pas de Calais (R-FR04) at 125 g picoxystrobin/ha would represent the most sensitive example. The reference item treatment showed individual taxon effects in all but two of the sites (R-FR06 Beauce and R-FR09 Sarthe). Overall it can be concluded that - There were no unacceptable effects on earthworm populations and biomass (recovery within 1 year) following application of picoxystrobin at realistic worst-case field rates in these nine sites in Northern France; - There were no apparent differences between effects on total juveniles and adults though it is considered that juvenile biomass may be a more sensitive indicator; - Endogeic groups were generally more affected than anecics. Epigeics showed no significant effects at all and all ecological group effects had completely recovered from any effects at all and all ecological group effects had completely recovered from any effect with no significant differences found by 12-months post application; - Individual taxon effects were very variable, but all were non-significant by 12-moths post application, apart from occasional significant decreases in abundance of Aporrectodea spp. Sensu lato J and Octolasion spp. J. Though these decreases are worth nothing, they frequently did not show a dose response and are not reflected in the results across all nine sites and may be viewed as anomalous when considered in the broad context provided by the nine studies together; Picoxystrobin applied at rates up to 2 x 250 g a.i./ha is not expected to cause unacceptable effects on earthworm populations in the field.

MRID: 48073810 An earthworm field study was conducted in Sweden following the BBA Guideline for testing the Effects of Pesticide on Earthworms in the filed (Kula and Kula, 1994) and the ISO Guideline 11268-3: Soil quality – effects of pollutants on earthworms. Part 3: Guidance on the effects in field situations (Anonymous, 1999). The study was carried out in the region of Uppsala in a winter wheat field (variety Kosack). After harvest of the crop, a cover crop (winter wheat, variety Kosack) was planted in order to guarantee a permanent cover. Test organisms were naturally occurring field resident populations of earthworms present at the field site. Twenty four plots, each 12 x 17 m, were arranged in a 4 x 6 formation, each plot surrounded by a 5 m guard row. Pre-treatment sampling was conducted to determine the density, diversity and homogeneity of earthworm populations at the site. The test item picoxystrobin was applied at nominal rates of 0 (control with tap water), 62.5, 125, 250 and 500 g a.i./ha in 300 L water per ha. Application was carried out once at BBCH 31-32 (27-05-2003). The formulated material was sprayed directly onto the plots to simulate a worst-case scenario for this formulation. The toxic reference BenlateTM (a.i. benomyl) was applied once to the plots as reference item at a rate of 4 kg a.i./ha. Actual applied rates of the item and the toxic reference were within the range of 3.4% to + 1.5% of target rate. Irrigation was applied to the field site in order to ensure earthworm exposure to the

134 test item and intentionally cause acute effects. As the soil was not sufficiently moist at treatment application, the field site was irrigated with 15.2 mm 5 days before application. A second irrigation of 15.1 mm took place on day 1 after application. Earthworm surface sampling for the monitoring of direct mortality effects on earthworms was performed every day from day 0 to 10 days after application. The number of dead earthworms was counted and species identification (where possible) of the collected earthworms was performed. Counting and collections were done by taking 4 visual observations per plots, per assessment, from a 1 m2 monitoring area. Earthworms were sampled from four 50 x 50 cm sampling areas per plot per sampling occasion. Defined sample areas were sampled to assess earthworm population before application (2 days before application, DBA) and 1 month (31 days after application, DAA), 4 months (122 DAA) 10 months (325 DAA) and 12 months (374 DA) after the application. 16 samples were taken from each treatment on each of the sampling occasions. Earthworms were sampled using the formaldehyde extraction method (Raw 1959). For this a 0.2% formaldehyde solution was uniformly applied at a rate of 40 L/m2 to the 4 sample areas within each of the 4 plots of each of the 6 treatments. As soon as the worms appeared on the soil surface they were collected. The earthworms collected were taxonomically identified, and their abundance and biomass recorded per sub-sample, plot, and sampling occasion. A total of 14 different taxa were observed and identified. The effect of the test item was assessed by comparing the data from the plots treated with test item with the water treated control. Surface sampling after application showed that earthworms were affected by all investigated rates of the test item. There were no dead earthworms in the control. Statistically significant reductions were reported in plots treated with the toxic reference benomyl. Total earthworm numbers were significantly reduced to 17.5% in comparison to total earthworms in control plots (31 DAA). The effect of the toxic reference persisted throughout the test and earthworm numbers were still at 39.5% at 374 DAA. Total earthworm weights were significantly reduced to 39.5% at 374 DAA. Total earthworm weights were significantly reduced to 33.5% (31 DAA) in comparison to total earthworms in control plots. The effect of the toxic reference persisted throughout the test and earthworm weights were still at 39.5% at 374 DAA. For population sampling, reductions in total earthworm numbers were reported to be statistically significant (p=5%) compared to the control in the 250 g picoxystrobin/ha treatment at 31 DAA and in 500 g a.i./ha treatment at 31, 122 and 374 DAA (detransformed unadjusted/adjusted means). Total earthworm biomass was found significantly reduced compared to the control (p=5%) in the 500 g a.i./ha treatment at 31 DAA. There were no statistically significant reductions compared to the control by 374 DAA in any of the picoxystrobin treatments according the study authors. The only groups or taxa where significant (p = 5%) reductions in numbers was determined to be at 374 DAA were Aporrectodea caliginosa adults in the 62.5 g a.i./ha and 250 g a.i./ha treatments and epilobous juveniles and total juveniles at 500 g a.i./ha. For biomass, the only groups or taxa where significant reductions remained at 374 DAA were in Apporrectodea caliginosa adults in the 125 g a.i. ha treatment and in epilobous juveniles and total juveniles at 500 g a.i./ha. Using probit analysis to determine a dose/response effect of picoxystrobin on earthworm field species and using William Multiple Sequential t-test procedure (OECD Guideline) to determine the 31-day NOEC for number of earthworm impacted by picoxystrobin, the PMRA determined a 31-day EC50 of 168.5 g a.i./ha, a 31-day NOEC < 62.5 g a.i./ha and a LOEC ≤62.5 g a.i./ha at 31 DAA. However, the authors of the study concluded that at rates up to and including 250 g a.i./ha, recovery of total earthworm populations had occurred by one year after application (374 DAA) with the exception of the adult species number and biomass of Aporrectodea caliginosa at a rate of 62.5 and 125 g a.i./ha, respectively.

135 At a rate of 500 g a.i./ha, a reduction in the number of earthworms was observed one year after application, which is probably resulting from a slight reduction in juveniles. The PMRA concurs to these observations.

MRID: 48073812 In a 14 day acute toxicity study, earthworms (Eisenia foetida) were exposed to AB12796B, a 250 g/L SC formulation of ZA1963 (picoxystrobin), at 0 (control), 2.1, 3.2, 5.0, 7.7 and 12.0 mg a.i./kg dw of artificial soil. The experiment was carried out in accordance with OECD 207, Earthworm, Acute Toxicity Tests. After 14 days of exposure, 0%, 2.5%, 97.5%, 100% and 100% mortality was observed in test concentrations of 2.1, 3.2, 5.0, 7.7 and 12.0 mg a.i./kg dw of soil, respectively. No mortality was observed in the control. The 14-day LC50 was 4.0 mg a.i./kg dw soil. The 14-day NOEC based on mortality was 3.2 mg a.i./kg dw soil. In the most recent test with the reference item, 2-chloroacetamide, the 14-day LC50 was 24.2 mg/kg dw soil. This result confirms that the worms were of the expected sensitivity. Earthworm mean fresh weights were reduced by 13.5% in the control and 10.4%, 28.0%, 98.7%, 100% and 100% for the treated groups of 2.1, 3.2, 5.0, 7.7 and 12.0 mg a.i./kg dw of soil, respectively. The weight reduction was statistically significant relative to the control at the test concentration of 3.2, 5.0, 7.7 and 12.0 mg a.i./kg dw of soil. The 14-day NOAEC based on body weight changes was 2.1 mg a.i./kg dw soil.

MRID: 48073813 In a toxicity study on earthworm species (annelida; Oligochaeta) under field conditions the naturally occurring earthworm population was exposed to a 250 g/L SC formulation of picoxystrobin (A12796B). The objective of the study was to determine the effects and potential recovery of earthworm populations following initial mortality brought about by the application of 250 g/L SC formulation of picoxystrobin (A12796B) and forced irrigation, applied in spring braley (Hordeum vulgare, variety Hanka) with Festuca pratensis as ground cover crop under field conditions. The study was conducted in a spring barley field in Polditz, between Leisnig and Grimma in Saxony. The test consisted of 6 treatments (test item in four increasing rates, control, toxic standard) arranged in a randomized complete block design. Each treatment consisted of 4 replicate plots of 16 m x 24 m (384 m2). The soil was a clay loam (Dystric + Cambisol) with a mean pH (CaCl2) of 6.2, mean cation exchange capacity of 10.9 cmol /kg, total organic carbon content of 0.9-1.2%, and a mean water holding capacity of 37% w/w. The test item was applied at rates of 62.5, 125, 250 and 500 g a.i./ha in a water volume of 300 L/ha. With these application rates a multi-rate study approach was chosen in order to cover the worst case potential exposure scenarios (i.e. the top dose reflects the worst case highest possible dose of 2 applications at max. rate assuming no degradation). Benomyl was applied as reference substance (toxic standard) to establish the sensitivity of the test system. As a control 300 L/ha tap water was applied. All treatments were applied once on the same day. Earthworm population were assessed on six sampling dates in the test duration of one year (pre-application sampling 1 to 2 days before application; and five post-application samplings at 49 days after application (DAA), 108 DAA, 177 DAA, 303 DAA, and 380 DAA). Furthermore, earthworms were assessed on the soil surface for a period of 11 days after application. Residue analysis in affected earthworms as well as on soil was carried out. To determine the potential recovery of earthworm populations following application of A12796B, species, age, distribution, abundance and biomass of earthworm communities were assessed. Reduction in abundance and biomass of earthworm species in the test item treatment when compared to the control (detransformed

136 unadjusted/adjusted means as % of control) were used as primary toxic endpoints. Surface sampling after application showed that earthworms were affected by all investigated rates of the test item. There were no dead earthworms in the control. With a cumulative abundance of dead worms per m2 of 0.13, 0.13, 4.0 and 10.6 at 62.5, 125, 250 and 500 g a.i./ha, respectively, earthworm mortality of emerged animals was low in all but the highest treatment levels in which the mortality continually increased over the observation period and amounted to 16.7% of the population assessed at pre-sampling. The sensitivity toward the test item differed on a species level and with age stages. In relation to the L terrestris population found in pre-sampling (100%) a proportion of 53% were assessed dead on the soil surface as opposed to only 9.7% geophagous species (as % of pre-sampling geophagous species). Compared to the adult and juvenile population at pre-sampling (corresponding parameters at pre-sampling 100%), 19.4% juveniles and 10% adults were assessed dead on the soil surface. For population sampling there were no statistically significant effects reported on total earthworm numbers (detransformed unadjusted/adjusted means) or total earthworm biomass (untransformed unadjusted/adjusted means) or total earthworm biomass (untransformed unadjusted/adjusted means) by the test item as compared to the control on any sampling date. On a species level both numbers of A. caliginosa A. and A. caliginosa J. were significantly reduced on the 1st sampling date (49 DAA) at 62.5 g a.i./ha. This is further reflected in a statistically significant reduction in numbers of total adult A. and total endogeic A. this effect was not observed in the higher treatment groups. The highest application rate of 500 g picoxystrobin/ha had a statistically significant effect on the abundance of L. terrestris A. (108 DAA and 177 DAA) and L. spp. J. (108 DAA). Accordingly, the reduction in abundance of total anecic A. (L. terrestris A.) was statistically significant 108 DAA and 177 DAA. There were no statistically significant differences in biomass reported on a species level. In the treatment with 250 g a.i./ha applied reductions in total numbers did not exceed 30% (108 DAA). At an application rate of 500 g a.i./ha total numbers were reduced by 31 and 39% 49 and 108 DAA. On all following sampling dates, total numbers showed a recovery. Total biomass (untransformed unadjusted/adjusted as % control) was reduced by approximately 34% at 500 g a.i./ha 49 DAA, 108 DAA, and 177 DAA and showed recovery by 380 DAA. After one year (380 DAA) it is reported that endogeic species showed no difference to the control. Anecic species (L. terrestris A.) were reduced by 75% and 85% 108 and 177 DAA at an application rate of 500 g a.i./ha. Lower application rates showed no statistically significant differences. On all other sampling dates, numbers were to low for statistical analysis, so that the effect of the test item on anecic A. over the test period was determined not detectable. Results of residue analysis in earthworms showed increased values with increasing amounts of picoxystrobin applied (Evan, 2003b). Summarising the results, this field test indicated that a single application of picoxystrobin at rates of 62.5, 125, 250 and 500 g a.i./ha did not result in significant effects on natural earthworm population in terms of total abundance or total biomass on the given test site. This equally applies to A. caliginosa and endogeic A. Results of the species L. terrestris indicate a greater sensitivity which would be attributed to the surface feeding of this species since the test item showed no significant infiltration into deeper soil profiles (Evans, 2003A). The study authors indicated that no conclusions could be made about the recovery of L. terrestris A. due to their low numbers on the last two sampling dates.

MRID: 48073814 In a toxicity study on earthworm species under field conditions, the naturally occurring earthworm population was exposed to a 250 g/L SC formulation of picoxystrobin (A12796B), in

137 a spring barley field in Appel, near Hamburg, North Germany. The objective of the study was to determine the effects and potential recovery of earthworm populations following initial mortality brought about by the application of 250 g/L SC formulation of picoxystrobin (A12796B) and forced irrigation, applied in spring barley (Hordeum vulgare, variety Barke) with Festuca rubra as ground cover crop under field conditions. The test consisted of 6 treatments arranged in a randomized complete block design. Each treatment consisted of 4 replicate plots of 15 m x 19 m (285 m2). The test item was applied at rates of 0 (tap water control), 62.5, 125, 250 and 500 g a.i./ha in a water volume of 300 L/ha. With these application rates a multi-rate study approach was chosen in order to cover the worst case potential exposure scenarios (i.e. the top dose reflects the worst case highest possible dose of 2 applications at max. rate assuming no degradation). Benomyl was applied as reference substance (toxic standard) to establish the sensitivity of the test system. All treatments were applied once on the same day. Earthworm populations were assessed on six sampling dates in the test duration of one year (pre-application sampling 2 to 3 days before application; and at 53, 109, 179, 312 and 381 days after application (DAA). Furthermore earthworms were assessed on the soil surface for a period of 9 days after application. Residue analysis was carried out on the soil and in affected earthworms. To determine the potential recovery of earthworm populations following application of A12796B species, age, distribution, abundance and biomass of earthworm communities were assessed. Reduction in abundance and biomass of earthworm species in the test item treatment when compared to the control (detransformed unadjusted/adjusted means as % of control) were used as primary toxic endpoints. All validity criteria for earthworm field tests (key species, earthworm abundance of 60 worms/m2, and sensitivity of the site for Benomyl) were met. Therefore, the site was considered suitable for the field trial. Surface sampling after application showed that earthworms were affected by all investigated rates of the test item. There were no dead earthworms in the control. Cumulative abundance of dead worms per m2 were 4.0, 7.6, 12.5, and 18 at 62.5, 125, 250 and 500 g picoxystrobin/ha, respectively. In the highest treatment rate, mortality was observed over a period of 8 days following application. Cumulative mortality at an application rate of 500 g a.i./ha amounted to 25.4% of the population assessed at pre-sampling. The sensitivity toward the test item differed on a species level and with age stages. In relation to the L. terrestris population found in pre-sampling (100%), a proportion of 42% were assessed dead on the soil surface as opposed to only 20% geophagous species (as % of pre-sampling geophagous species). Compared to the adult and juvenile population at pre-sampling (corresponding parameters at pre-sampling 100%), 29% juveniles and 16% adults were assessed dead on the soil surface. During the test period, earthworm numbers were related to soil moisture and were lowest on sampling dates with low moisture content combined with high soil temperature on pre-sampling and Day 381 after application. For population sampling, reduction in total earthworm numbers were statistically significant compared to the control in the 250 g a.i./ha treatment at 109 and 179 DAA and in the 500 g a.i./ha at 53, 109, 179 and 381 DAA (detransformed unadjusted/adjusted means). On a species level, the test item had the greatest effect on L. spp., all other species showed no statistically significant reduction. L.spp J. was statistically reduced at 250 g a.i./ha on 109 and 312 DAA and at 500 g a.i./ha on 109 and 179 DAA. Accordingly the reduction in abundance of total juveniles was statistically significant at 500 g a.i./ha on 53, 109, 179 and 381 DAA. There were no statistically significant reductions in total earthworm biomass at any application rate or sampling occasion. Total juvenile biomass was significantly reduced at 500 g a.i./ha on 109 and 179 DAA. There were no statistically significant differences for total endogeic worms. Total anecic worms were not analysed due to

138 low numbers. Summarising the results, this field test indicates that a single application of picoxystrobin at rates of 250 and 500 g a.i./ha had a negative effect on natural earthworm population in terms of abundance and biomass on the given test site. At 250 g a.i./ha, earthworm populations fully recovered in the course of one year. An application rate of 500 g a.i./ha reduced total earthworm numbers by more than 50% (179 DAA). In the course of the following months, populations recovered, but were still reduced by approximately 39% in total earthworm numbers and 42% in total biomass after one year, the reduction in total numbers being statistically significant. Based on EPPO standard (2003), picoxystrobin at 500 g a.i./ha would be categorized as high risk because of the effects >50% and the lack of recovery after one year exposure. Juvenile earthworms were more sensitive (40% reduction in numbers and 22% reduction in biomass), with numbers of juveniles being statistically significantly different after one year. L. spp. J. was affected most during the test period and seemed to recover after one year, but numbers were too low for statistical analysis.

MRID: 48073815 In a 14-day acute toxicity study, earthworms (Eisenia foetida) were exposed to R408509 (Compound 8), a transformation product of ZA1963, at 0 (control), 9.9, 100 and 1000 mg/kg of artificial soil. The reference chemical used was 2-chloracetamide with concentrations of 0 (control), 34, 43, 53 and 66 mg/kg soil. The experiment was carried out in accordance with OECD 207, Earthworm, Acute Toxicity Tests. After 14 days of exposure, mortalities were 0% in the control, 9.9 and 100 mg R408509/kg test concentrations. Mortalities were 100% in the 1000 mg R408509/kg soil test concentration. The 14-day LC50 was 320 mg R408509/kg soil. The 14- day NOEC based on mortality was 100 mg/kg soil. The 14-day LC50 for the reference chemical was 68 mg/kg soil, within the normal range and confirming that the worms were of the expected sensitivity. No significant change in body weight was detected between the control and the 9.9 and 100 mg/kg test concentrations. The % change in body weight (adjusted for mortality) between day 0 and day 14 was an average of -9.6%, -10.2%, and -11.1% in the control, 9.9 and 100 mg/kg soil treatment levels, respectively. There was 100% mortality in the 1000 mg/kg soil test concentration, thus, this concentration was not included in the analysis. The 14-day NOEC based on body weight changes was 100 mg/kg soil.

MRID: 48073816 In a 14-day acute toxicity study, earthworms (Eisenia foetida) were exposed to R403814 (Compound 3), a transformation product of ZA1963, at 0 (control), 8.7, 100 and 1000 mg/kg of artificial soil. The reference chemical used was 2-chloracetamide with concentrations of 0 (control), 34, 43, 53 and 66 mg/kg soil. The experiment was carried out in accordance with OECD 207, Earthworm, Acute Toxicity Tests. After 14 days of exposure, mortalities were 2.5%, 0%, 0% and 100% in the control, 8.7, 100 and 1000 mg R403814/kg test concentrations, respectively. The 14-day LC50 was 320 mg R403814/kg soil. The 14-day NOEC based on mortality was 100 mg/kg soil. The 14-day LC50 for the reference chemical was 68 mg/kg soil, within the normal range and confirming that the worms were of the expected sensitivity. As there was 100% mortality in the 1000 mg/kg soil test concentration, this concentration was not included in the analysis for bodyweight. After 14 days of exposure, a significant change in body weight was detected between the control and the 100 mg/kg test concentration. The % change in body weight (adjusted for mortality) between day 0 and day 14 was an average of -6.6%, -7.7% and +1.2% in the control, 9.9 and 100 mg/kg soil treatment levels, respectively.

139 The 14-day NOEC based on body weight changes was 8.7 mg/kg soil. However, the effects at the 100 mg/kg test concentration were positive, with an increase in body weight compared to the control. Thus the 14-day NOAEC was 100 mg/kg.

MRID: 48073817 In a 14-day acute toxicity study, earthworms (Eisenia foetida) were exposed to R403092 (Compound 2), a transformation product of ZA1963, at 0 (control), 17.5, 100 and 1000 mg/kg of artificial soil. The reference chemical used was 2-chloracetamide with concentrations of 0 (control), 34, 43, 53 and 66 mg/kg soil. The experiment was carried out in accordance with OECD 207, Earthworm, Acute Toxicity Tests. No statistically significant differences in mortality were observed between any test concentration and the control. After 14 days of exposure, mortalities were 2.5%, 0%, 2.5% and 7.5% in the control, 17.5, 100 and 1000 mg R403092/kg soil test concentrations. The 14-day LC50 was >1000 mg R403092/kg soil. The 14-day NOEC based on mortality was 1000 mg/kg soil, the highest concentration tested. After 14 days of exposure, a significant change in body weight was detected between the control and the highest test concentration, 1000 mg/kg soil. The % change in body weight (adjusted for mortality) between day 0 and day 14 was an average of -2.6%, -4.6%, -4.5%, and -11.6% in the control, 17.5, 100 and 1000 mg/kg soil treatment levels, respectively. The 14-day NOEC based on body weight changes was 100 mg/kg soil. The 14-day LC50 for the reference chemical was 68 mg/kg soil, within the normal range and confirming that the worms were of the expected sensitivity.

MRID: 48073818 The effects of a ZA 1963 25SC, a 250 g a.i./L SC formulation of ZA 1963 (picoxystrobin), on earthworm populations during a twelve month period following application was investigated in a field study. The study design consisted of four replicates of five treatments. ZA 1963 25SC was applied twice at a 14-day interval to 10 m x 10 m bare earth plots in March 1998 to represent the maximum field use pattern. ZA 1963 25SC was applied at rates of 50 g a.i./ha (simulating 80% interception), 125 g a.i./ha (simulating 50% interception) and 250 g a.i./ha (maximum field rate) in a water volume of 400 L/ha. Tap water was applied twice as a control. Benomyl was applied once at 2 kg a.i./ha as a toxic reference at the same time as the first application of ZA 1963 25SC. Following applications the site was seeded to give a grassland site. Analysis of the soil found residue levels consistent with the correct application rates of ZA 1963 25SC having been applied to the field plots. Earthworms were sampled, using a formaldehyde extraction method, from two sampling areas of 60 cm x 60 cm, within the 10 m x 10 m plot, on four occasions; pre application and approximately one month, six months and twelve months post the second application. ZA 1963 25SC applied twice, at an interval of 14 days, to bare earth field plots at rates of 50, 125 and 250 g a.i./ha had no adverse effects on naturally occurring field populations of earthworms up to twelve months after application.

MRID: 48073819 In a 14 day acute toxicity study, earthworms (Eisenia foetida) were exposed to ZA1963 technical (picoxystrobin) at 0 (control), 1.0, 1.8, 3.2, 5.6 and 10 mg a.i./kg of artificial soil. The reference chemical used was 2-chloracetamide with concentrations of 0 (control), 20, 40 and 80 mg/kg soil. The experiment was carried out in accordance with OECD 207, Earthworm, Acute Toxicity Tests. Mortalities were not observed in the either the control or in the 1.0, 1.8 and 3.2 mg a.i./kg soil test concentrations. An average of 15% and 98% mortality was observed after 14 days in the

140 5.6 and 10 mg a.i./kg soil test concentrations. The 14-day LC50 was 6.7 mg a.i./kg of artificial soil. Weight change of the earthworms was an average of -5.9%, -5.9%, -1.4%, +0.2%, -3.6% and -9.6% in the control, 1.0, 1.8, 3.2, 5.6 and 10 mg a.i./kg soil test concentrations, respectively. The 14-day NOEC, based on mortality and weight loss was 3.2 mg a.i./kg of artificial soil. The 14-day LOEC was 5.6 mg a.i./kg soil. The 14-day LC50 for the reference chemical, 2-chloroacetamide, was 52 mg/kg soil.

MRID: 48073820 The mortality and subsequent recovery of earthworm populations was studied following one application of a 250 g/L SC formulation of the fungicide picoxystrobin after forcing effects with artificial irrigation to ensure maximum exposure. The study was conducted in a spring barley field in southern UK. A single application of the test item was applied, at four treatment rates, with a water control and carbendazim reference item treatment. Sampling was carried out on one occasion before application and on five occasions over a period of one year after application. The study was conducted according to BBA Part VI-2-3 (1994) and ISO 11268-3 (1999) guidelines. The study consisted of a randomized block design of six treatments and four replicates. Treatments were applied on the 6 June 2002 at the following rates: 0 (control), 62.5, 125, 250 and 500 g a.i./ha. The reference item was applied at 4000 g carbendazim/ha. All treatments were applied in a volume of 300 L/ha using a self-propelled boom sprayer. The soil was a silty clay, with a mean pH of 5.9, mean cation exchange capacity of 16.5 meq/100g, mean organic matter content of 5.7% w/w and mean moisture holding capacity of 35.9% w/w. Sampling took place within a central 12 m x 12 m area of each plot (18 m x 18 m), using four 0.25 m2 quadrats in each plot. Earthworms were sampled using a digging and hand-sorting method once before treatment and approximately 7 months after application of treatments. Earthworms were sampled by the formalin method (Raw, 1959) after approximately 1, 4, 10 and 12 months. For a period of ten days immediately after application, surface searches were carried out daily and earthworms collected from the same 1 m2 areas per plot were identified and counted in order to determine the percentage effect of the test and reference items. Samples of soil and earthworms were collected for analytical verification. Earthworm species representative of the major functional groups were present on the site at the time of the pre-treatment sampling, including Lumbricus terrestris, and Aporrectodea caliginosa. Lumbricus spp. Juveniles and epilobus juveniles were the dominant groups in terms of numbers and biomass. Adults of other species, such as Aporrectodea caliginosa, allolobophora chlorotica, L. festivus, L. castaneus and L. rubellus were also present. The reference item, carbendazim, significantly reduced total numbers and biomass of earthworms when compared with controls for the first and second post-treatment sampling occasions, approximately one and four months after treatment. According to the authors, this would confirm the validity of the study. There were no significant differences 7, 10 or 12 months after treatment between total numbers of earthworms in the reference item and the control. Mean epilobous and total juvenile numbers were significantly lower than the control treatment on the fourth sampling occasion, approximately 10 months after application, but there were no significant differences after one year. Results of the post treatment surface searches showed that the required forced effect, in terms of mortality, had occurred within ten days of application of the test item, when mean mortality, as a percentage of the pre-treatment population, was 15% in the 250 g a.i./ha treatment and 28% in the 500 g a.i./ha treatment. At the lower application rates, 62.5 and 125 g a.i./ha picoxystrobin, the number of worms observed dead on the surface, as a percentage of the worms sampled before treatment, was less than 5% after ten days. On the first

141 post-treatment sampling occasion in July 2002, approximately one month after application, significant reductions in abundance were found in both juvenile taxa, total juvenile and total earthworm groups in the 125, 250 and 500 g a.i./ha treatments compared with the control. There were reductions in biomass in the epilobous and total juvenile groups in the 125 and 500 g a.i./ha picoxystrobin treatments compared with the controls. There were significant reductions in abundance and biomass for Lumbricus festivus on the second post-treatment sampling occasion in October 2002, approximately 5 months after application, in the 125, 250 and 500 g a.i./ha picoxystrobin treatments compared with the controls. A similar pattern was observed for the epigeic adult ecological group that contains L. festivus. There were no significant reductions in abundance or biomass for any taxonomic or ecological group on subsequent sampling occasions. There were no significant reductions in abundance or biomass for any taxonomic or ecological group in the lowest test item treatment, 62.5 g a.i./ha picoxystrobin throughout the study. In summary, the results of this study indicate that a single application of 250 and 500 g a.i./ha picoxystrobin (combined with irrigation) caused mortality greater than 15% of the pre-treatment sampled population. Reduction in abundance and biomass were observed in the juvenile population after approximately one moth in the 125, 250 and 500 g a.i./ha picoxystrobin treatments compared with the control but recovery was observed after five months. Reductions in abundance and biomass were observed in one species, Lumbricus festivus after approximately five months compared with control, in the 125, 250 and 500 g a.i./ha picoxystrobin treatment but had recovered by the next sampling occasion, approximately eight months after application. A similar pattern was observed in the epigeic ecological group, of which L festivus is a member. In conclusion, when applied at 62.5 g a.i./ha, picoxystrobin resulted in no observed effects on either abundance or biomass of any earthworm taxonomic or ecological group. At application rates up to and including 500 g a.i./ha, no effects of picoxystrobin on abundance or biomass of any taxonomic or ecological group were apparent by seven months after treatment.

MRID: 48073821 In a 48-hour acute toxicity study, the parasitic wasp Aphidius rhopalosiphi was exposed to ZA1963 (picoxystrobin) as a 250 g/L suspension concentrate YF10267, at 0, 250 and 500 g a.i./ha for assessment of survival, adult fecundity and/or behavior. The reference chemical used was dimethoate, at a rate of 336 g a.i./ha. Treatments were applied using a Potter Tower laboratory sprayer, calibrated to deliver spray at a volume rate equivalent to 200 L/ha. The test chemical was sprayed on barley seedlings enclosed within an untreated glass cylinder. The study chambers consisted of pots of barley seedlings enclosed within an untreated glass cylinder. Four replicates of 5 Aphidius rhopalosiphi were used for treatment and control groups. Mortality was assessed after 0, 1, 2, 4, 24 and 48 hours of exposure. Behavior was also assessed at 30 minutes and 2 hours after exposure. Mortality by 48 hours after introduction was 100% in the 250 and 500 g a.i./ha units, compared to 10% in control units. Therefore no fecundity test could be conducted in this study. Behavior assessments showed that the test substance has a toxic effect within 30 minutes to 2 hours.

MRID: 48073822 An aged residue test was conducted in a field of winter wheat sown in South West England to evaluate the effect of single and repeated applications of ZA1963 (picoxystrobin) as a 250 g/L SC formulation, YF10434, on mortality and fecundity of the parasitoid wasp Aphidius rhopalosiphi. The study was of randomised block design with four replicates of four treatments

142 and sixteen experimental plots. Effects of ZA1963 applied once or twice (with an interval of 13 days) at a rate of 250 g a.i./ha were evaluated. Water was supplied as a control and dimethoate was applied as a toxic reference substance at a rate of 680 g a.i./ha. All spray applications were made using a boom and nozzle sprayer calibrated to deliver 400 L/ha. Twelve tillers (30 cm long sections) of treated wheat plants were removed from each test plot at six intervals after treatment (0, 1, 3, 5, 8 and 12 days after application of all treatments) and taken back to the laboratory. The treated plant material was sprayed with a sugar solution as a food source before being placed into untreated cylinders. Six adult A. rhopalosiphi were introduced to each test unit. Mortality was monitored after 24 and 48 hours. The fecundity of surviving females was assessed by introducing females into untreated chambers containing aphid infested barley seedlings. The number of aphid mummies produced after twelve days was counted to determine the number of mummies produced per female. When applied once or twice at a rate of 250 g a.i./ha, ZA1963 had an initial effect on the mortality of A. rhopalosiphi after exposure to fresh residues when compared to the control (68.8% and 77.1% mortality on Day 0 for one and two applications, respectively compared to control mortality of 10.7%). As residues aged over a period of twelve days, mortality in both ZA1963 treatments declined. After one day, no significant differences in mortality relative to the control were detected in the test with the single application. For the double application, no significant differences in mortality were detected after three days. Surviving female A. rhopalosiphi exposed to fresh residues of the single application of ZA1963 were fecund and produced similar numbers of mummies per female compared to the control females. The single surviving female from the wasps exposed to fresh residues of ZA1963 applied twice did not produce any mummies. Females exposed to residues of ZA1963 aged three days or longer produced mummies. Using corrected mortality and fecundity results, the overall reduction in beneficial capacity (E%) was calculated by the PMRA reviewer for both treatments and 0 and 3-day exposures. At day 0, beneficial capacity was reduced by 54.6 and 100% in the single and double application treatments, respectively. At day 3, the respective values were 22.5 and 24.8%, indicating a potential recovery of a population from migration at the tested application rates.

MRID: 48073823 An aged residue test was conducted in a field of winter sown wheat in South West England to evaluate the effect of fresh an aged residues from single and repeated applications of a 250 g a.i./L SC formulation of ZA1963 (picoxystrobin) on mortality and fecundity of the parasitoid wasp, Chrysoperla carnea. The study was of randomised block design with four replicates of four treatments and sixteen experimental plots. Effects of ZA1963 applied once or twice (with an interval of 13 days) at a rate of 250 g a.i./ha were evaluated. Water was supplied as a control and dimethoate was applied as a toxic reference substance at a rate of 680 g a.i./ha. All spray applications were made using a boom and nozzle sprayer calibrated to deliver 400 L/ha. Individual second instar C. carnea larvae were enclosed in cages covering the top of a single wheat plant in the field. Eight enclosures were established per plot on each of five larval release dates, 0, 1, 3, 5 and 8 days after the second treatment date. When cages were assembled, Ephestia eggs were glued to leaves within each cylinder as food for the lacewing larvae and to encourage foraging on the plant. Fresh Ephestia eggs were also provided three days after each larval release. Larval mortality was assessed seven days after each larval introduction to enclosures. Thereafter, survivors were transferred to individual containers in the laboratory and examined at regular intervals. Survivorship and pupation were recorded. Pupae from each plot

143 and release date were placed together in a fecundity chamber for emergence. Fecundity assessments of individuals from the first three release dates were carried out twice a week over 4 weeks. Each assessment covered an egg laying period of 48 hours. Adult lacewings in each chamber were sexed before and after each egg-laying period. There were no statistically significant differences between any of the ZA1963 treatments and the control on any release date. Female C. carnea exposed to both ZA1963 treatments were fecund and produced similar mean numbers of eggs as those from the control. From corrected mortality and fecundity results, the overall reduction in beneficial capacity (E%) was calculated by the PMRA reviewer for both treatments and 0 and 1-day exposures. At day 0, beneficial capacity was reduced by 36.9 and 35.0% in the single and double application treatments, respectively. At Day 1, the respective values were 33.2 and 34.8%. Based on mortality and fecundity results, C. carnea were not affected by a single and a double application of 250 g a.i./ha of ZA1963.

MRID: 48073824 In a 7-day acute toxicity study, the predatory mite, Typhlodromus pyri, was exposed to ZA1963 (picoxystrobin) as a 250 g/L suspension concentrate YF10267, at 0, 250 and 500 g a.i./ha for assessment of mortality. The reference chemical used was Meothrin (100 g/L fenpropathrin), at a rate of 100 g a.i./ha. Treatments were applied using a Potter Tower sprayer, calibrated to deliver spray at a volume rate equivalent to 200 L/ha. The test chemical was sprayed onto glass plates comprising the test units and to both sides of plastic shelters. The experiment was conducted following the open method as described by Overmeer (1988) and Louis & Ufer (1995), and in compliance with the GLP standard OCDE/GD(92)32. Each test unit consisted of two glass slides each held together with two glass bars, with a narrow gap filled by paper between the two slides to be used as a water source during the test. The number of living and dead mites was recorded at 1, 3 and 7 days after treatment. In the second part of the test, the number of eggs and juveniles present in each test unit were counted to determine the number of eggs produced per surviving female at 7, 10, 12 and 14 days after treatment. Five replicates of four T. pyri were used for treatment and control groups. Seven days after treatment, T. pyri mortality was 64 and 59% in the 250 and 500 g a.i./ha treatments, respectively, compared with a mortality of 19% in the control treatment. Mortality in Meothrin treated test units reach 100% by one day after treatment. Mortality in test units treated at both rates of ZA1963 was significantly higher than mortality in the control units (p < 0.05). In reproduction assessments, significantly fewer eggs laid per female in the ZA1963 test units (at both rates) compared to the control were reported (p < 0.05). However, discrepancies were noted between tables and appendices in the number of females reported in all assessments and treatments. Therefore, no conclusion can be made with regards to fecundity.

MRID: 48258009 In a 96-h acute toxicity study under static conditions, fathead minnow (Pimephales promelas) were exposed to ZA1963 in the presence of sediment at nominal overlying water concentrations of 0 (dilution water control), 0 (solvent control), 30, 40, 50, 60 and 120 µg a.i./L. Initial (0-hour) measured concentrations were <0.54 (

144 the 0-hour measured concentrations were used for the calculation and reporting of all results. No mortalities occurred in the dilution water control, the solvent control or the 0-hour measured 49 μg a.i./L test concentration throughout the study. After 24 hours, 1, 7, 26 and 30 fish were dead in the in 0-hour measured 36, 50, 76 and 140 μg a.i./L test concentrations (3%, 23%, 87% and 100% mortality, respectively). After 48 hours, two additional mortalities were observed: one each in the 0-hour measured 36 and 76 μg a.i./L test concentrations, for a total percent mortality of 7% and 90%, respectively. Based on calculations of the study reviewer, the 96-hour LC50 of ZA1963 in the presence of sediment was 56.8 μg a.i./L, based on initial measured concentrations. The 96-hour NOEC (mortality) of ZA1963 in the presence of sediment was 49 μg a.i./L, based on initial measured concentrations. No sublethal effects were noted in any test concentration throughout the study

MRID: 48258011 In a 28-day prolonged toxicity study under flow through conditions, rainbow trout (Oncorhynchus mykiss) were exposed to ZA1963 at nominal concentrations of 0 (dilution water control), 0 (solvent control), 10, 18, 32, 56 and 100 µg a.i./L. Mean measured concentrations were <1.5 (

MRID: 48258013 The acute toxicity of ZA1963 technical (picoxystrobin) to a range of freshwater aquatic invertebrates was investigated in an exploratory study conducted under static conditions for a period of 24 to 48 hours, depending on the taxa. The study was not conducted in compliance with Good Laboratory Practice Standards. Nineteen different organisms representing most of the major taxa present in freshwater habitats were tested: Platyhelminthes (planarians), Rotatoria (rotifers), Mollusca (freshwater snails), Annelida (oligochaete worms and leeches), Insecta (Ephemeroptera, Odonata, Trichoptera, Diptera and Hemiptera) and Crustacea (Cladodera, Copepoda, Cyclopoda, Isopoda and Amphipoda). Nominal test concentrations varied for each test, but ranged from 1.6 to 4000 μg a.i./L. Controls were dilution water containing methanol at a maximum of 0.025% for all tests except for the rotifer test, were the solvent concentration was 0.1%. Measured concentrations in select test vessels ranged from 90 to 127% of nominal concentrations. From two to ten organisms per replicate were exposed per treatment. With the exception of the rotifer test, a single replicate per test concentration was used. In most cases, the test vessels consisted of plastic cups. The toxicity of ZA1963 to the organisms was assessed after 24 hours and 48 hours (only at 48 hours for Agrypnia). The 24-hour LC50 (for the rotifer,

145 Brachionus) and 48-hour LC50s (for other species tested) ranged from 5 to >4000 μg a.i./L. Raw mortality data were not provided. Despite problems with this study, including the small number of organisms, the lack of replication, the uncertainty associated with exposure levels, the non- GLP status, and the uncertainty in the endpoints reported, the study provides some useful information on the toxicity of ZA1963 to a variety of aquatic invertebrate species. Information from this study could be useful in a risk assessment.

Results Synopsis Test Organism 48-hour LC50 (µg a.i./L) Dugesia sp. – planarian 200-1000 Polycelis sp. – planarian 200-1000 Brachionus calcyciflorus – freshwater rotifer >4000 (24-hour LC50) Limnea stagnalis – freshwater snail >1000 Tubificidae (a mixture of Limnodrilus hofmeisteri and Tubifex sp.) 299 Erpobdella octoculata – leech 200-1000 Cloeon dipterum – mayfly, nymph 194 Coenagrion puella – damselfly, nymph >1000 Agrypnia varia – cased caddisfly larvae 158 Chaoborus crystallinus – phantom midge larva 332 Chironomus riparius – midge, 2nd instar larva 326 Notonecta sp. – water-boatman, adult >1000 Naucoridae – creeping water bug, adult >1000 Daphnia magna – water flea, first instar 18 Daphnia pulex – pond water flea >50 Macrocyclops fuscus – cyclopoid copepods, adults 5 Diaptomus sp. – calanoid copepods, adults 87 Asellus aquaticus – water louse, juvenile 152 Crangonyx pseudogracilis – freshwater shrimp, juvenile 63

146 Appendix C. Effects Bibliography

Ecological Effects MRID Studies Submitted to EPA

Guideline: OPPTS 850.2100 Avian Single Dose Oral Toxicity ------MRID: 48073780 Hubbard, P.M. and J.B. Beavers. 2009. Picoxystrobin (DPX-YT669) technical: an acute oral toxicity study with the zebra finch (Poephila guttata). Wildlife International Ltd., Easton, Maryland. Wildlife International Ltd. Project No. 112-635. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. DuPont Report No.: DuPont-27315. June 30, 2009.

MRID: 48073781 Gallagher, S. P., K.H. Martin, J. Grimes and J.B. Beavers. 1998. ZA 1963: an acute oral toxicity study with the northern bobwhite quail. Wildlife International Ltd., Easton, Maryland. Project No. 123-178. Sponsored by Zeneca Agrochemicals, Jealott’s Hill Research Station, Bracknell Berkshire, UK and E.I. du Pont de Nemours and Company, Wilmington, Delaware. April 20, 1998.

Guideline: OPPTS 850.2300 Avian Dietary Toxicity ------MRID: 48073782 Gallagher, S.P., K.H. Martin, J. Grimes and J.B. Beavers. 1998. ZA 1963: a dietary LC50 study with the northern bobwhite. Wildlife International Ltd., Easton, Maryland. Wildlife International Ltd. Project No.: 123-176. Sponsored by Zeneca Agrochemicals, Bracknell, Berkshire, UK and E.I. du Pont de Nemours and Company, Wilmington, Delaware. January 29, 1998.

MRID: 48073783 Gallagher, S.P., K.H. Martin, J. Grimes and J.B. Beavers. 1998. ZA 1963: a dietary LC50 study with the mallard. Wildlife International Ltd., Easton, Maryland. Wildlife International Ltd. Project No.: 123-177. Sponsored by Zeneca Agrochemicals, Bracknell, Berkshire, UK and E.I. du Pont de Nemours and Company, Wilmington, Delaware. January 29, 1998.

Guideline OPPTS 850.2300 Avian Reproduction ------MRID: 48073784 Temple, D.L., K.H. Martin, J.B. Beavers and M. Jaber. 2010. Picoxystrobin (DPX-YT669) technical: a reproduction study with the northern bobwhite (Colinus virginianus). Wildlife International, Ltd., Easton, Maryland. Wildlife International Ltd. Study No.: 112-634. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. Dupont Report No.: Dupont-27412. February 9, 2010.

MRID: 48073785 Frey, L.T., K.H. Martin, J.B. Beavers and M. Jaber. 1998. ZA 1963: a reproduction study with the mallard duck (Anas platyrhynchos). Wildlife International, Ltd., Easton, Maryland. Wildlife International Ltd. Study No.: 123- 181. Submitted to Zeneca Agrochemicals, Jealott’s Hill Research Station, Bracknell Berkshire, UK. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. November 12, 1998.

Guideline OPPTS 850.1075 Freshwater and Estuarine/marine Fish Acute Toxicity ------

MRID: 48073768

147 Fournier, A.E. 2009. Picoxystrobin (DPX-YT669) Technical: Acute toxicity to sheepshead minnow (Cyprinodon variegatus) under static conditions. Springborn Smithers Laboratories, Wareham, Massachusetts. Springborn Smithers Study number 97.6449. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number: DuPont-27337. December 1, 2009.

MRID: 48073769 Kent, S.J. and N. Shillabeer. 1996. ZA1963: Acute toxicity to rainbow trout (Oncorhynchus mykiss). Brixham Environmental Laboratory, ZENECA Limited, Brixham, Devon, UK. Brixham study number AB0975/B. Sponsored by ZENECA Agrochemicals, Fernhurst, Haslemere, Surrey, UK. and E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number BL5783/B. 13 August 1996.

MRID: 48073770 Kent, S.J. and N. Shillabeer. 1997. ZA1963: Acute toxicity to bluegill sunfish (Lepomis macrochirus). Brixham Environmental Laboratory, ZENECA Limited, Brixham, Devon, UK. Brixham study number AB0975/F. Sponsored by ZENECA Agrochemicals, Fernhurst, Haslemere, Surrey, UK. and E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number BL5785/B. 17 March 1997.

MRID: 48073771 Kent, S.J. and N. Shillabeer. 1997. ZA1963: Acute toxicity to rainbow trout (Oncorhynchus mykiss) of a 250 g l-1 formulation. Brixham Environmental Laboratory, ZENECA Limited, Brixham, Devon, UK. Brixham study number AC1115/B. Sponsored by ZENECA Agrochemicals, Fernhurst, Haslemere, Surrey, UK. and E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number BL5966/B. 29 August 1997.

MRID: 48258008 Kent, S.J. and N. Shillabeer. 1997. ZA1963: Acute toxicity to fathead minnow (Pimephales promelas). Brixham Environmental Laboratory, ZENECA Limited, Brixham, Devon, UK. Brixham study number AB0975/G. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number BL5786/B. 12 March 1997.

MRID: 48258010 Kent, S.J., Shillabeer, N. and K.W.J. Long. 1997. ZA1963: Acute toxicity mirror carp (Cyprinus carpio). Brixham Environmental Laboratory, ZENECA Limited, Brixham, Devon, UK. Brixham study number AB0975/E. Sponsored by ZENECA Agrochemicals, Fernhurst, Haslemere, Surrey, UK. and E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number BL5784/B. 19 March 1997.

MRID: 48258012 Kent, S.J. and N. Shillabeer. 1997. ZA1963: Acute toxicity to three-spined stickleback (Gasterosteus aculeatus) . Brixham Environmental Laboratory, ZENECA Limited, Brixham, Devon, UK. Brixham study number AB0975/H. Sponsored by ZENECA Agrochemicals, Fernhurst, Haslemere, Surrey, UK. and E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number BL5787/B. 5 March 1997.

MRID: 48258014 Magor, S.E. and N. Shillabeer. 1998. R408631: Acute toxicity to fathead minnow (Pimephales promelas). Brixham Environmental Laboratory, ZENECA Limited, Brixham, Devon, UK. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number BL6338/B. 10 June 1998.

MRID: 48258016 Magor, S.E. and N. Shillabeer. 1998. R403814: Acute toxicity to fathead minnow (Pimephales promelas). Brixham Environmental Laboratory, ZENECA Limited, Brixham, Devon, UK. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number BL6344/B. 12 June 1998.

MRID: 48258018 Magor, S.E. and N. Shillabeer. 1998. R403092: Acute toxicity to fathead minnow (Pimephales promelas). Brixham Environmental Laboratory, ZENECA Limited, Brixham, Devon, UK. Sponsored by E.I. du Pont de Nemours and

148 Company, Wilmington, Delaware. Report Number BL6341/B. 16 June 1998.

MRID: 48258020 Magor, S.E. and N. Shillabeer. 1998. R408509: Acute toxicity to fathead minnow (Pimephales promelas). Brixham Environmental Laboratory, ZENECA Limited, Brixham, Devon, UK. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number BL6347/B. 24 June 1998.

MRID: 48258022 Magor, S.E. and N. Shillabeer. 1999. R413834: Acute toxicity to rainbow trout (Oncorhynchus mykiss). Brixham Environmental Laboratory, ZENECA Limited, Brixham, Devon, UK. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number BL6541/B. 25 March 1999.

Guideline OPPTS 850.1010 Freshwater Invertebrate Acute Toxicity ------MRID: 48073764 Kent, S.J. and N. Shallabeer. 1997. ZA1963: Acute toxicity to Daphnia magna. Brixham Environmental Laboratory, ZENECA Limited, Brixham, Devon, UK. Brixham study number AB0975/K. Sponsored by ZENECA Agrochemicals, Fernhurst, Haslemere, Surrey, UK. and E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number BL5820/B. 23 January 1997.

MRID: 48073765 Kent, S.J. and N. Shallabeer. 1997. ZA1963: Acute toxicity to Daphnia magna of a 250 g l-1 SC formulation. Brixham Environmental Laboratory, ZENECA Limited, Brixham, Devon, UK. Brixham study number AC1115/C. Sponsored by ZENECA Agrochemicals, Fernhurst, Haslemere, Surrey, UK. and E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number BL5967/B. 29 August 1997.

MRID: 48258015 Magor, S.E. and N. Shillabeer. 1998. R408631: Acute toxicity to Daphnia magna. Brixham Environmental Laboratory, ZENECA Limited, Brixham, Devon, UK. Brixham study number AF0011/C. Sponsored by ZENECA Agrochemicals, Fernhurst, Haslemere, Surrey, UK and E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number BL6339/B. 10 June 1998.

MRID: 48258017 Magor, S.E. and N. Shillabeer. 1998. R403814: Acute toxicity to Daphnia magna. Brixham Environmental Laboratory, ZENECA Limited, Brixham, Devon, UK. Brixham study number AF0013/C. Sponsored by ZENECA Agrochemicals, Fernhurst, Haslemere, Surrey, UK and E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number BL6345/B. 12 June 1998.

MRID: 48258019 Magor, S.E. and N. Shillabeer. 1998. R403092: Acute toxicity to Daphnia magna. Brixham Environmental Laboratory, ZENECA Limited, Brixham, Devon, UK. Brixham study number AF0012/C. Sponsored by ZENECA Agrochemicals, Fernhurst, Haslemere, Surrey, UK and E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number BL6342/B. 16 June 1998.

MRID: 48258021 Magor, S.E. and N. Shillabeer. 1998. R408509: Acute toxicity to Daphnia magna. Brixham Environmental Laboratory, ZENECA Limited, Brixham, Devon, UK. Brixham study number AF0014/C. Sponsored by ZENECA Agrochemicals, Fernhurst, Haslemere, Surrey, UK and E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number BL6348/B. 24 June 1998.

MRID: 48258023 Magor, S.E. and N. Shillabeer. 1999. R413834: Acute toxicity to Daphnia magna. Brixham Environmental Laboratory, ZENECA Limited, Brixham, Devon, UK. Brixham study number AF0677/C. Sponsored by ZENECA

149 Agrochemicals, Fernhurst, Haslemere, Surrey, UK. and E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number BL6542/B. 26 March 1999.

Guideline OPPTS 850.1025 Estuarine/Marine Mollusk Acute Toxicity (Shell Deposition) ------MRID: 48073766 Duncan O. and B.S. York. 2009. DPX-YT669 (Picoxystrobin) Technical: Acute Toxicity to Eastern Oyster (Crassostrea virginica) Under Flow-Through Conditions. Unpublished study performed by Springborn Smithers Laboratories, Wareham, Massachusetts. Laboratory Study No. 97.6451. Study sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. DuPont-27341. Study completed July 29, 2009.

Guideline OPPTS 850.1035 Estuarine/Marine Invertebrate Acute Toxicity ------MRID: 48073767 A. E. Fournier. 2009. Picoxystrobin (DPX-YT669) Technical: Acute Toxicity to Mysid (Americamysis bahia) Under Static-Renewal Conditions. Unpublished study performed by Springborn Smithers Laboratories, Wareham, Massachusetts. Laboratory Study No. 97.6450. Study sponsored by E.I. du Pont de Nemours and Company Wilmington, Delaware. DuPont-27340. August 5, 2009.

Guideline OPPTS 850.1300 Freshwater Aquatic Invertebrate Life Cycle ------MRID: 48073772 Kent, S.J. and N. Shallabeer. 1996. ZA1963: Chronic toxicity to Daphnia magna. Brixham Environmental Laboratory, ZENECA Limited, Brixham, Devon, UK. Brixham study number AB0975/C. Sponsored by ZENECA Agrochemicals, Fernhurst, Haslemere, Surrey, UK. Report Number BL5792/B. 17 October 1996.

Guideline OPPTS 850.1350 Estuarine/Marine Invertebrate Life Cycle ------MRID: 48073773 Lee, M.R. 2010. Picoxystrobin (DPX-YT669 Technical – Life-cycle toxicity test with mysids (Americamysis bahia) following draft OPPTS Guideline 850.1350. Springborn Smither Laboratories, Wareham, Massachusetts, USA. Springborn Smithers Study No. 97.6453. E.I. DuPont de Nemours and Co. Delaware, U.S.A. Unpublished. January 29, 2010.

Guideline OPPTS 850.1400 Freshwater and Estuarine/marine Fish Early-Life Stage ------MRID: 48073774 Lee, M. R. 2009. Picoxystrobin (DPX-YT669) Technical - Early Life-Stage Toxicity Test with Sheepshead Minnow (Cyprinodon variegatus). Unpublished study performed by Springborn Smithers Laboratories, Wareham, Massachusetts. Laboratory Project ID: DuPont-27339. Study sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. Study completion date: November 5, 2009.

MRID: 48073775 Kent, S.J. and Shillabeer, N. 1997. ZA 1963: Chronic toxicity to fathead minnow (Pimephales promelas) embryos and larvae. Brixham Environmental Laboratory, Zeneca Limited, Brixham, Devon, UK. AB0975/1. Sponsored by Zeneca Agrochemicals, Fernhurst Haslemere, Surrey, UK, and also E.I. du Pont de Nemours and Company, Wilmington, Delaware. BL5789/B. 21 March 1997. Unpublished report.

Guideline OPPTS 850.3020 Honeybee Acute Contact Toxicity ------

150 MRID: 48073786 Gough, H. J. and D. Jackson. 1997. ZA1963 Acute contact and oral toxicity to honey bees (Apis mellifera) of technical material. Zeneca Agrochemicals, Jealott’s Hill Research Station, Bracknell, Berkshire, UK. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number RJ2422B. 27 November 1997.

MRID: 48073787 Gough, H. J. and D. Jackson. 1997. ZA1963 Acute contact and oral toxicity to honey bees (Apis mellifera) of a 250 g/L formulation. Zeneca Agrochemicals, Jealott’s Hill Research Station, Bracknell, Berkshire, UK. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number RJ2423B. 2 December 1997.

Guideline OPPTS 850.6200 Earthworm Subchronic Toxicity ------MRID: 48073811 Friedrich S. 2003. Picoxystrobin (ZA1963): Sublethal toxicity of a 250 g/L SC formulation (A12796B) to the earthworm Eisenia fetida. Biochem Agrar, Gerichschain, Germany. Report number No. 03 10 48 027. Sponsored by Syngenta Crop Protection AG; Ecological Sciences, 4002 Basel, Switzerland. 28 pp. June 19, 2003.

Guideline OPPTS 850.4100 Seedling Emergence ------MRID: 48073801 Porch, J.R. and T.Z. Kendall. 2009. Picoxystrobin (DPX-YT669): a greenhouse study to investigate the effects on seedling emergence and growth of ten terrestrial plants following soil exposure. Wildlife International, Ltd., Easton, Maryland. Wildlife International Study Number 112-648. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. DuPont Study Number: DuPont-27333. October 14, 2009.

Guideline OPPTS 850.4150 Vegetative Vigor ------MRID: 47090329 Porch, J.R. and T.Z. Kendall. 2009. Picoxystrobin (DPX-YT669): a greenhouse study to investigate the effects on vegetative vigor of ten terrestrial plants following foliar exposure. Wildlife International, Ltd., Easton, Maryland. Wildlife International Study Number 112-649. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. DuPont Study Number: DuPont-27334. August 11, 2009.

Guideline OPPTS 850.4400 Aquatic Vascular Plant Toxicity ------MRID: 48073803 Softcheck, K.A. 2010. Picoxystrobin (DPX-YT669) technical – Effects on growth and reproduction to the aquatic plant Lemna gibba. Springborn Smithers Laboratories, Wareham, Massachusetts. Springborn Smithers Study No. 97.6445. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. DuPont Number 27335, Revision No. 2. Study completed on January 22, 2010 (original report), January 27, 2010 (revision no. 1), February 17, 2010 (revision no. 2).

Guideline OPPTS 850.5400 Algal Plant Toxicity ------MRID: 48073804 Softcheck, K.A. 2010. Picoxystrobin (DPX-YT669) Technical – Effect on growth and growth rate to the marine diatom, Skeletonema costatum. Springborn Smithers Laboratories, Wareham, Massachusetts. Springborn Smithers Study No. 97.6448. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. DuPont Number 27384. December 3, 2009.

MRID: 48073805

151 Dengler, D. 2010. Picoxystrobin (DPX-YT669) Technical: Influence on growth and growth rate of the blue-green alga Anabaena flos-aquae (Cyanophyta). eurofins-GAB GmbH, D-75223 Niefern-Öschelbronn, Germany. Study No. S09-00577-L1. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. DuPont Number 27382, Revision No.1. 23 October 2009 (original report). 13 January 2010 (Revision No. 1).

MRID: 48073806 Softcheck, K.A. 2010. Picoxystrobin (DPX-YT669) Technical – Effect on growth and growth rate to the freshwater diatom, Navicula pelliculosa. Springborn Smithers Laboratories, Wareham, Massachusetts. Springborn Smithers Study No. 97.6447. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. DuPont Number 27383. 18 March 2010.

MRID: 48258024 Smyth, D.V., S.J. Kent and N. Shillabeer. 1999. ZA1963: Toxicity to the green alga Selenastrum capricornutum. Brixham Environmental Laboratory, Brixham, Devon, UK. Sponsored by E.I. du Pont de Nemours and Company. Wilmington, Delaware. BK\L5753/B. 23 September 1999.

MRID: 48258025 Smyth, D.V., S.J. Kent and N. Shillabeer. 1997. ZA1963: Toxicity to the green alga Selenastrum capricornutum of a 250 g/L SC formulation. Brixham Environmental Laboratory, Brixham, Devon, UK. Sponsored by E.I. du Pont de Nemours and Company. Wilmington, Delaware. BL5968/B. August 29, 1997.

MRID: 48258026 Smyth, D.V., S.E. Magor and N. Shillabeer. 1998. R403814: Toxicity to the green alga Selenastrum capricornutum. Brixham Environmental Laboratory, Brixham, Devon, UK. Sponsored by E.I. du Pont de Nemours and Company. Wilmington, Delaware. BL6308/B. June 18, 1998.

MRID: 48258027 Smyth, D.V., S.E. Magor and N. Shillabeer. 1998. R408631: Toxicity to the green alga Selenastrum capricornutum. Brixham Environmental Laboratory, Brixham, Devon, UK. Sponsored by E.I. du Pont de Nemours and Company. Wilmington, Delaware. BL6302/B. June 10, 1998.

MRID: 48258028 Smyth, D.V., S.E. Magor and N. Shillabeer. 1998. R403092: Toxicity to the green alga Selenastrum capricornutum. Brixham Environmental Laboratory, Brixham, Devon, UK. Sponsored by E.I. du Pont de Nemours and Company. Wilmington, Delaware. BL6303/B. 16 June 1998.

MRID: 48258029 Smyth, D.V., S.E. Magor and N. Shillabeer. 1998. R408509: Toxicity to the green alga Selenastrum capricornutum. Brixham Environmental Laboratory, Brixham, Devon, UK. Sponsored by E.I. du Pont de Nemours and Company. Wilmington, Delaware. BL6309/B.

MRID: 48258030 Smyth, D.V., S.E. Magor and N. Shillabeer. 1999. R413834: Toxicity to the green alga Selenastrum capricornutum. Brixham Environmental Laboratory, Brixham, Devon, UK. Sponsored by E.I. du Pont de Nemours and Company. Wilmington, Delaware. BL6503/B. 25 March 1999.

Non-guideline Studies ------MRID: 48073777 Gentle, W.E. 1997. Sediment toxicity test with Chironomus riparius. Jealott’s Hill Research Station, Bracknell, Berkshire, UK. ZENECA Agrochemicals. E.I. du Pont de Nemours and Company, Wilmington, Delaware, USA. Study Number 96JH241, Report Number RJ2334B. January 1997-Oct 1997. Unpublished.

152

MRID: 48073778 Gentle, W.E. and J.H. Rapley. 1997. BBA Toxicity Test with Sediment-dwelling Chironomus riparius. Jealott’s Hill Research Station, Bracknell, Berkshire, UK. ZENECA Agrochemicals. E.I. du Pont de Nemours and Company, Wilmington, Delaware, USA. Report Series RJ2335B, Study Number 96JH242. January 1997-Oct 1997. Unpublished.

MRID: 48073779 Cole, J.F.H., H.A. Yearsdon, A.R Brown, C.J. Everett and S.J. Maund. 1999. ZA1963: An Outdoor Pond Microcosm Study. Zeneca Agrochemicals, Jealott’s Hill Research Station, Bracknell, Berkshire, UK. Study Number 97JH004. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number RJ2514B. 11 January 1999. 213pp.

MRID: 48073807 Blake, R.J. Coulson, J.M., Shaw, A.C, Dicketts, D. and K.M. Wyeth. Determination of the effect of moisture and soil ageing on the toxicity of a 250 g/L SC Formulation (A12796B) to the earthworm Eisenia fetida in 18 Acres soil. Report Number TMJ4955B. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware 19898, USA. 102 p.

MRID: 48073808 Coulson, J.M., Shaw, A.C., Dark, R., Chapman, P.F., Harvey, B.R. and Sweeney, P.J.J. 2003. Picoxystrobin: Field monitoring programme to investigate the effects on earthworm populations. Syngenta Jealott’s Hill International Research Centre, Bracknell, Berkshire, UK. Unpublished. Report Series TMJ4797B. Study No. 2023541. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware, 19898, USA. 20 January 2003. 443 p.

MRID: 48073809 Coulson, J.M., Shaw, A.C., Dark, R., Harvey, B.R. and Sweeney, P.J.J. 2003. Picoxystrobin: Field Trials to Investigate the Effects on Earthworm Populations in France. Syngenta Jealott’s Hill International Research Centre, Bracknell, Berkshire, UK. Unpublished. Report Series TMJ4859B. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware, 19898, USA. 28 November 2003. 44 p.

MRID: 48073810 Klein, O. 2004. Picoxystrobin: A Field Study to evaluate the effects of picoxystrobin on the earthworm fauna in cereals in middle Sweden. GAB Biotechnologie GmbH & GAB Analytik GmbH, Eutinger Str. 24 D-75223 Niefern- Oeschelbronn, Germany. Final Report 20031170/SW1-NFEw. Applicant/Sponsored by E.I du Pont de Nemours and Company, Wilmington, Delaware 19898, U.S.A. 351 p.

MRID: 48073812 Friedrich, S. 2002. Picoxystrobin (ZA1963): Acute toxicity of a 250 g/L SC formulation (A12796B) to the earthworm Eisenia fetida. BioChem agrar, Labor für biologische und chemische Analytik GmbH, Kupferstraße 6, D-04827 Gerichshain, Germany. Report Number 02 10 48 045. Sponsored by Syngenta Crop Protection AG, Ecological Sciences, CH-4002 Basel, Switzerland. 11 December 2002.

MRID: 48073813 Krück, S. 2003. Picoxystrobin: a field study to investigate the forced effect and recovery of earthworm populations following application of a 250 g/L SC formulation (A12796B) in a spring cereal field in North East Germany. Biochem agrar. Labor für biologishe und chemishe Analytic GmbH, Germany. Unpublished Report No.02 10 48 046, Sponsor project Number 2023605. Sponsored by Syngenta Crop Protection AG; Ecological Sciences, 4002 Basel, Switzerland. 5 December 2003. 319 pp.

MRID: 48073814 Kruck, S. 2003. Picoxystrobin: a field study to investigate the forced effect and recovery of earthworm populations following application of a 250 g/L SC formulation (A12796B) in a spring cereal field in North Germany. Biochem

153 agrar. Labor für biologishe und chemishe analytic GmbH, Germany. Report Number 02 10 48 047, Sponsor project Number 2023606. Sponsored by Syngenta Crop Protection AG; Ecological Sciences, 4002 Basel, Switzerland. 5 December, 2003. 326 p.

MRID: 48073815 Lees, C.J. and H.J. Gough. 1998. ZA1963: Toxicity of the metabolite R408509 (Compound 8) to the earthworm Eisenia fetida in an artificial soil test. ZENECA Agrochemicals, Jealott’s Hill Research Station, Bracknell, Berkshire, UK. Report Number RJ2712B. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. 21 December 1998.

MRID: 48073816 Lees, C.J. and H.J. Gough. 1998. ZA1963: Toxicity of the metabolite R403814 (Compound 3) to the earthworm Eisenia fetida in an artificial soil test. ZENECA Agrochemicals, Jealott’s Hill Research Station, Bracknell, Berkshire, UK. Report Number RJ2711B. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. 21 December 1998.

MRID: 48073817 Lees, C.J. and H.J. Gough. 1999. ZA1963: Toxicity of the metabolite R403082 (Compound 2) to the earthworm Eisenia fetida in an artificial soil test. ZENECA Agrochemicals, Jealott’s Hill Research Station, Bracknell, Berkshire, UK. Report Number RJ2710B. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. 6 January 1999.

MRID: 48073818 Travis, A. and Coulson, J.M. 1999. ZA1963: investigation of the effects on field earthworm populations of a 250 g a.i./L SC formulation. Syngenta Jealott’s Hill International Research Centre, Bracknell, Berkshire, UK. Unpublished Report Number RJ2696B. Study No. 97JH303. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware, 19898, USA. 22 October 1999. 141 p.

MRID: 48073819 Jackson, D. and J.M. Coulson. 1997. ZA1963: Toxicity of technical material to the earthworm Eisenia fetida in an artificial soil test. ZENECA Agrochemicals, Jealott’s Hill Research Station, Bracknell, Berkshire, UK. Report Number RJ2411B. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. 6 November 1997.

MRID: 48073820 Forster, A. and Pease, G. 2003. Picoxystrobin: a field study to investigate the forced effect and recovery of earthworm populations following application of a 250 g/L SC formulation (A12796B) in a spring cereal field in South UK. Revision No. 1. Syngenta Jealott’s Hill International Research Centre, Bracknell, Berkshire, UK. Unpublished Rep. No. ER-03-KCB173. Study No. KCB 173. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware, 19898, USA. 198 p. Original report: 18 November 1993; Revision No. 1: 7 September 2005.

MRID: 48073821 H. Austin, 1997. A Laboratory Study to Evaluate the Effects of ZA1963 on the Parasitic Wasp Aphidius rhopalosiphi. Ecotox Limited, Tavistock, Devon PL19 0YU, England. Experiment No. HMA 179, Report No. ER- 97-32, Sponsor Zeneca Agrochemicals. Study completed on August 29th 1997.

MRID: 48073822 H.M. Austin, 1999. Semi-Field Study to Evaluate the Effects of Fresh and Aged Residues of ZA1963 on Aphidius rhopalosiphi in a cereal field in England. Ecotox Limited, Tavistock, Devon PL19 0YU, England. Experiment No. KCB 106, Report No. ER-98-57, Sponsor Zeneca Agrochemicals. Study completed on March 10th 1999.

MRID: 48073823 K.C. Brown, 1999. A Semi-Field Study to Evaluate the Effects of Fresh and Aged Residues of ZA1963 on Chrysoperla carnea in a cereal field in England. Ecotox Limited, Tavistock, Devon PL19 0YU, England.

154 Experiment No. KCB 105, Report No. ER-98-34, Sponsor Zeneca Agrochemicals. Study completed on March 5th 1999.

MRID: 48073824 Gill, A. and H. Austin, 1997. A Laboratory Study to Evaluate the Effects of ZA1963 on the Predatory Mite Typhlodromus pyri. Ecotox Limited, Tavistock, Devon PL19 0YU, England, Experiment No. HMA 177, Report No. ER-97-28, Sponsor Zeneca Agrochemicals. Study completed September 1st 1997.

MRID: 48258009 Kent, S.J. and N. Shillabeer. 1998. ZA1963: Acute toxicity to fathead minnow (Pimephales promelas) in the presence of sediment. Brixham Environmental Laboratory, ZENECA Limited, Brixham, Devon, UK. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number BL6277/B. 17 March, 1998.

MRID: 48258011 Kent, S.J. and N. Shillabeer. 1997. ZA1963: The 28 day LC50 to rainbow trout (Oncorhynchus mykiss). Brixham Environmental Laboratory, ZENECA Limited, Brixham, Devon, UK. Brixham. Brixham study number AB0975/J. Sponsored by E. I. du Pont de Nemours and Company, Wilmington, Delaware. Report Number BL5790/B. March 21, 1997.

MRID: 48258013 Farrelly, E. and L. Prevo. 1996. ZA1963: Acute toxicity of the technical material to aquatic invertebrates. ZENECA Agrochemicals, Jealott’s Hill Research Station, Bracknell, Berkshire. Study Number 95JH197. Sponsored by E.I. du Pont de Nemours and Company, Wilmington, Delaware. Report Series TMJ3529B. 23 August 1996.

155 Appendix D

Submitted environmental fate studies for picoxystrobin and its degradates

Guideline MRID Study Title Status 835.2120 48073834 Hydrolysis Study Acceptable (161-1) 835.2240 48073835 Photodegradation in Water Acceptable (161-2) 835.2410 48073836 Photodegradation on Soil Supplemental (161-3) 835.4100 48073837 Aerobic Soil Metabolism Supplemental (162-1) 835.4200 48073838 Anaerobic Soil Metabolism Waived (162-2) 845.4300 48073839 Aerobic Aquatic Metabolism Supplemental (1 62-4) 835.4400 48073840 Anaerobic Aquatic Metabolism Supplemental (1 62-3) 835.1230 48073832 Mobility/ Supplemental (163-1) Adsorption/Desorption 835.1410 48073833 Laboratory Volatility Supplemental (163-2) 835.6100 48073841 Terrestrial Field Dissipation Supplemental (164-1) 48073842 (North America) Supplemental 48073843 Supplemental 48073844 Supplemental

48073846 Terrestrial Field Dissipation 48073847 (Europe) Supplemental 48073848 Supplemental 48073 849 Supplemental 48073850 Supplemental 48073851 Supplemental Supplemental 835.6200 48073838 (as an Aquatic Field Dissipation Waived (1 64-2) attachment to the anaerobic soil waiver request) 835.1730 48073776 Fish Accumulation Acceptable (165-4) 850.7100 48073725 Validation of analytical method Acceptable 850.7100 48073726 Validation of analytical method Acceptable 850.7100 48073727 Validation of analytical method Acceptable 850.7100 48073728 Validation of analytical method Acceptable 850.7100 48073729 Validation of analytical method Acceptable 850.7 100 48073730 Validation of analytical method 850.7100 48073731 Validation of analytical method Acceptable Acceptable N/A 48073845 Non-guideline N/A Comparison of precipitation, temperature, and soils at European field testing sites to those at proposed use sited in the US and Canada

156 Appendix E

Summary of environmental fate studies

MRID 48073834 (Hydrolysis): The hydrolysis of [pyridinyl-14C]-labeled methyl(E)-2-{2-[6- (trifluoromethyl)pyridin-2-yloxymethyl]phenyl}-3-methoxyacrylate (picoxystrobin, ZA1963; radiochemical purity 98.2%), at 1.07 mg a.i./L, was studied in sterile aqueous buffered pH 4 (0.01M acetate) and pH 7 (0.01M acetate) solutions at 50.0 ± 1.0°C for 6 days posttreatment; in pH 9 (0.01M borate) solutions at 50.0 ± 1.0°C for 32 days; and at pH 5 (0.01M acetate), pH 7, and pH 9 solutions at 25.0 ± 1.0°C for 32 days. Aliquots of all samples were directly analyzed for total radioactivity using LSC. Aliquots of a single sample from each sampling interval were analyzed using one-dimensional, normal phase TLC with four solvent systems and one-dimensional, reverse phase TLC with two solvent systems. In 50 °C solutions, two major transformation products were isolated: ZA1963/02]; and ZA1963/07. ZA1963/02 and ZA1963/07 were maximums of 32.1% and 37.9% of the applied, respectively, at 32 days posttreatment. No minor transformation products were identified. In 25 °C no major transformation products were isolated, and no minor transformation products were identified. Results indicate that there is no evidence of degradation via hydrolysis which was studied across environmental pHs

MRID 48073835 (Photodegradation in Water): The aqueous phototransformation of [pyridinyl-14C]- and [phenylacrylate-14C]-labeled methyl (2E)-3-methoxy-2-{2-[6-(trifluoromethyl)-2-pyridyloxymethyl]phenyl}acrylate (picoxystrobin, ZA1963; radiochemical purities >99%), at 1.36-1.43 mg a.i./L, was studied at 25 ± 1°C in sterile aqueous buffered pH 7 solutions (0.01M acetate) that were continuously irradiated using a Xenon arc lamp (300-400 nm) for 425-431 hours. The intensity of the artificial light (32.95-33.96 W/m2) was such that ca. 15.5 hours of artificial light was equivalent to 1 summer day at 50°N. The test system consisted of sealed glass irradiation vessels containing treated test solution (8 mL) that were placed in a temperature controlled stainless steel tank directly under the Xenon arc lamp. The dark controls were covered with aluminum foil and placed in a temperature-controlled waterbath. Single samples of each test solution (duplicates at time 0) were collected at time 0 and ca. 89, 168, 258, 343, and 428 hours posttreatment for the irradiated samples and at ca. 428 hours for the dark controls. Acetonitrile rinses of the sample vessels were added to the samples prior to analysis, but samples were otherwise not modified. Aliquots of the samples were analyzed for total radioactivity using LSC, then were stored frozen prior to one- and two-dimensional analysis using TLC. Based on first order linear regression analysis, picoxystrobin (combined labels) dissipated from the irradiated samples with a reviewer-calculated half-life of 385 hours (16 24-hour days) in the pH 7 buffer, based on the continuous irradiation used in the study. Picoxystrobin was stable in the dark controls. Three transformation products were identified in the irradiated solutions: Compound 4, Compound 12; and Compound 3. Compounds 4 and 12 were major phototransformation products in both label treatments. Compound 3 was a minor transformation product, detected only in the irradiated solution treated with the pyridinyl label.

MRID 48073836 (Photodegradation in Soil): The phototransformation of [pyridinyl-5-14C]- and [phenylacrylate-2-14C]-labeled methyl(E)-2-{2-[6-(trifluoromethyl)pyridin-2-yloxymethyl]phenyl}-3-methoxyacrylate (picoxystrobin, ZA1963; radiochemical purities ≥98.3%), at a rate equivalent to 788-789 g a.i./ha, was studied at 20 ± 1°C on sandy clay loam soil (pH 6.9, organic matter 4.9%) from the UK. The soil was continuously irradiated using a filtered xenon arc lamp for up to ca. 500 hours (ca. 20 days). Based on the intensity of the sunlamp (ca. 30.6 W/m2), ca. 17 hours of artificial light was equivalent to 1 solar summer day at 50°N. The irradiated test systems consisted of photolysis vessels (4.1-cm diameter, 2- cm height; 13.2 cm2 surface area) containing treated soil (ca. 1 g, <1 mm depth) that were covered with quartz glass lids. The vessels were placed under the xenon arc lamp in a stainless steel tank with cooled water circulating through its base. Dark control vessels (not described) were stoppered with Teflon plugs, wrapped in aluminum foil, and placed in a temperature- controlled room. Volatiles were not trapped. For the phenylacrylate treatment, single samples were collected after 0, 17.01, 90.66, 166.00, 329.29, and 497.64 hours of irradiation. Soil samples were sequentially extracted twice with acetonitrile (2 x 7 mL), twice with acetonitrile:water (80:20, v:v; 2 x 7 mL), and twice with acetonitrile:0.1M HCl (75:25, v:v; 2 x 7 mL) at ambient temperatures by shaking then ultrasonicating. The soil extracts were analyzed using LSC and one-dimensional reverse- and normal-phase TLC. [14C]Compounds were identified by comparison to unlabeled reference standards of picoxystrobin and 16 probable transformation products that were cochromatographed with the samples. Identifications and quantifications were confirmed using HPLC and LC/MS. For the irradiated samples, overall [14C]residue recoveries were 96.4 ± 4.8% (86.8-99.2%) of the applied in the soil treated with the phenylacrylate label and 96.9 ± 3.6% (93.3-102.2%) in the soil treated with the pyridinyl label. overall [14C]residue recoveries were 100.6% and 101.6% of the applied in the soil treated with the phenylacrylate and pyridinyl labels, respectively. Based on first-order linear regression analysis, picoxystrobin (combined labels) degraded with a half-life of 277 hours in the irradiated samples. Picoxystrobin was stable in the dark controls. Major degradates include: Compound 3; Compound 4; compound 8; Compound 12; Compound 13; both labels); and Compound 15. study is classified as supplemental and upgradable upon the submission of the following information: if the soils were air-dry throughout the experiment, the application rate calculated in terms of mg/kg soil, and the limits of Detection and Quantitation.

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MRID 48073837 (Aerobic Soil Metabolism): The biotransformation of [pyridinyl-5-14C]- and [phenylacrylate- 2-14C]-labeled methyl(E)-2-{2-[6-(trifluoromethyl)pyridin-2-yloxymethyl]phenyl}-3-methoxyacrylate (picoxystrobin, ZA1963; radiochemical purities ≥97.5%) was studied in four soils from the UK using : a sandy loam (Hyde Farm; pH 6.3-7.6, organic matter 3.5-2.8%); a sandy clay loam (18 Acres; pH 6.1-7.3, organic matter 4.3-5.0%); a sand (Chamberlain’s Farm; pH 7.4-8.1, organic matter 2.3%); and a sandy loam (Frensham; pH 6.7, organic matter 2.4%).

The experiments were conducted under aerobic conditions for 119 or 364 (Hyde Farm only) days in the dark at 20°C and a soil moisture of ca. pF2. Picoxystrobin was applied to the soil at measured concentrations of 0.48-0.59 mg a.i./kg. The test system consisted of glass pots (ca. 4.6 cm i.d. x 6.0 cm high) containing moist treated soil (36-40 g dry wt). The pots were placed on metal trays inside glass cylinders, and the glass cylinders were attached to a flow-through volatile trapping system. Moistened air was continuously drawn through the cylinders (20-30 mL/minute), then through two carbon sieves and tubes of ethanolamine. Two pots of each soil/label treatment were collected for immediate analysis at time 0, then single pots were collected at 9, 21, 29, 50, 70, 91, and 119 days (also 219 & 364 days for Hyde Farm soil only); an additional sample/treatment was collected at each interval and stored frozen. Samples were extracted by mechanical shaking at ambient temperatures once with acetone (all samples), once with acetone:water (80:20, v:v; 0-29 days); once with acetone:0.1M HCl (75:25, v:v; 29 days to termination), and once with acetone:1M HCl (75:25, v:v; 50 days to termination). Aliquots of the individual extracts were analyzed by LSC and one-dimensional reverse- and normal-phase TLC.

Based on nonlinear regression analyses, picoxystrobin (combined labels) dissipated with reviewer-calculated half-lives of 31.4 days in the Hyde Farm sandy loam soil, 23.6 days in the 18 Acres sandy clay loam soil, 36.1 days in the Chamberlain’s Farm sand soil and 28.4 days in the Frensham sandy loam soil. Four transformation products were identified in the soil extracts: Compound 2; Compound 3; Compound 7; and compound 8 with minor products as Compound 26 and CO2. This study is still classified as supplemental even with the submission of additional data (Report No. TMJ4245, TMJ4038B, and TMJ2750B) which solved the inadequacy of the trapping system. This study could be upgraded to acceptable upon the submission of data that shows soils used in this study (from the UK) were typical of the pesticide use area in the US.

MRID 48073839 (Aerobic Aquatic Metabolism): The biotransformation of [pyridinyl-5-14C]- and [phenylacrylate-2-14C]-labeled methyl (2E)-3-methoxy-2-{2-[6-(trifluoromethyl)-2-pyridyloxymethyl]phenyl}acrylate (picoxystrobin, ZA1963; radiochemical purity ≥98.9%) in two water-sediment systems from England: a water-sandy clay loam sediment system (“Old Basing”, water: pH 7.4, total carbon 72.8; sediment: pH 7.4-8.0, organic carbon 8.3%); and a water-sand sediment system (“Virginia Water”, water: pH 6.8, total carbon 14.1; sediment: pH 6.0-6.6, organic carbon 2.8%).

The samples were treated at 81-83 µg a.i./L (equivalent to 250 g a.i./ha) and incubated for up to 120 days in the dark at 20 ± 2°C. The water was removed from the sediment, and the sediment was extracted by mechanical shaking at ambient temperatures once with acetone and once with acetone:water (90:10, v:v). Aliquots of the water and the sediment extracts were analyzed by LSC and one-dimensional reverse- and normal-phase TLC.

For the Old Basing water-sandy clay loam sediment system (both labels), based on nonlinear regression analysis, picoxystrobin dissipated with half-lives of 47.5 days in the total system, 17.3 days in the water layer, and 36.5 days in the sediment. For the Virginia Water water-sand sediment system (both labels), picoxystrobin dissipated with half-lives of 57.3 days in the total system, 13.1 days in the water layer, and 44.1 days in the sediment. Four transformation products were identified: Compound 2; Compound 3; Compound 7; and Compound 8. This study is classified as supplemental and upgradable upon submission of pesticide use history around the sampling sites.

MRID 48073840 (Anaerobic Aquatic Metabolism): The biotransformation of [pyridinyl-5-14C]- and [phenylacrylate-2-14C]-labeled methyl(E)-2-{2-[6-(trifluoromethyl)pyridin-2-yloxymethyl]phenyl}-3-methoxyacrylate (picoxystrobin, ZA1963; radiochemical purities ≥99.0%) in a purified water-UK sandy loam soil system (soil: pH 6.7, organic matter 2.8%) in the dark at ca. 20°C for 360 days. Picoxystrobin was applied to the systems at measured concentrations of 0.49 mg a.i./kg soil, reported to be equivalent to a field rate of ca. 0.25 kg a.i./ha. The test system consisted of glass pots (ca. 4.6 cm i.d. x 6.0 cm high) containing soil (35 g dry wt) flooded with Ultra-pure water (depth ca. 2.0-cm, volume not reported). The pots were placed on metal trays inside glass cylinders, and the glass cylinders were attached to a flow-through volatile trapping system. Moistened nitrogen gas was continuously drawn through the cylinders (flow rate not reported), then through two carbon sieves and tubes of ethanolamine. The water:soil systems were incubated for 33 days prior to treatment. After treatment, two pots of each label treatment were collected for immediate analysis at time 0, then single pots were collected at 4, 9, 21, 30, 50, 70, 91, 120, 220 and 360 days. Aliquots of the water and the soil extracts were analyzed by LSC and one-dimensional reverse- and normal-phase TLC. Based on nonlinear regression analyses, picoxystrobin (combined labels) dissipated with reviewer- calculated half-lives of 54.2 days in the total system, 5.2 days in the water and 67.3 days in the soil. Four transformation products were identified: Compound 2; Compound 3; Compound 7; and Compound 8.

158 This study is classified as supplemental. The stud was conducted using one soil/sediment instead of two sediments. The study was conducted using field soil and purified water, rather than natural sediment and its co-located water. Material balances were quite variable, ranging as low as 85.6-86.1% of the applied and there were concerns about the adequacy of the volatile trapping system and the analytical method (TLC). Redox potentials were measured in untreated surrogate samples rather than the treated samples, and dissolved oxygen content (water) were not measured in any samples. Limits of Detection and Quantitation were not reported. The temperature was reported only as ca. 20°C. It was not reported whether the water and soil extracts were stored prior to TLC analysis.

MRID 48073832 (Mobility Adsorption/Desorption): The adsorption/desorption characteristics of [pyridinyl-14C]-labeled methyl (2E)-3-methoxy-2-{2-[6-(trifluoromethyl)-2-pyridyloxymethyl]phenyl}acrylate (picoxystrobin; ZA1963; radiochemical purity 99%) were studied in two U.S. soils: a sandy loam [ERTC; pH 6.0, organic carbon 0.6%] from North Carolina and a silty clay loam [Champaign; pH 6.2, organic carbon 2.2%] from Illinois, and in four European soils: a sandy loam [Kenny Hill; pH 8.5; organic carbon 3.0%] from Suffolk, a sandy loam [18 Acres; pH 7.4; organic carbon 1.8%] from Berkshire, a sand [Lilly Field; pH 5.7, organic carbon 0.3%] from Surrey, and a sandy clay loam [Hyde Farm; pH 7.5; organic carbon 1.7%] from Berkshire, in a batch equilibrium experiment. The adsorption phase of the study was carried out by equilibrating air-dried soil with [14C]picoxystrobin at nominal concentrations of 0.2, 0.4, 0.8, 4.0, and 8.0 mg a.i./kg soil for all test soils. The test soils were equilibrated at 20 ± 2°C for 24 hours. The equilibrating solution used was 0.01M CaCl2 solution, with soil solution ratios of 1:4 (w:v) for all test soils. The desorption phase of the study was carried out by replacing the adsorption solution with an equivalent volume of 0.01M CaCl2 solution and equilibrating for >21 days. A single desorption step was conducted for all soils.

Following the adsorption and desorption phases, the supernatant solutions were separated by centrifugation and analyzed for total radioactivity using LSC. Average reviewer-calculated adsorption Kd values were 5.0, 24.0, 22.2, 16.8, 3.2, and 14.9 for the ERTC sandy loam, Champaign silty clay loam, Kenny Hill sandy loam, 18 Acres sandy loam, Lilly Field sand, and Hyde Farm sandy clay loam soils, respectively; corresponding adsorption Koc values were 837, 1089, 741, 933, 1067, and 878. Based on linear regression analysis, reviewer-calculated adsorption Kd values were 5.1, 23.4, 22.2, 16.5, 3.5, and 14.7 for the ERTC sandy loam, Champaign silty clay loam, Kenny Hill sandy loam, 18 Acres sandy loam, Lilly Field sand, and Hyde Farm sandy clay loam soils, respectively. Reviewer-calculated adsorption KF values were 4.9, 22.4, 22.4, 15.7, 3.5, and 14.0 for the ERTC sandy loam, Champaign silty clay loam, Kenny Hill sandy loam, 18 Acres sandy loam, Lilly Field sand, and Hyde Farm sandy clay loam soils, respectively; corresponding adsorption KFoc values were 817, 1018, 747, 872, 1167, and 824. Registrant-calculated desorption Kd values were 6.8, 28, 27, 20, 4.6, and 18 for the ERTC sandy loam, Champaign silty clay loam, Kenny Hill sandy loam, 18 Acres sandy loam, Lilly Field sand, and Hyde Farm sandy clay loam soils, respectively; corresponding desorption Koc values were 1200, 1300, 900, 1100, 1600, and 1000. Registrant-calculated Freundlich desorption K values were not reported. Freundlich desorption Koc values were 1100, 1000, 880, 1000, 1900, and 920 for the ERTC sandy loam, Champaign silty clay loam, Kenny Hill sandy loam, 18 Acres sandy loam, Lilly Field sand, and Hyde Farm sandy clay loam soils, respectively. This study is classified as supplemental and upgradable upon the submission of data answering the following issues: Analytically measured test concentrations were not reported. Sufficient raw data were not available for the reviewer to confirm study-author calculated data. It was unclear whether residues in the intercalculated solutions were accounted for in the data provided by the study authors. Mass balances were not determined for all test soil/test substance concentration combinations. Mass balances were not within acceptable limits for the 18 Acres sandy loam test soil. It was not reported whether the study was conducted in the dark. It was not established that the European soils used in this study were comparable to soils that would be found at the intended use sites in the United States.

MRID 48073833 (Laboratory Volatility): The laboratory volatility of [phenylacrylate-14C]-picoxystrobin (methyl(E)-a-(methoxymethylene)-2-[[[6-(trifluoromethyl)-2-pyridinyl]oxy]methyl]-benzeneacetate(9Cl); ZA1963, formulation of ca. 10% w/w suspension concentrate; batch no.: 96-J8; radiochemical purity 99.1-99.3%) on the surface of loamy sand soil (Speyer 2.1; pH 5.9; organic matter 0.6%) from the United Kingdom and Dwarf French Bean (Phaseolus vulgaris) leaves was measured following surface-spray application. The test material was applied to glass pots of moist soil (60% moisture holding capacity) and bean leaves at the flowering/fruit stage at an actual application rate of 225.1 g a.i./ha and 212.9 g a.i./ha, respectively. The nominal application rate of 250 g a.i./ha was equivalent to the maximum field rate for Dwarf French Bean plants. Treated soil pots were placed in a fume cupboard, and treated plant pots were placed in a glasshouse in front of an electric fan (air flow 1 to 2 m/s for each). Duplicate soil pots and leaves were collected at 0 (prior to being placed in air flow and within 5 minutes of application), 1, 3, 6, 20, and 24 hours.

Moist soil was sieved (2 mm), and a sample (ca. 1.5 g) was adjusted to 60% moisture holding capacity. Soil was placed in weighed glass pots (4.8 cm diameter x 3 cm deep), the surface of the soil was levelled, and the pot was re-weighed. The leaves of the bean plants were marked with a 5-cm diameter circle to indicate the area of test substance application, and excess leaves were removed. The test material was applied to the soil and leaves using a Camag Linomat III TLC applicator, which holds the

159 application solution in a glass syringe mounted above the surface, and aspirates the solution by a stream of nitrogen as a motor advances the plunger, applying the test material in a fine spray. Soil samples (amount not reported) were extracted by ultrasonication with acetonitrile:water (ca. 100 mL; 1:1, v:v) for ca. 15 minutes, followed by centrifugation (2500 rpm for 15 minutes) and decantation. Extracts were made to volume (not reported) and analyzed by LSC. Extracted soil was analyzed by LSC following combustion. Leaves were divided in equal pieces and analyzed by LSC following combustion. In the soil, total [14C]residue recoveries were 92.5% of the applied at time 0, and ranged from 87.4-93.1% of the applied over the 24-hour period. From the leaf surface, total [14C]residue recoveries were 87.8% of the applied at time 0, and ranged from 84.7-96.3% of the applied over the 24-hour period. Total [14C]residue recoveries after 24 hours were 91.1% of the applied in both the soil and leaf systems. This study is classified supplemental. Significant deviations from good scientific practices were noted. A material balance was not determined. Picoxystrobin was not identified; only [14C]residue recoveries in the soil extracts and leaf combustion samples were reported. Volatility was not expressed as µg/cm2/hour, and air concentrations were not expressed as µg/m3 or mg/m3. A method validation was not performed.

MRID 48073841 (Terrestrial Field Dissipation-North America): Soil dissipation/accumulation of picoxystrobin (DPX-YT669; (methyl(E)-2-{2-[6-(trifluoromethyl)pyridin-2-yloxymethyl]phenyl}-3-methoxyacrylate) under Canadian field conditions was studied using a bare plot of clay loam/loam soil at one site in Manitoba, Canada (Ecoregion 9.2). Picoxystrobin was broadcast once at a nominal rate of 1.0 kg a.i./ha (0.89 lb a.i./A) onto three 8 x 20 m replicate plots, which is above the proposed total seasonal application rate for picoxystrobin. Rainfall was supplemented with irrigation to reach 38.47 inches or 137% of the 30-year average rainfall during the study period. A control plot was established 30 m from the treated plot. For the total soil profile, picoxystrobin had a reviewer-calculated half-life value of 151 days (r2 = 0.8926) in soil. The major route of dissipation of picoxystrobin under terrestrial field conditions was transformation to IN-QDK50, IN-QDY62, and IN-QDY63. This study is classified as supplemental and upgradable upon the submission of the following data: the stability of picoxystrobin and its transformation products under typical laboratory storage conditions; and to establish comparability between the test site soils and US soils.

MRID 48073842 (Terrestrial Field Dissipation-North America): Soil dissipation/accumulation of picoxystrobin (DPX-YT669; (methyl(E)-2-{2-[6-(trifluoromethyl)pyridin-2-yloxymethyl]phenyl}-3-methoxyacrylate) under U.S. field conditions was studied using a bare plot of sandy loam soil at one site near Porterville, California (Ecoregion 11.1. Picoxystrobin was broadcast once at a nominal rate of 1.0 kg a.i./ha (0.89 lb a.i./A) onto three 6 x 15 m replicate plots, which is above the proposed total annual application rate for picoxystrobin (the maximum proposed rate was not reported). Rainfall was supplemented with irrigation to reach 44.46 inches or 573% of the 10-year average rainfall through 270 days posttreatment. A control plot was established 258 m from the treated plot. Soil samples were collected prior to application and at 0, 1, 5, 11, 15, 29, 43, 60, 89, 119, 148, 180, 270, and 363 days following application to a depth of 0-90 cm, excluding day 0 samples which were collected to a depth of 30 cm. The reviewer calculated a half-life of 8.6 days (r2 = 0.9064. Picoxystrobin was not detected in soil below the 0-5 cm depth at a mean concentration above the LOQ, precluding the determination of a half-life for the total soil profile. The major route of dissipation of picoxystrobin under terrestrial field conditions was transformation to IN-QDK50, IN- QDY62, and IN-QDY63. This study is classified supplemental and upgradable upon the submission of information demonstrating the stability of picoxystrobin and its transformation products under typical laboratory storage conditions.

MRID 48073843 (Terrestrial Field Dissipation-North America): Soil dissipation/accumulation of picoxystrobin (DPX-YT669; (methyl(E)-2-{2-[6-(trifluoromethyl)pyridin-2-yloxymethyl]phenyl}-3-methoxyacrylate) under US field conditions was studied using a bare plot of sandy loam/loamy sand soil at one site near Arkansaw, Wisconsin (Ecoregion 8.1). Picoxystrobin was broadcast once at a nominal rate of 1.0 kg a.i./ha (0.89 lb a.i./A) onto three 37 x 5 m replicate plots, which is above the proposed total annual application rate for picoxystrobin. Rainfall was supplemented with irrigation to reach 17.2 inches or 116% of the 10-year average rainfall through 120 days posttreatment. A control plot was established ca. 15 m from the treated plot. The reviewer calculated a half-life of 6.6 days (r2 = 0.9174). Picoxystrobin was not detected below the 0-5 cm depth at a concentration above the LOQ, precluding the determination of a half-life for the total soil profile. The major route of dissipation of picoxystrobin under terrestrial field conditions was transformation to IN-QDK50, IN-QDY62, and IN-QDY63. This study is classified supplemental and upgradable upon the submission of information demonstrating the stability of picoxystrobin and its transformation products under typical laboratory storage conditions.

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MRID 48073844 (Terrestrial Field Dissipation-North America): Soil dissipation/accumulation of picoxystrobin (DPX-YT669; (methyl(E)-2-{2-[6-(trifluoromethyl)pyridin-2-yloxymethyl]phenyl}-3-methoxyacrylate) under Canadian field conditions was studied using a bare plot of sandy loam soil at one site in Prince Edward Island, Canada (Ecoregion 8.1). Picoxystrobin was broadcast once at a nominal rate of 1.0 kg a.i./ha (0.89 lb a.i./A) onto three 6 x 20 m replicate plots, which is above the proposed total seasonal application rate for picoxystrobin (the maximum proposed rate was not reported). Rainfall was supplemented with irrigation to reach 33.76 inches or 150% of the 30-year average rainfall through 177 days posttreatment. A control plot was established 16 m from the treated plot.

The reviewer calculated a half-life of 13.4 days (r2 = 0.9122). Picoxystrobin was not detected below the 0-5 cm depth at a concentration above the LOQ, precluding the determination of a half-life for the total soil profile. The major route of dissipation of picoxystrobin under terrestrial field conditions was transformation to IN-QDK50, IN-QDY62, and IN-QDY63. This study is classified as supplemental and upgradable upon the submission of the following data: the stability of picoxystrobin and its transformation products under typical laboratory storage conditions; and to establish comparability between the test site soils and US soils.

MRID 48073846 (Terrestrial Field Dissipation-Europe): Soil dissipation/accumulation of picoxystrobin (ZA1963; (methyl(E)-2-{2-[6-(trifluoromethyl)pyridin-2-yloxymethyl]phenyl}-3-methoxyacrylate) under France field conditions was studied using a bare plot of silty clay loam soil near Grisolles, in Southern France (Site 1) and a bare plot of sandy loam soil near Vitray, in Southern France (Site 2). Picoxystrobin was sprayed once at a target rate of 0.750 kg a.i./ha (0.670 lb a.i./A) onto one plot measuring 34-36 x 3 m. The test application was made at the highest European label application rate for cereals. Total rainfall during the study period was 713 mm or 93.2% of the normal precipitation for Site 1, and was 518 mm for Site 2 (historical precipitation data were not reported for Site 2). A control plot was not established at either test site. The reviewer calculated a half-life of 35 days (r2 = 0.9560). Residues of picoxystrobin were not detected above the LOQ in soil below the 0-10 cm depth, precluding the separate determination of a total soil half-life. The major route of dissipation of picoxystrobin under terrestrial field conditions at the two test sites was transformation to R403092, R403814, and R408509. This study is classified as supplemental and upgradable upon the submission of the following data: the stability of picoxystrobin and its transformation products under typical laboratory storage conditions; a plot use history; and to establish comparability between the test site soils and US soils.

MRID 48073847 (Terrestrial Field Dissipation-Europe): Soil dissipation/accumulation of picoxystrobin (ZA1963; (methyl(E)-2-{2-[6-(trifluoromethyl)pyridin-2-yloxymethyl]phenyl}-3-methoxyacrylate) under UK field conditions was studied using a bare plot of sandy clay loam soil near Maidenhead, in the United Kingdom. Picoxystrobin was sprayed once at a target rate of 0.750 kg a.i./ha (0.670 lb a.i./A) onto one plot measuring 5 x 45 m. The test application was made at the highest European label application rate for cereals. Total rainfall during the study period was not reported, but was believed to be less than the historical average precipitation. A control plot was not established at the test site. The reviewer calculated a half-life of 55 days (r2 = 0.9805. Residues of picoxystrobin were not detected above the LOQ in soil below the 0-10 cm depth, precluding the separate determination of a total soil half-life. The major route of dissipation of picoxystrobin under terrestrial field conditions at the test site was transformation to R403092, R403814, and R408509. This study is classified as supplemental and upgradable upon the submission of the following data: the stability of picoxystrobin and its transformation products under typical laboratory storage conditions; a plot use history; and to establish comparability between the test site soils and US soils.

MRID 48073848 (Terrestrial Field Dissipation-Europe): Soil dissipation/accumulation of picoxystrobin (ZA1963; (methyl(E)-2-{2-[6-(trifluoromethyl)pyridin-2-yloxymethyl]phenyl}-3-methoxyacrylate) under Germany field conditions was studied using a bare plot of sandy clay loam soil in Saxe-Anhalt, Germany. Picoxystrobin was sprayed once at a target rate of 0.750 kg a.i./ha (0.670 lb a.i./A) onto one plot measuring 2.5 x 32 m. The proposed maximum label rate was not reported. The total rainfall during the study period was 502 mm or 79% of the historical average (reviewer-calculated). A control plot was not established at the test site.

The reviewer calculated a half-life of 26 days (r2 = 0.9443). Residues of picoxystrobin were not detected above the LOQ in soil below the 0-10 cm depth, precluding the separate determination of a total soil half-life. The major route of dissipation of picoxystrobin under terrestrial field conditions at the test site was transformation to R403092, R403814, and R408509. This study is classified as supplemental and upgradable upon the submission of the following data: the stability of picoxystrobin and its transformation products under typical laboratory storage conditions; a plot use history; and to

161 establish comparability between the test site soils and US soils.

MRID 48073849 (Terrestrial Field Dissipation-Europe): Soil dissipation/accumulation of picoxystrobin (ZA1963; (methyl(E)-2-{2-[6-(trifluoromethyl)pyridin-2-yloxymethyl]phenyl}-3-methoxyacrylate) under France field conditions was studied using a bare plot of silty clay soil at St Remy de Provence, in Southern France (Site 1), and a bare plot of clay loam soil at Cessac, in Southern France (Site 2). Picoxystrobin was sprayed once at a target rate of 0.750 kg a.i./ha (0.670 lb a.i./A) onto one plot measuring a minimum of 32 x 3 m. The test application was made at the proposed label rate. Total water input (rainfall + irrigation) during the study period was 539 mm for Site 1, and was 926 mm for Site 2 (historical precipitation data were not reported for either site). A control plot was not established at either test site. The reviewer calculated a half-life of 47 days (r2 = 0.9898). Residues of picoxystrobin were not detected above the LOQ in soil below the 0-10 cm depth, precluding the separate determination of a total soil half-life. The major route of dissipation of picoxystrobin under terrestrial field conditions at the two test sites was transformation to R403814 and R408509. This study is classified as supplemental and upgradable upon the submission of the following data: the stability of picoxystrobin and its transformation products under typical laboratory storage conditions; a plot use history; and to establish comparability between the test site soils and US soils.

MRID 48073850 (Terrestrial Field Dissipation-Europe): Soil dissipation/accumulation of picoxystrobin (ZA1963; (methyl(E)-2-{2-[6-(trifluoromethyl)pyridin-2-yloxymethyl]phenyl}-3-methoxyacrylate) under Germany field conditions was studied using a bare plot of sandy loam soil in Schleswig-Holstein, Germany. Picoxystrobin was sprayed once at a target rate of 0.750 kg a.i./ha (0.670 lb a.i./A) onto one plot measuring 2.5 x 32 m. The proposed maximum label rate was not reported. The total rainfall during the study period was 716 mm or 99% of the historical average (reviewer-calculated). A control plot was not established at the test site. The reviewer calculated a half-life of 10 days (r2 = 0.9748). Residues of picoxystrobin were not detected above the LOQ in soil below the 0-10 cm depth, precluding the separate determination of a total soil half-life. The major route of dissipation of picoxystrobin under terrestrial field conditions at the test site was transformation to R403814 and R408509. This study is classified as supplemental and upgradable upon the submission of the following data: the stability of picoxystrobin and its transformation products under typical laboratory storage conditions; a plot use history; and to establish comparability between the test site soils and US soils.

MRID 48073851 (Terrestrial Field Dissipation-Europe): Soil dissipation/accumulation of picoxystrobin (ZA1963; (methyl(E)-2-{2-[6-(trifluoromethyl)pyridin-2-yloxymethyl]phenyl}-3-methoxyacrylate) under UK field conditions was studied using a bare plot of sandy clay loam soil at Bracknell, Berkshire, in the United Kingdom. Picoxystrobin was sprayed once at a target rate of 0.750 kg a.i./ha (0.670 lb a.i./A) onto one plot measuring 5 x 45 m. The test application was made at the proposed label rate at the time of the study. Total rainfall during the study period was ca. 866 mm (reviewer-calculated), and was higher than the historical average precipitation. A small control plot was established adjacent to the treated plot.

The reviewer calculated a half-life of 3.5 days (r2 = 0.9395). Residues of picoxystrobin were not detected above the LOQ in soil below the 0-10 cm depth (excluding one detection at the LOQ), precluding the separate determination of a total soil half-life. The major route of dissipation of picoxystrobin under terrestrial field conditions at the test site was transformation to R403092, R403814, and R408509. This study is classified as supplemental and upgradable upon the submission of the following data: the stability of picoxystrobin and its transformation products under typical laboratory storage conditions; a plot use history; and to establish comparability between the test site soils and US soils.

MRID 48073776 (Fish Accumulation): The bioconcentration of [14C]ZA1963 (purity >99%) was studied in the bluegill sunfish (Lepomis macrochirus) under flow-through conditions. A total of 128 fish (64 fish/test aquarium) with a mean body weight of 1.21 g and mean body length of 39.0 mm were exposed to ZA1963 in 100L glass aquaria for 28 days (uptake phase), at a nominal concentration of 0 (solvent control) and 5.0 µg a.i./L. The subsequent depuration phase lasted 14 days. Throughout the experiments, the pH of the water ranged from 7.30 to 7.9, the dissolved oxygen ranged from 7.0 to 8.6 mg/L and the temperature ranged from 21.8 to 22.4°C. The photoperiod was 16-hours light/ 8-hours dark, with artificial lighting at an intensity of 590-750 lux.

162

In the experiment, four fish and triplicate water samples were collected on days -2, 0, 1, 3, 7, 14, 21, and 28 during the exposure phase, and on days 0.3, 1, 3, 7 and 14 of the depuration phase. Total radioactivity in water and fish tissue was measured using Liquid Scintillation Counting (LSC). Water and fish tissue extracts were analyzed for [14C]ZA1963 residues by solid phase extraction followed by Thin Layer Chromatography (TLC). [14C]ZA1963 concentrations in fish during the uptake phase showed a clear accumulation trend in fish tissue, reaching steady state within 5 days of exposure. The steady state BCF in various fish tissues was 1400 in viscera, 110 in flesh and 170 in the carcass. The steady state whole fish BCF was 290. When expressed on a mean lipid weight basis, the steady state whole fish BCF was 3400. When exposure ceased, the residues were depurated with a reviewer-calculated half-life of 0.98 days for whole fish tissues. A total of 55% and 86% of the steady state residues levels were depurated from whole fish within 24 hours and 14 days in uncontaminated dilution water, respectively. The uptake rate constant, -1 -1 K1, and the depuration rate constant, K2, were determined to be 181 day and 0.63 day , respectively. The reviewer-calculated kinetic bioconcentration factor (BCFK; calculated as K1/K2) for whole fish was 287, which corresponds well with the steady state BCF of 290. In general, the data indicate that [14C]ZA1963 does not appear to bioconcentrate in fish under the test conditions of this study. This study is classified as supplemental and upgradable upon the submission of water samples analysis for [14C]ZA1963 or its transformation products

163 Appendix F

The aquatic exposure model inputs and outputs stored as pcxyNDWheatGr.out Chemical: picoxystrobin PRZM environment: NDwheatSTD.txt modified Tueday, 29 May 2007 at 13:59:34 EXAMS environment: pond298.exv modified Thuday, 29 August 2002 at 16:33:30 Metfile: w14914.dvf modified Wedday, 3 July 2002 at 09:05:52 Water segment concentrations (ppb)

Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 1961 1.147 1.107 0.9919 0.8421 0.7695 0.2968 1962 1.585 1.543 1.342 1.247 1.199 0.7428 1963 2.067 1.976 1.697 1.319 1.157 0.7672 1964 1.392 1.343 1.179 0.9935 0.9133 0.7034 1965 0.9997 0.9652 0.9047 0.8579 0.8457 0.6841 1966 1.42 1.369 1.247 1.062 0.9795 0.6978 1967 0.6891 0.6865 0.676 0.6534 0.6387 0.492 1968 0.5149 0.4964 0.4712 0.4021 0.3677 0.313 1969 2.798 2.671 2.316 1.775 1.542 0.7327 1970 1.865 1.798 1.577 1.309 1.201 0.8206 1971 1.283 1.248 1.189 1.132 1.108 0.838 1972 1.016 0.9824 0.9144 0.8819 0.8482 0.7536 1973 1.775 1.721 1.564 1.381 1.305 0.7834 1974 4.014 3.855 3.307 2.663 2.451 1.422 1975 2.929 2.846 2.485 2.002 1.857 1.487 1976 1.209 1.205 1.188 1.152 1.128 0.7522 1977 2.282 2.207 1.851 1.394 1.277 0.7714 1978 1.63 1.589 1.384 1.118 1.049 0.8548 1979 1.56 1.495 1.306 1.024 0.9369 0.7623 1980 1.801 1.745 1.549 1.374 1.29 0.8134 1981 1.161 1.119 0.9793 0.888 0.8643 0.7299 1982 1.741 1.7 1.512 1.259 1.133 0.6376 1983 1.576 1.511 1.302 1.141 1.102 0.8463 1984 1.642 1.594 1.458 1.252 1.091 0.7361 1985 1.396 1.343 1.218 1.128 1.039 0.8176 1986 1.188 1.157 1.06 0.9429 0.9162 0.7176 1987 1.086 1.039 0.9325 0.8632 0.8026 0.6198 1988 1.353 1.308 1.17 0.9874 0.9112 0.5928 1989 2.21 2.133 1.908 1.573 1.427 0.8568 1990 1.01 1.006 0.9895 0.956 0.9333 0.7095

Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly 0.032258064516129 4.014 3.855 3.307 2.663 2.451 1.487 0.0645161290322581 2.929 2.846 2.485 2.002 1.857 1.422 0.0967741935483871 2.798 2.671 2.316 1.775 1.542 0.8568 0.129032258064516 2.282 2.207 1.908 1.573 1.427 0.8548 0.161290322580645 2.21 2.133 1.851 1.394 1.305 0.8463 0.193548387096774 2.067 1.976 1.697 1.381 1.29 0.838

164 0.225806451612903 1.865 1.798 1.577 1.374 1.277 0.8206 0.258064516129032 1.801 1.745 1.564 1.319 1.201 0.8176 0.290322580645161 1.775 1.721 1.549 1.309 1.199 0.8134 0.32258064516129 1.741 1.7 1.512 1.259 1.157 0.7834 0.354838709677419 1.642 1.594 1.458 1.252 1.133 0.7714 0.387096774193548 1.63 1.589 1.384 1.247 1.128 0.7672 0.419354838709677 1.585 1.543 1.342 1.152 1.108 0.7623 0.451612903225806 1.576 1.511 1.306 1.141 1.102 0.7536 0.483870967741936 1.56 1.495 1.302 1.132 1.091 0.7522 0.516129032258065 1.42 1.369 1.247 1.128 1.049 0.7428 0.548387096774194 1.396 1.343 1.218 1.118 1.039 0.7361 0.580645161290323 1.392 1.343 1.189 1.062 0.9795 0.7327 0.612903225806452 1.353 1.308 1.188 1.024 0.9369 0.7299 0.645161290322581 1.283 1.248 1.179 0.9935 0.9333 0.7176 0.67741935483871 1.209 1.205 1.17 0.9874 0.9162 0.7095 0.709677419354839 1.188 1.157 1.06 0.956 0.9133 0.7034 0.741935483870968 1.161 1.119 0.9919 0.9429 0.9112 0.6978 0.774193548387097 1.147 1.107 0.9895 0.888 0.8643 0.6841 0.806451612903226 1.086 1.039 0.9793 0.8819 0.8482 0.6376 0.838709677419355 1.016 1.006 0.9325 0.8632 0.8457 0.6198 0.870967741935484 1.01 0.9824 0.9144 0.8579 0.8026 0.5928 0.903225806451613 0.9997 0.9652 0.9047 0.8421 0.7695 0.492 0.935483870967742 0.6891 0.6865 0.676 0.6534 0.6387 0.313 0.967741935483871 0.5149 0.4964 0.4712 0.4021 0.3677 0.2968

0.1 2.7464 2.6246 2.2752 1.7548 1.5305 0.8566 Average of yearly averages: 0.758416666666667

Inputs generated by pe5.pl - Novemeber 2006

Data used for this run: Output File: pcxyNDWheatGr Metfile: w14914.dvf PRZM scenario: NDwheatSTD.txt EXAMS environment file: pond298.exv Chemical Name: picoxystrobin Description Variable Name Value Units Comments Molecular weight mwt 367.3 g/mol Henry's Law Const. henry 6.6E-9 atm-m^3/mol Vapor Pressure vapr 4.14E-8 torr Solubility sol 3 mg/L Kd Kd mg/L Koc Koc 799 mg/L Photolysis half-life kdp 28.9 days Half-life Aerobic Aquatic Metabolism kbacw 43.8 days Halfife Anaerobic Aquatic Metabolism kbacs 250 days Halfife Aerobic Soil Metabolism asm 60.5 days Halfife Hydrolysis: pH 7 0 days Half-life Method: CAM 2 integer See PRZM manual Incorporation Depth: DEPI 0 cm Application Rate: TAPP 0.073 kg/ha Application Efficiency: APPEFF 0.99 fraction Spray Drift DRFT 0.01 fraction of application rate applied to pond

165 Application Date Date 04-06 dd/mm or dd/mmm or dd-mm or dd-mmm Interval 1 interval 18 days Set to 0 or delete line for single app. app. rate 1 apprate 0.218 kg/ha Interval 2 interval 7 days Set to 0 or delete line for single app. app. rate 2 apprate 0.218 kg/ha Interval 3 interval 7 days Set to 0 or delete line for single app. app. rate 3 apprate 0.146 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)

stored as pcxyNDWheatAr.out Chemical: picoxystrobin PRZM environment: NDwheatSTD.txt modified Tueday, 29 May 2007 at 13:59:34 EXAMS environment: pond298.exv modified Thuday, 29 August 2002 at 16:33:30 Metfile: w14914.dvf modified Wedday, 3 July 2002 at 09:05:52 Water segment concentrations (ppb)

Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 1961 1.413 1.37 1.249 1.084 1.005 0.4963 1962 2.628 2.526 2.254 1.932 1.78 1.07 1963 2.565 2.462 2.136 1.697 1.594 1.121 1964 1.956 1.871 1.698 1.417 1.426 1.067 1965 1.886 1.814 1.691 1.546 1.463 1.088 1966 1.917 1.857 1.739 1.591 1.542 1.109 1967 1.898 1.827 1.661 1.363 1.201 0.9177 1968 1.743 1.671 1.514 1.227 1.08 0.7428 1969 3.596 3.442 3.101 2.37 2.094 1.14 1970 2.202 2.133 1.904 1.629 1.518 1.209 1971 1.979 1.931 1.779 1.493 1.469 1.229 1972 1.912 1.842 1.676 1.565 1.479 1.153 1973 2.129 2.073 1.909 1.745 1.656 1.182 1974 4.475 4.307 3.729 3.149 2.889 1.793 1975 3.885 3.782 3.412 2.707 2.459 1.853 1976 2.035 1.957 1.787 1.46 1.407 1.129 1977 3.35 3.192 2.745 2.072 1.864 1.15 1978 2.111 2.058 1.865 1.708 1.674 1.241 1979 2.347 2.253 1.966 1.768 1.596 1.154 1980 2.176 2.117 1.91 1.759 1.659 1.2 1981 2.146 2.064 1.872 1.605 1.454 1.126 1982 2.082 2.04 1.851 1.597 1.472 1.045 1983 2.482 2.375 2.241 1.86 1.718 1.236

166 1984 2.021 1.942 1.771 1.562 1.409 1.12 1985 2.297 2.21 1.973 1.811 1.678 1.218 1986 2.006 1.925 1.782 1.606 1.545 1.131 1987 1.892 1.813 1.579 1.495 1.395 1.014 1988 1.67 1.623 1.478 1.289 1.223 0.9559 1989 2.546 2.468 2.238 1.883 1.745 1.207 1990 2.042 1.965 1.795 1.471 1.301 1.081

Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly 0.032258064516129 4.475 4.307 3.729 3.149 2.889 1.853 0.0645161290322581 3.885 3.782 3.412 2.707 2.459 1.793 0.0967741935483871 3.596 3.442 3.101 2.37 2.094 1.241 0.129032258064516 3.35 3.192 2.745 2.072 1.864 1.236 0.161290322580645 2.628 2.526 2.254 1.932 1.78 1.229 0.193548387096774 2.565 2.468 2.241 1.883 1.745 1.218 0.225806451612903 2.546 2.462 2.238 1.86 1.718 1.209 0.258064516129032 2.482 2.375 2.136 1.811 1.678 1.207 0.290322580645161 2.347 2.253 1.973 1.768 1.674 1.2 0.32258064516129 2.297 2.21 1.966 1.759 1.659 1.182 0.354838709677419 2.202 2.133 1.91 1.745 1.656 1.154 0.387096774193548 2.176 2.117 1.909 1.708 1.596 1.153 0.419354838709677 2.146 2.073 1.904 1.697 1.594 1.15 0.451612903225806 2.129 2.064 1.872 1.629 1.545 1.14 0.483870967741936 2.111 2.058 1.865 1.606 1.542 1.131 0.516129032258065 2.082 2.04 1.851 1.605 1.518 1.129 0.548387096774194 2.042 1.965 1.795 1.597 1.479 1.126 0.580645161290323 2.035 1.957 1.787 1.591 1.472 1.121 0.612903225806452 2.021 1.942 1.782 1.565 1.469 1.12 0.645161290322581 2.006 1.931 1.779 1.562 1.463 1.109 0.67741935483871 1.979 1.925 1.771 1.546 1.454 1.088 0.709677419354839 1.956 1.871 1.739 1.495 1.426 1.081 0.741935483870968 1.917 1.857 1.698 1.493 1.409 1.07 0.774193548387097 1.912 1.842 1.691 1.471 1.407 1.067 0.806451612903226 1.898 1.827 1.676 1.46 1.395 1.045 0.838709677419355 1.892 1.814 1.661 1.417 1.301 1.014 0.870967741935484 1.886 1.813 1.579 1.363 1.223 0.9559 0.903225806451613 1.743 1.671 1.514 1.289 1.201 0.9177 0.935483870967742 1.67 1.623 1.478 1.227 1.08 0.7428 0.967741935483871 1.413 1.37 1.249 1.084 1.005 0.4963

0.1 3.5714 3.417 3.0654 2.3402 2.071 1.2405 Average of yearly averages: 1.13929

Inputs generated by pe5.pl - Novemeber 2006

Data used for this run: Output File: pcxyNDWheatAr Metfile: w14914.dvf PRZM scenario: NDwheatSTD.txt EXAMS environment file: pond298.exv Chemical Name: picoxystrobin Description Variable Name Value Units Comments

167 Molecular weight mwt 367.3 g/mol Henry's Law Const. henry 6.6E-9 atm-m^3/mol Vapor Pressure vapr 4.14E-8 torr Solubility sol 3 mg/L Kd Kd mg/L Koc Koc 799 mg/L Photolysis half-life kdp 28.9 days Half-life Aerobic Aquatic Metabolism kbacw 43.8 days Halfife Anaerobic Aquatic Metabolism kbacs 250 days Halfife Aerobic Soil Metabolism asm 60.5 days Halfife Hydrolysis: pH 7 0 days Half-life Method: CAM 2 integer See PRZM manual Incorporation Depth: DEPI 0 cm Application Rate: TAPP 0.073 kg/ha Application Efficiency: APPEFF 0.95 fraction Spray Drift DRFT 0.05 fraction of application rate applied to pond Application Date Date 04-06 dd/mm or dd/mmm or dd-mm or dd-mmm Interval 1 interval 18 days Set to 0 or delete line for single app. app. rate 1 apprate 0.218 kg/ha Interval 2 interval 7 days Set to 0 or delete line for single app. app. rate 2 apprate 0.218 kg/ha Interval 3 interval 7 days Set to 0 or delete line for single app. app. rate 3 apprate 0.146 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)

stored as pcxyMSCornGr.out Chemical: picoxystrobin PRZM environment: MScornSTD.txt modified Tueday, 29 May 2007 at 13:57:40 EXAMS environment: pond298.exv modified Thuday, 29 August 2002 at 16:33:30 Metfile: w03940.dvf modified Wedday, 3 July 2002 at 09:05:46 Water segment concentrations (ppb)

Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 1961 4.429 4.247 3.731 3.19 2.799 1.142 1962 2.07 1.96 1.807 1.657 1.549 1.165 1963 1.402 1.354 1.291 1.001 0.9404 0.7004 1964 4.976 4.797 4.175 3.372 3.112 1.691 1965 6.838 6.48 5.33 4.012 3.459 2.005 1966 6.2 5.989 4.976 3.723 3.272 1.977 1967 2.936 2.801 2.512 2.068 1.948 1.483 1968 2.2 2.091 1.8 1.543 1.46 1.206 1969 3.763 3.558 2.884 2.081 1.829 1.155

168 1970 3.388 3.271 3.064 2.705 2.517 1.487 1971 4.872 4.604 4.029 3.202 3.033 1.811 1972 1.88 1.863 1.798 1.658 1.558 1.196 1973 1.274 1.213 1.118 1.035 0.9667 0.7523 1974 2.801 2.66 2.349 2.174 2.015 1.058 1975 15.17 14.55 12.75 9.454 7.974 3.294 1976 4.03 3.872 3.658 3.363 3.159 2.517 1977 3.981 3.763 3.039 2.49 2.335 1.715 1978 2.513 2.424 2.211 1.791 1.809 1.357 1979 8.509 8.081 6.91 6.24 5.687 2.932 1980 3.131 3.108 3.025 2.856 2.719 1.74 1981 2.301 2.222 1.968 1.678 1.652 1.173 1982 8.962 8.446 6.994 5.096 4.508 2.303 1983 3.886 3.675 3.111 2.451 2.326 1.875 1984 4.27 4.048 3.392 2.526 2.496 1.751 1985 6.86 6.471 5.218 3.865 3.396 1.927 1986 3.601 3.445 2.852 2.263 2.114 1.746 1987 2.669 2.56 2.163 1.653 1.539 1.289 1988 2.944 2.84 2.518 2.293 2.139 1.236 1989 2.708 2.63 2.44 2.165 2.122 1.395 1990 1.977 1.957 1.89 1.723 1.593 1.129

Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly 0.032258064516129 15.17 14.55 12.75 9.454 7.974 3.294 0.0645161290322581 8.962 8.446 6.994 6.24 5.687 2.932 0.0967741935483871 8.509 8.081 6.91 5.096 4.508 2.517 0.129032258064516 6.86 6.48 5.33 4.012 3.459 2.303 0.161290322580645 6.838 6.471 5.218 3.865 3.396 2.005 0.193548387096774 6.2 5.989 4.976 3.723 3.272 1.977 0.225806451612903 4.976 4.797 4.175 3.372 3.159 1.927 0.258064516129032 4.872 4.604 4.029 3.363 3.112 1.875 0.290322580645161 4.429 4.247 3.731 3.202 3.033 1.811 0.32258064516129 4.27 4.048 3.658 3.19 2.799 1.751 0.354838709677419 4.03 3.872 3.392 2.856 2.719 1.746 0.387096774193548 3.981 3.763 3.111 2.705 2.517 1.74 0.419354838709677 3.886 3.675 3.064 2.526 2.496 1.715 0.451612903225806 3.763 3.558 3.039 2.49 2.335 1.691 0.483870967741936 3.601 3.445 3.025 2.451 2.326 1.487 0.516129032258065 3.388 3.271 2.884 2.293 2.139 1.483 0.548387096774194 3.131 3.108 2.852 2.263 2.122 1.395 0.580645161290323 2.944 2.84 2.518 2.174 2.114 1.357 0.612903225806452 2.936 2.801 2.512 2.165 2.015 1.289 0.645161290322581 2.801 2.66 2.44 2.081 1.948 1.236 0.67741935483871 2.708 2.63 2.349 2.068 1.829 1.206 0.709677419354839 2.669 2.56 2.211 1.791 1.809 1.196 0.741935483870968 2.513 2.424 2.163 1.723 1.652 1.173 0.774193548387097 2.301 2.222 1.968 1.678 1.593 1.165 0.806451612903226 2.2 2.091 1.89 1.658 1.558 1.155 0.838709677419355 2.07 1.96 1.807 1.657 1.549 1.142 0.870967741935484 1.977 1.957 1.8 1.653 1.539 1.129 0.903225806451613 1.88 1.863 1.798 1.543 1.46 1.058 0.935483870967742 1.402 1.354 1.291 1.035 0.9667 0.7523

169 0.967741935483871 1.274 1.213 1.118 1.001 0.9404 0.7004

0.1 8.3441 7.9209 6.752 4.9876 4.4031 2.4956 Average of yearly averages: 1.60692333333333

Inputs generated by pe5.pl - Novemeber 2006

Data used for this run: Output File: pcxyMSCornGr Metfile: w03940.dvf PRZM scenario: MScornSTD.txt EXAMS environment file: pond298.exv Chemical Name: picoxystrobin Description Variable Name Value Units Comments Molecular weight mwt 367.3 g/mol Henry's Law Const. henry 6.6E-9 atm-m^3/mol Vapor Pressure vapr 4.14E-8 torr Solubility sol 3 mg/L Kd Kd mg/L Koc Koc 799 mg/L Photolysis half-life kdp 28.9 days Half-life Aerobic Aquatic Metabolism kbacw 43.8 days Halfife Anaerobic Aquatic Metabolism kbacs 250 days Halfife Aerobic Soil Metabolism asm 60.5 days Halfife Hydrolysis: pH 7 0 days Half-life Method: CAM 2 integer See PRZM manual Incorporation Depth: DEPI 0 cm Application Rate: TAPP 0.073 kg/ha Application Efficiency: APPEFF 0.99 fraction Spray Drift DRFT 0.01 fraction of application rate applied to pond Application Date Date 26-05 dd/mm or dd/mmm or dd-mm or dd-mmm Interval 1 interval 44 days Set to 0 or delete line for single app. app. rate 1 apprate 0.218 kg/ha Interval 2 interval 7 days Set to 0 or delete line for single app. app. rate 2 apprate 0.218 kg/ha Interval 3 interval 7 days Set to 0 or delete line for single app. app. rate 3 apprate 0.146 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)

stored as pcxyMSCornAr.out Chemical: picoxystrobin PRZM environment: MScornSTD.txt modified Tueday, 29 May 2007 at 13:57:40 EXAMS environment: pond298.exv modified Thuday, 29 August 2002 at 16:33:30

170 Metfile: w03940.dvf modified Wedday, 3 July 2002 at 09:05:46 Water segment concentrations (ppb)

Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 1961 5.093 4.873 4.298 3.629 3.153 1.267 1962 2.689 2.545 2.072 1.743 1.637 1.345 1963 1.901 1.805 1.63 1.285 1.083 0.9064 1964 5.014 4.84 4.233 3.444 3.289 1.861 1965 6.9 6.546 5.409 4.108 3.558 2.171 1966 6.577 6.348 5.283 3.98 3.527 2.156 1967 3.307 3.16 2.828 2.344 2.236 1.697 1968 2.593 2.469 2.148 1.802 1.717 1.426 1969 4.118 3.9 3.181 2.454 2.212 1.36 1970 3.468 3.354 3.153 2.81 2.639 1.673 1971 5.528 5.225 4.558 3.563 3.33 1.981 1972 2.282 2.172 1.886 1.744 1.64 1.38 1973 1.577 1.507 1.313 1.159 1.13 0.9553 1974 3.098 2.949 2.613 2.41 2.24 1.258 1975 15.35 14.73 12.97 9.585 8.081 3.414 1976 4.253 4.097 3.859 3.403 3.197 2.671 1977 4.715 4.456 3.596 2.86 2.633 1.895 1978 2.648 2.56 2.354 1.93 1.936 1.544 1979 8.919 8.472 7.423 6.593 5.958 3.067 1980 3.203 3.18 3.096 2.924 2.785 1.908 1981 2.421 2.343 2.09 1.818 1.82 1.36 1982 9.373 8.837 7.307 5.418 4.759 2.45 1983 4.384 4.148 3.497 2.664 2.389 2.044 1984 4.684 4.445 3.747 2.85 2.717 1.931 1985 7.126 6.729 5.447 4.05 3.559 2.096 1986 4.34 4.154 3.5 2.701 2.461 1.915 1987 3.134 3.016 2.61 2.093 1.866 1.477 1988 3.065 2.962 2.644 2.41 2.252 1.428 1989 2.832 2.737 2.549 2.28 2.254 1.585 1990 2.086 2.067 1.999 1.826 1.691 1.326

Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly 0.032258064516129 15.35 14.73 12.97 9.585 8.081 3.414 0.0645161290322581 9.373 8.837 7.423 6.593 5.958 3.067 0.0967741935483871 8.919 8.472 7.307 5.418 4.759 2.671 0.129032258064516 7.126 6.729 5.447 4.108 3.559 2.45 0.161290322580645 6.9 6.546 5.409 4.05 3.558 2.171 0.193548387096774 6.577 6.348 5.283 3.98 3.527 2.156 0.225806451612903 5.528 5.225 4.558 3.629 3.33 2.096 0.258064516129032 5.093 4.873 4.298 3.563 3.289 2.044 0.290322580645161 5.014 4.84 4.233 3.444 3.197 1.981 0.32258064516129 4.715 4.456 3.859 3.403 3.153 1.931 0.354838709677419 4.684 4.445 3.747 2.924 2.785 1.915 0.387096774193548 4.384 4.154 3.596 2.86 2.717 1.908 0.419354838709677 4.34 4.148 3.5 2.85 2.639 1.895 0.451612903225806 4.253 4.097 3.497 2.81 2.633 1.861 0.483870967741936 4.118 3.9 3.181 2.701 2.461 1.697 0.516129032258065 3.468 3.354 3.153 2.664 2.389 1.673

171 0.548387096774194 3.307 3.18 3.096 2.454 2.254 1.585 0.580645161290323 3.203 3.16 2.828 2.41 2.252 1.544 0.612903225806452 3.134 3.016 2.644 2.41 2.24 1.477 0.645161290322581 3.098 2.962 2.613 2.344 2.236 1.428 0.67741935483871 3.065 2.949 2.61 2.28 2.212 1.426 0.709677419354839 2.832 2.737 2.549 2.093 1.936 1.38 0.741935483870968 2.689 2.56 2.354 1.93 1.866 1.36 0.774193548387097 2.648 2.545 2.148 1.826 1.82 1.36 0.806451612903226 2.593 2.469 2.09 1.818 1.717 1.345 0.838709677419355 2.421 2.343 2.072 1.802 1.691 1.326 0.870967741935484 2.282 2.172 1.999 1.744 1.64 1.267 0.903225806451613 2.086 2.067 1.886 1.743 1.637 1.258 0.935483870967742 1.901 1.805 1.63 1.285 1.13 0.9553 0.967741935483871 1.577 1.507 1.313 1.159 1.083 0.9064

0.1 8.7397 8.2977 7.121 5.287 4.639 2.6489 Average of yearly averages: 1.78492333333333

Inputs generated by pe5.pl - Novemeber 2006

Data used for this run: Output File: pcxyMSCornAr Metfile: w03940.dvf PRZM scenario: MScornSTD.txt EXAMS environment file: pond298.exv Chemical Name: picoxystrobin Description Variable Name Value Units Comments Molecular weight mwt 367.3 g/mol Henry's Law Const. henry 6.6E-9 atm-m^3/mol Vapor Pressure vapr 4.14E-8 torr Solubility sol 3 mg/L Kd Kd mg/L Koc Koc 799 mg/L Photolysis half-life kdp 28.9 days Half-life Aerobic Aquatic Metabolism kbacw 43.8 days Halfife Anaerobic Aquatic Metabolism kbacs 250 days Halfife Aerobic Soil Metabolism asm 60.5 days Halfife Hydrolysis: pH 7 0 days Half-life Method: CAM 2 integer See PRZM manual Incorporation Depth: DEPI 0 cm Application Rate: TAPP 0.073 kg/ha Application Efficiency: APPEFF 0.95 fraction Spray Drift DRFT 0.05 fraction of application rate applied to pond Application Date Date 26-05 dd/mm or dd/mmm or dd-mm or dd-mmm Interval 1 interval 44 days Set to 0 or delete line for single app. app. rate 1 apprate 0.218 kg/ha Interval 2 interval 7 days Set to 0 or delete line for single app. app. rate 2 apprate 0.218 kg/ha Interval 3 interval 7 days Set to 0 or delete line for single app. app. rate 3 apprate 0.146 kg/ha Record 17: FILTRA IPSCND 1 UPTKF

172 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)

stored as pcxyMSsoybeanG.out Chemical: picoxystrobin PRZM environment: MSsoybeanSTD.txt modified Tueday, 29 May 2007 at 13:58:06 EXAMS environment: pond298.exv modified Thuday, 29 August 2002 at 16:33:30 Metfile: w03940.dvf modified Wedday, 3 July 2002 at 09:05:46 Water segment concentrations (ppb)

Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 1961 2.16 2.053 1.691 1.454 1.363 0.5896 1962 4.317 4.149 3.775 3.092 2.566 1.025 1963 2.369 2.247 1.836 1.387 1.383 0.7853 1964 6.613 6.306 5.17 3.72 3.143 1.308 1965 1.284 1.236 1.091 0.8855 0.7725 0.5398 1966 5.119 4.961 4.35 3.543 3.072 1.288 1967 7.132 6.825 6.023 4.852 4.074 1.787 1968 3.743 3.613 3.3 2.707 2.279 1.151 1969 4.095 3.923 3.52 2.63 2.18 0.9815 1970 2.351 2.241 1.868 1.489 1.281 0.6489 1971 6.882 6.579 5.682 4.756 3.967 1.539 1972 3.104 2.96 2.803 2.098 1.766 0.859 1973 4.567 4.362 3.976 3.476 2.881 1.138 1974 4.352 4.192 3.877 3.183 2.848 1.251 1975 4.927 4.687 4.107 3.186 2.656 1.199 1976 4.803 4.588 4.202 3.331 2.824 1.272 1977 2.935 2.814 2.526 1.918 1.652 0.8787 1978 4.17 3.98 3.753 2.844 2.404 1.023 1979 9.293 8.889 7.882 7.188 6.341 2.696 1980 11.2 10.76 9.437 8.182 6.886 2.821 1981 3.963 3.792 3.526 2.812 2.388 1.297 1982 5.204 4.98 4.684 3.476 3.181 1.45 1983 9.095 8.768 7.427 5.673 5.209 2.231 1984 3.79 3.624 3.096 2.426 2.134 1.158 1985 1.428 1.373 1.188 0.9223 0.8163 0.5387 1986 4.466 4.236 3.527 2.533 2.09 0.8948 1987 2.165 2.059 1.771 1.525 1.421 0.7289 1988 2.84 2.717 2.339 1.673 1.381 0.6928 1989 6.04 5.759 5.05 4.325 3.639 1.488 1990 4.677 4.463 3.803 3.089 2.584 1.189

Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly 0.032258064516129 11.2 10.76 9.437 8.182 6.886 2.821 0.0645161290322581 9.293 8.889 7.882 7.188 6.341 2.696 0.0967741935483871 9.095 8.768 7.427 5.673 5.209 2.231 0.129032258064516 7.132 6.825 6.023 4.852 4.074 1.787 0.161290322580645 6.882 6.579 5.682 4.756 3.967 1.539

173 0.193548387096774 6.613 6.306 5.17 4.325 3.639 1.488 0.225806451612903 6.04 5.759 5.05 3.72 3.181 1.45 0.258064516129032 5.204 4.98 4.684 3.543 3.143 1.308 0.290322580645161 5.119 4.961 4.35 3.476 3.072 1.297 0.32258064516129 4.927 4.687 4.202 3.476 2.881 1.288 0.354838709677419 4.803 4.588 4.107 3.331 2.848 1.272 0.387096774193548 4.677 4.463 3.976 3.186 2.824 1.251 0.419354838709677 4.567 4.362 3.877 3.183 2.656 1.199 0.451612903225806 4.466 4.236 3.803 3.092 2.584 1.189 0.483870967741936 4.352 4.192 3.775 3.089 2.566 1.158 0.516129032258065 4.317 4.149 3.753 2.844 2.404 1.151 0.548387096774194 4.17 3.98 3.527 2.812 2.388 1.138 0.580645161290323 4.095 3.923 3.526 2.707 2.279 1.025 0.612903225806452 3.963 3.792 3.52 2.63 2.18 1.023 0.645161290322581 3.79 3.624 3.3 2.533 2.134 0.9815 0.67741935483871 3.743 3.613 3.096 2.426 2.09 0.8948 0.709677419354839 3.104 2.96 2.803 2.098 1.766 0.8787 0.741935483870968 2.935 2.814 2.526 1.918 1.652 0.859 0.774193548387097 2.84 2.717 2.339 1.673 1.421 0.7853 0.806451612903226 2.369 2.247 1.868 1.525 1.383 0.7289 0.838709677419355 2.351 2.241 1.836 1.489 1.381 0.6928 0.870967741935484 2.165 2.059 1.771 1.454 1.363 0.6489 0.903225806451613 2.16 2.053 1.691 1.387 1.281 0.5896 0.935483870967742 1.428 1.373 1.188 0.9223 0.8163 0.5398 0.967741935483871 1.284 1.236 1.091 0.8855 0.7725 0.5387

0.1 8.8987 8.5737 7.2866 5.5909 5.0955 2.1866 Average of yearly averages: 1.21496666666667

Inputs generated by pe5.pl - Novemeber 2006

Data used for this run: Output File: pcxyMSsoybeanG Metfile: w03940.dvf PRZM scenario: MSsoybeanSTD.txt EXAMS environment file: pond298.exv Chemical Name: picoxystrobin Description Variable Name Value Units Comments Molecular weight mwt 367.3 g/mol Henry's Law Const. henry 6.6E-9 atm-m^3/mol Vapor Pressure vapr 4.14E-8 torr Solubility sol 3 mg/L Kd Kd mg/L Koc Koc 799 mg/L Photolysis half-life kdp 28.9 days Half-life Aerobic Aquatic Metabolism kbacw 43.8 days Halfife Anaerobic Aquatic Metabolism kbacs 250 days Halfife Aerobic Soil Metabolism asm 60.5 days Halfife Hydrolysis: pH 7 0 days Half-life Method: CAM 2 integer See PRZM manual Incorporation Depth: DEPI 0 cm Application Rate: TAPP 0.218 kg/ha Application Efficiency: APPEFF 0.99 fraction Spray Drift DRFT 0.03 fraction of application rate applied to pond Application Date Date 11-04 dd/mm or dd/mmm or dd-mm or dd-mmm Interval 1 interval 7 days Set to 0 or delete line for single app.

174 app. rate 1 apprate 0.218 kg/ha Interval 2 interval 7 days Set to 0 or delete line for single app. app. rate 2 apprate 0.218 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)

stored as pcxyMSsoybeanAr.out Chemical: picoxystrobin PRZM environment: MSsoybeanSTD.txt modified Tueday, 29 May 2007 at 13:58:06 EXAMS environment: pond298.exv modified Thuday, 29 August 2002 at 16:33:30 Metfile: w03940.dvf modified Wedday, 3 July 2002 at 09:05:46 Water segment concentrations (ppb)

Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 1961 2.511 2.389 1.975 1.652 1.544 0.6751 1962 4.743 4.557 4.101 3.344 2.775 1.107 1963 2.418 2.296 2.069 1.656 1.609 0.8757 1964 6.95 6.627 5.444 3.936 3.319 1.377 1965 1.852 1.777 1.538 1.223 1.052 0.6445 1966 5.272 5.109 4.485 3.765 3.259 1.371 1967 7.348 7.032 6.188 4.972 4.171 1.852 1968 4.024 3.89 3.528 2.941 2.503 1.24 1969 4.396 4.204 3.871 2.907 2.409 1.072 1970 2.782 2.652 2.215 1.801 1.542 0.7496 1971 7.041 6.732 5.9 4.939 4.116 1.608 1972 3.508 3.346 3.112 2.357 2.002 0.9502 1973 4.861 4.644 4.317 3.717 3.077 1.218 1974 4.8 4.607 4.148 3.431 3.047 1.33 1975 5.217 4.965 4.369 3.376 2.837 1.281 1976 5.026 4.805 4.381 3.489 2.976 1.357 1977 3.446 3.301 2.923 2.213 1.887 0.9704 1978 4.383 4.186 3.984 3.082 2.615 1.108 1979 9.43 9.02 7.977 7.284 6.41 2.721 1980 11.38 10.94 9.564 8.241 6.931 2.836 1981 4.163 3.993 3.689 2.921 2.539 1.369 1982 5.57 5.335 4.991 3.699 3.352 1.517 1983 9.091 8.771 7.44 5.833 5.324 2.274 1984 4.166 3.983 3.396 2.711 2.365 1.245 1985 1.981 1.913 1.636 1.266 1.1 0.6464 1986 4.583 4.351 3.643 2.656 2.222 0.9855 1987 2.483 2.364 2.032 1.754 1.656 0.8258 1988 3.351 3.207 2.743 1.986 1.635 0.7924 1989 6.173 5.889 5.256 4.448 3.737 1.559 1990 4.918 4.694 4.001 3.305 2.774 1.269

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

175 0.032258064516129 11.38 10.94 9.564 8.241 6.931 2.836 0.0645161290322581 9.43 9.02 7.977 7.284 6.41 2.721 0.0967741935483871 9.091 8.771 7.44 5.833 5.324 2.274 0.129032258064516 7.348 7.032 6.188 4.972 4.171 1.852 0.161290322580645 7.041 6.732 5.9 4.939 4.116 1.608 0.193548387096774 6.95 6.627 5.444 4.448 3.737 1.559 0.225806451612903 6.173 5.889 5.256 3.936 3.352 1.517 0.258064516129032 5.57 5.335 4.991 3.765 3.319 1.377 0.290322580645161 5.272 5.109 4.485 3.717 3.259 1.371 0.32258064516129 5.217 4.965 4.381 3.699 3.077 1.369 0.354838709677419 5.026 4.805 4.369 3.489 3.047 1.357 0.387096774193548 4.918 4.694 4.317 3.431 2.976 1.33 0.419354838709677 4.861 4.644 4.148 3.376 2.837 1.281 0.451612903225806 4.8 4.607 4.101 3.344 2.775 1.269 0.483870967741936 4.743 4.557 4.001 3.305 2.774 1.245 0.516129032258065 4.583 4.351 3.984 3.082 2.615 1.24 0.548387096774194 4.396 4.204 3.871 2.941 2.539 1.218 0.580645161290323 4.383 4.186 3.689 2.921 2.503 1.108 0.612903225806452 4.166 3.993 3.643 2.907 2.409 1.107 0.645161290322581 4.163 3.983 3.528 2.711 2.365 1.072 0.67741935483871 4.024 3.89 3.396 2.656 2.222 0.9855 0.709677419354839 3.508 3.346 3.112 2.357 2.002 0.9704 0.741935483870968 3.446 3.301 2.923 2.213 1.887 0.9502 0.774193548387097 3.351 3.207 2.743 1.986 1.656 0.8757 0.806451612903226 2.782 2.652 2.215 1.801 1.635 0.8258 0.838709677419355 2.511 2.389 2.069 1.754 1.609 0.7924 0.870967741935484 2.483 2.364 2.032 1.656 1.544 0.7496 0.903225806451613 2.418 2.296 1.975 1.652 1.542 0.6751 0.935483870967742 1.981 1.913 1.636 1.266 1.1 0.6464 0.967741935483871 1.852 1.777 1.538 1.223 1.052 0.6445

0.1 8.9167 8.5971 7.3148 5.7469 5.2087 2.2318 Average of yearly averages: 1.29422

Inputs generated by pe5.pl - Novemeber 2006

Data used for this run: Output File: pcxyMSsoybean Metfile: w03940.dvf PRZM scenario: MSsoybeanSTD.txt EXAMS environment file: pond298.exv Chemical Name: picoxystrobin Description Variable Name Value Units Comments Molecular weight mwt 367.3 g/mol Henry's Law Const. henry 6.6E-9 atm-m^3/mol Vapor Pressure vapr 4.14E-8 torr Solubility sol 3 mg/L Kd Kd mg/L Koc Koc 799 mg/L Photolysis half-life kdp 28.9 days Half-life Aerobic Aquatic Metabolism kbacw 43.8 days Halfife Anaerobic Aquatic Metabolism kbacs 250 days Halfife Aerobic Soil Metabolism asm 60.5 days Halfife Hydrolysis: pH 7 0 days Half-life Method: CAM 2 integer See PRZM manual Incorporation Depth: DEPI 0 cm

176 Application Rate: TAPP 0.218 kg/ha Application Efficiency: APPEFF 0.95 fraction Spray Drift DRFT 0.05 fraction of application rate applied to pond Application Date Date 11-04 dd/mm or dd/mmm or dd-mm or dd-mmm Interval 1 interval 7 days Set to 0 or delete line for single app. app. rate 1 apprate 0.218 kg/ha Interval 2 interval 7 days Set to 0 or delete line for single app. app. rate 2 apprate 0.218 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)

stored as pcxyMIbeansAr.out Chemical: picoxystrobin PRZM environment: MIbeansSTD.txt modified Tueday, 29 May 2007 at 13:56:44 EXAMS environment: pond298.exv modified Thuday, 29 August 2002 at 16:33:30 Metfile: w14826.dvf modified Wedday, 3 July 2002 at 09:05:38 Water segment concentrations (ppb)

Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 1961 2.142 2.051 1.84 1.536 1.391 0.5772 1962 1.494 1.438 1.291 1.143 1.037 0.8342 1963 1.363 1.305 1.131 0.9713 0.918 0.6706 1964 2.267 2.17 1.829 1.454 1.322 0.8001 1965 2.079 1.998 1.72 1.447 1.312 0.9474 1966 1.516 1.456 1.308 1.084 1.003 0.8295 1967 1.53 1.472 1.326 1.105 1.04 0.7761 1968 3.715 3.556 3.01 2.332 2.066 1.221 1969 3.663 3.51 3.197 2.59 2.244 1.497 1970 2.931 2.81 2.394 1.952 1.816 1.339 1971 2.379 2.291 2.03 1.73 1.545 1.163 1972 3.241 3.101 2.628 2.123 1.959 1.283 1973 1.77 1.705 1.478 1.325 1.282 1.125 1974 1.649 1.585 1.363 1.17 1.063 0.9053 1975 3.908 3.729 3.543 2.91 2.584 1.293 1976 2.676 2.57 2.253 1.797 1.599 1.387 1977 2.019 1.932 1.674 1.4 1.258 1.02 1978 1.462 1.404 1.203 1.044 1.01 0.8298 1979 2.106 2.02 1.883 1.572 1.383 0.8772 1980 3.215 3.069 2.642 2.222 2.023 1.193 1981 2.176 2.088 1.864 1.7 1.632 1.326 1982 1.777 1.711 1.568 1.374 1.31 1.132 1983 2.104 2.008 1.727 1.498 1.377 1.023 1984 1.771 1.703 1.547 1.38 1.279 0.9585 1985 2.945 2.837 2.517 2.124 1.964 1.159 1986 2.812 2.736 2.58 2.309 2.192 1.502 1987 2.061 2.001 1.851 1.639 1.542 1.384

177 1988 1.666 1.621 1.488 1.431 1.347 1.132 1989 2.051 1.999 1.809 1.688 1.61 1.162 1990 1.608 1.548 1.364 1.175 1.127 1.035

Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly 0.032258064516129 3.908 3.729 3.543 2.91 2.584 1.502 0.0645161290322581 3.715 3.556 3.197 2.59 2.244 1.497 0.0967741935483871 3.663 3.51 3.01 2.332 2.192 1.387 0.129032258064516 3.241 3.101 2.642 2.309 2.066 1.384 0.161290322580645 3.215 3.069 2.628 2.222 2.023 1.339 0.193548387096774 2.945 2.837 2.58 2.124 1.964 1.326 0.225806451612903 2.931 2.81 2.517 2.123 1.959 1.293 0.258064516129032 2.812 2.736 2.394 1.952 1.816 1.283 0.290322580645161 2.676 2.57 2.253 1.797 1.632 1.221 0.32258064516129 2.379 2.291 2.03 1.73 1.61 1.193 0.354838709677419 2.267 2.17 1.883 1.7 1.599 1.163 0.387096774193548 2.176 2.088 1.864 1.688 1.545 1.162 0.419354838709677 2.142 2.051 1.851 1.639 1.542 1.159 0.451612903225806 2.106 2.02 1.84 1.572 1.391 1.132 0.483870967741936 2.104 2.008 1.829 1.536 1.383 1.132 0.516129032258065 2.079 2.001 1.809 1.498 1.377 1.125 0.548387096774194 2.061 1.999 1.727 1.454 1.347 1.035 0.580645161290323 2.051 1.998 1.72 1.447 1.322 1.023 0.612903225806452 2.019 1.932 1.674 1.431 1.312 1.02 0.645161290322581 1.777 1.711 1.568 1.4 1.31 0.9585 0.67741935483871 1.771 1.705 1.547 1.38 1.282 0.9474 0.709677419354839 1.77 1.703 1.488 1.374 1.279 0.9053 0.741935483870968 1.666 1.621 1.478 1.325 1.258 0.8772 0.774193548387097 1.649 1.585 1.364 1.175 1.127 0.8342 0.806451612903226 1.608 1.548 1.363 1.17 1.063 0.8298 0.838709677419355 1.53 1.472 1.326 1.143 1.04 0.8295 0.870967741935484 1.516 1.456 1.308 1.105 1.037 0.8001 0.903225806451613 1.494 1.438 1.291 1.084 1.01 0.7761 0.935483870967742 1.462 1.404 1.203 1.044 1.003 0.6706 0.967741935483871 1.363 1.305 1.131 0.9713 0.918 0.5772

0.1 3.6208 3.4691 2.9732 2.3297 2.1794 1.3867 Average of yearly averages: 1.07939666666667

Inputs generated by pe5.pl - Novemeber 2006

Data used for this run: Output File: pcxyMIbeansAr Metfile: w14826.dvf PRZM scenario: MIbeansSTD.txt EXAMS environment file: pond298.exv Chemical Name: picoxystrobin Description Variable Name Value Units Comments Molecular weight mwt 367.3 g/mol Henry's Law Const. henry 6.6E-9 atm-m^3/mol Vapor Pressure vapr 4.14E-8 torr Solubility sol 3 mg/L Kd Kd mg/L Koc Koc 799 mg/L Photolysis half-life kdp 28.9 days Half-life

178 Aerobic Aquatic Metabolism kbacw 43.8 days Halfife Anaerobic Aquatic Metabolism kbacs 250 days Halfife Aerobic Soil Metabolism asm 60.5 days Halfife Hydrolysis: pH 7 0 days Half-life Method: CAM 2 integer See PRZM manual Incorporation Depth: DEPI 0 cm Application Rate: TAPP 0.218 kg/ha Application Efficiency: APPEFF 0.95 fraction Spray Drift DRFT 0.05 fraction of application rate applied to pond Application Date Date 26-06 dd/mm or dd/mmm or dd-mm or dd-mmm Interval 1 interval 7 days Set to 0 or delete line for single app. app. rate 1 apprate 0.218 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)

stored as pcxyMIbeansGr.out Chemical: picoxystrobin PRZM environment: MIbeansSTD.txt modified Tueday, 29 May 2007 at 13:56:44 EXAMS environment: pond298.exv modified Thuday, 29 August 2002 at 16:33:30 Metfile: w14826.dvf modified Wedday, 3 July 2002 at 09:05:38 Water segment concentrations (ppb)

Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 1961 1.955 1.867 1.659 1.371 1.238 0.455 1962 0.8648 0.8376 0.8002 0.7733 0.7561 0.6209 1963 0.6408 0.6202 0.5785 0.5236 0.4856 0.4212 1964 1.576 1.51 1.274 1.016 0.9435 0.5537 1965 1.75 1.676 1.423 1.189 1.069 0.6994 1966 0.7823 0.7778 0.7607 0.73 0.7103 0.5744 1967 0.7664 0.7422 0.7077 0.6647 0.6439 0.5067 1968 3.437 3.283 2.755 2.101 1.846 0.9737 1969 2.858 2.742 2.564 2.132 1.853 1.266 1970 2.234 2.143 1.832 1.502 1.432 1.109 1971 1.74 1.678 1.506 1.239 1.127 0.9268 1972 2.639 2.523 2.133 1.746 1.633 1.05 1973 1.232 1.225 1.198 1.149 1.111 0.8888 1974 0.9427 0.9341 0.9056 0.872 0.8497 0.6653 1975 3.699 3.521 3.357 2.729 2.409 1.067 1976 1.836 1.781 1.61 1.429 1.391 1.169 1977 1.143 1.101 1.014 0.9034 0.8802 0.7884 1978 1.004 0.9831 0.8944 0.7633 0.7094 0.5888 1979 1.398 1.343 1.205 1.071 0.9557 0.6346 1980 2.49 2.377 2.063 1.803 1.669 0.9586 1981 1.789 1.751 1.631 1.484 1.424 1.095 1982 1.153 1.146 1.127 1.086 1.06 0.8937

179 1983 1.266 1.227 1.119 1.037 0.9908 0.7996 1984 1.241 1.194 1.084 0.9626 0.897 0.7347 1985 2.748 2.641 2.322 1.919 1.77 0.9357 1986 2.655 2.58 2.417 2.13 2.008 1.288 1987 1.859 1.8 1.654 1.43 1.377 1.175 1988 1.305 1.257 1.118 1.032 1.024 0.9196 1989 1.822 1.771 1.59 1.415 1.343 0.9386 1990 1.052 1.034 0.9799 0.9464 0.9218 0.7982

Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly 0.032258064516129 3.699 3.521 3.357 2.729 2.409 1.288 0.0645161290322581 3.437 3.283 2.755 2.132 2.008 1.266 0.0967741935483871 2.858 2.742 2.564 2.13 1.853 1.175 0.129032258064516 2.748 2.641 2.417 2.101 1.846 1.169 0.161290322580645 2.655 2.58 2.322 1.919 1.77 1.109 0.193548387096774 2.639 2.523 2.133 1.803 1.669 1.095 0.225806451612903 2.49 2.377 2.063 1.746 1.633 1.067 0.258064516129032 2.234 2.143 1.832 1.502 1.432 1.05 0.290322580645161 1.955 1.867 1.659 1.484 1.424 0.9737 0.32258064516129 1.859 1.8 1.654 1.43 1.391 0.9586 0.354838709677419 1.836 1.781 1.631 1.429 1.377 0.9386 0.387096774193548 1.822 1.771 1.61 1.415 1.343 0.9357 0.419354838709677 1.789 1.751 1.59 1.371 1.238 0.9268 0.451612903225806 1.75 1.678 1.506 1.239 1.127 0.9196 0.483870967741936 1.74 1.676 1.423 1.189 1.111 0.8937 0.516129032258065 1.576 1.51 1.274 1.149 1.069 0.8888 0.548387096774194 1.398 1.343 1.205 1.086 1.06 0.7996 0.580645161290323 1.305 1.257 1.198 1.071 1.024 0.7982 0.612903225806452 1.266 1.227 1.127 1.037 0.9908 0.7884 0.645161290322581 1.241 1.225 1.119 1.032 0.9557 0.7347 0.67741935483871 1.232 1.194 1.118 1.016 0.9435 0.6994 0.709677419354839 1.153 1.146 1.084 0.9626 0.9218 0.6653 0.741935483870968 1.143 1.101 1.014 0.9464 0.897 0.6346 0.774193548387097 1.052 1.034 0.9799 0.9034 0.8802 0.6209 0.806451612903226 1.004 0.9831 0.9056 0.872 0.8497 0.5888 0.838709677419355 0.9427 0.9341 0.8944 0.7733 0.7561 0.5744 0.870967741935484 0.8648 0.8376 0.8002 0.7633 0.7103 0.5537 0.903225806451613 0.7823 0.7778 0.7607 0.73 0.7094 0.5067 0.935483870967742 0.7664 0.7422 0.7077 0.6647 0.6439 0.455 0.967741935483871 0.6408 0.6202 0.5785 0.5236 0.4856 0.4212

0.1 2.847 2.7319 2.5493 2.1271 1.8523 1.1744 Average of yearly averages: 0.849846666666667

Inputs generated by pe5.pl - Novemeber 2006

Data used for this run: Output File: pcxyMIbeansGr Metfile: w14826.dvf PRZM scenario: MIbeansSTD.txt EXAMS environment file: pond298.exv Chemical Name: picoxystrobin Description Variable Name Value Units Comments Molecular weight mwt 367.3 g/mol Henry's Law Const. henry 6.6E-9 atm-m^3/mol

180 Vapor Pressure vapr 4.14E-8 torr Solubility sol 3 mg/L Kd Kd mg/L Koc Koc 799 mg/L Photolysis half-life kdp 28.9 days Half-life Aerobic Aquatic Metabolism kbacw 43.8 days Halfife Anaerobic Aquatic Metabolism kbacs 250 days Halfife Aerobic Soil Metabolism asm 60.5 days Halfife Hydrolysis: pH 7 0 days Half-life Method: CAM 2 integer See PRZM manual Incorporation Depth: DEPI 0 cm Application Rate: TAPP 0.218 kg/ha Application Efficiency: APPEFF 0.99 fraction Spray Drift DRFT 0.01 fraction of application rate applied to pond Application Date Date 26-06 dd/mm or dd/mmm or dd-mm or dd-mmm Interval 1 interval 7 days Set to 0 or delete line for single app. app. rate 1 apprate 0.218 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)

Pore Water EECs stored as pcxyMSsoybeanPoreben.out Chemical: picoxystrobin PRZM environment: MSsoybeanSTD.txt modified Tueday, 29 May 2007 at 13:58:06 EXAMS environment: pond298.exv modified Thuday, 29 August 2002 at 16:33:30 Metfile: w03940.dvf modified Wedday, 3 July 2002 at 09:05:46 Benthic segment concentrations (ppb)

181 Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 1961 1.029 1.029 1.024 0.9938 0.9542 0.5075 1962 1.909 1.909 1.898 1.83 1.738 0.9668 1963 1.166 1.166 1.158 1.108 1.08 0.7643 1964 2.274 2.273 2.259 2.174 2.075 1.175 1965 0.8495 0.8492 0.8454 0.8187 0.7843 0.6213 1966 2.201 2.201 2.189 2.098 1.993 1.124 1967 2.904 2.903 2.888 2.792 2.67 1.592 1968 1.91 1.91 1.898 1.82 1.73 1.178 1969 1.703 1.702 1.692 1.626 1.547 0.9507 1970 1.148 1.148 1.142 1.102 1.051 0.6892 1971 2.752 2.752 2.736 2.625 2.491 1.322 1972 1.522 1.522 1.514 1.456 1.385 0.902 1973 2.108 2.107 2.094 2.002 1.894 1.045 1974 2.037 2.036 2.026 1.966 1.9 1.157 1975 1.991 1.991 1.985 1.922 1.838 1.129 1976 2.102 2.102 2.091 2.022 1.929 1.168 1977 1.379 1.378 1.371 1.335 1.288 0.9029 1978 1.839 1.839 1.828 1.748 1.654 0.9482 1979 4.293 4.292 4.27 4.146 4.009 2.264 1980 4.939 4.938 4.905 4.694 4.449 2.552 1981 1.9 1.9 1.887 1.853 1.781 1.293 1982 2.175 2.174 2.16 2.115 2.072 1.305 1983 3.788 3.787 3.767 3.611 3.419 1.95 1984 1.853 1.852 1.842 1.78 1.707 1.219 1985 0.843 0.8426 0.8374 0.8106 0.7825 0.6046 1986 1.595 1.594 1.584 1.517 1.438 0.8112 1987 1.182 1.182 1.174 1.124 1.092 0.7407 1988 1.179 1.178 1.171 1.121 1.069 0.6884 1989 2.584 2.584 2.569 2.473 2.36 1.309 1990 2.052 2.051 2.038 1.953 1.852 1.165

Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly 0.032258064516129 4.939 4.938 4.905 4.694 4.449 2.552 0.0645161290322581 4.293 4.292 4.27 4.146 4.009 2.264 0.0967741935483871 3.788 3.787 3.767 3.611 3.419 1.95 0.129032258064516 2.904 2.903 2.888 2.792 2.67 1.592 0.161290322580645 2.752 2.752 2.736 2.625 2.491 1.322 0.193548387096774 2.584 2.584 2.569 2.473 2.36 1.309 0.225806451612903 2.274 2.273 2.259 2.174 2.075 1.305 0.258064516129032 2.201 2.201 2.189 2.115 2.072 1.293 0.290322580645161 2.175 2.174 2.16 2.098 1.993 1.219 0.32258064516129 2.108 2.107 2.094 2.022 1.929 1.178 0.354838709677419 2.102 2.102 2.091 2.002 1.9 1.175 0.387096774193548 2.052 2.051 2.038 1.966 1.894 1.168 0.419354838709677 2.037 2.036 2.026 1.953 1.852 1.165 0.451612903225806 1.991 1.991 1.985 1.922 1.838 1.157 0.483870967741936 1.91 1.91 1.898 1.853 1.781 1.129 0.516129032258065 1.909 1.909 1.898 1.83 1.738 1.124 0.548387096774194 1.9 1.9 1.887 1.82 1.73 1.045 0.580645161290323 1.853 1.852 1.842 1.78 1.707 0.9668 0.612903225806452 1.839 1.839 1.828 1.748 1.654 0.9507 0.645161290322581 1.703 1.702 1.692 1.626 1.547 0.9482 0.67741935483871 1.595 1.594 1.584 1.517 1.438 0.9029 0.709677419354839 1.522 1.522 1.514 1.456 1.385 0.902

182 0.741935483870968 1.379 1.378 1.371 1.335 1.288 0.8112 0.774193548387097 1.182 1.182 1.174 1.124 1.092 0.7643 0.806451612903226 1.179 1.178 1.171 1.121 1.08 0.7407 0.838709677419355 1.166 1.166 1.158 1.108 1.069 0.6892 0.870967741935484 1.148 1.148 1.142 1.102 1.051 0.6884 0.903225806451613 1.029 1.029 1.024 0.9938 0.9542 0.6213 0.935483870967742 0.8495 0.8492 0.8454 0.8187 0.7843 0.6046 0.967741935483871 0.843 0.8426 0.8374 0.8106 0.7825 0.5075

0.1 3.6996 3.6986 3.6791 3.5291 3.3441 1.9142 Average of yearly averages: 1.13482666666667

Inputs generated by pe5.pl - Novemeber 2006

Data used for this run: Output File: pcxyMSsoybeanPore Metfile: w03940.dvf PRZM scenario: MSsoybeanSTD.txt EXAMS environment file: pond298.exv Chemical Name: picoxystrobin Description Variable Name Value Units Comments Molecular weight mwt 367.3 g/mol Henry's Law Const. henry 6.6E-9 atm-m^3/mol Vapor Pressure vapr 4.14E-8 torr Solubility sol 3 mg/L Kd Kd mg/L Koc Koc 799 mg/L Photolysis half-life kdp 28.9 days Half-life Aerobic Aquatic Metabolism kbacw 43.8 days Halfife Anaerobic Aquatic Metabolism kbacs 250 days Halfife Aerobic Soil Metabolism asm 60.5 days Halfife Hydrolysis: pH 7 0 days Half-life Method: CAM 2 integer See PRZM manual Incorporation Depth: DEPI 0 cm Application Rate: TAPP 0.218 kg/ha Application Efficiency: APPEFF 0.95 fraction Spray Drift DRFT 0.05 fraction of application rate applied to pond Application Date Date 11-04 dd/mm or dd/mmm or dd-mm or dd-mmm Interval 1 interval 7 days Set to 0 or delete line for single app. app. rate 1 apprate 0.218 kg/ha Interval 2 interval 7 days Set to 0 or delete line for single app. app. rate 2 apprate 0.218 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)

183 Appendix G. TerrPlant

Table 1. Chemical Identity. Chemical Name Picoxystrobin PC code 129200 Use all Application Method Ground Application Form Spray Solubility in Water (ppm) 3.1

Table 2. Input parameters used to derive EECs. Input Parameter Symbol Value Units Application Rate A 0.195 lb ai/A Incorporation I 1 none Runoff Fraction R 0.01 none Drift Fraction D 0.01 none

Table 3. EECs for Picoxystrobin. Units in lb ai/A. Description Equation EEC Runoff to dry areas (A/I)*R 0.00195 Runoff to semi-aquatic areas (A/I)*R*10 0.0195 Spray drift A*D 0.00195 Total for dry areas ((A/I)*R)+(A*D) 0.0039 Total for semi-aquatic areas ((A/I)*R*10)+(A*D) 0.02145

Table 4. Plant survival and growth data used for RQ derivation. Units are in lb ai/A. Seedling Emergence Vegetative Vigor Plant type EC25 NOAEC EC25 NOAEC Monocot 0.45 0.45 0.45 0.45 Dicot 0.45 0.45

Table 5. RQ values for plants in dry and semi-aquatic areas exposed to Picoxystrobin through runoff and/or spray drift.* Plant Type Listed Status Dry Semi-Aquatic Spray Drift Monocot non-listed <0.1 <0.1 <0.1 Monocot listed <0.1 <0.1 <0.1 Dicot non-listed <0.1 <0.1 <0.1 Dicot listed #DIV/0! #DIV/0! #DIV/0! *If RQ > 1.0, the LOC is exceeded, resulting in potential for risk to that plant group.

184 Table 1. Chemical Identity. Chemical Name Picoxystrobin PC code 129200 Use all Application Method Aerial Application Form Spray Solubility in Water (ppm) 3.1

Table 2. Input parameters used to derive EECs. Input Parameter Symbol Value Units Application Rate A 0.195 lb ai/A Incorporation I 1 none Runoff Fraction R 0.01 none Drift Fraction D 0.05 none

Table 3. EECs for Picoxystrobin. Units in lb ai/A. Description Equation EEC Runoff to dry areas (A/I)*R 0.00195 Runoff to semi-aquatic areas (A/I)*R*10 0.0195 Spray drift A*D 0.00975 Total for dry areas ((A/I)*R)+(A*D) 0.0117 Total for semi-aquatic areas ((A/I)*R*10)+(A*D) 0.02925

Table 4. Plant survival and growth data used for RQ derivation. Units are in lb ai/A. Seedling Emergence Vegetative Vigor Plant type EC25 NOAEC EC25 NOAEC Monocot 0.45 0.45 0.45 0.45 Dicot 0.45 0.45

Table 5. RQ values for plants in dry and semi-aquatic areas exposed to Picoxystrobin through runoff and/or spray drift.* Plant Type Listed Status Dry Semi-Aquatic Spray Drift Monocot non-listed <0.1 <0.1 <0.1 Monocot listed <0.1 <0.1 <0.1 Dicot non-listed <0.1 <0.1 <0.1 Dicot listed #DIV/0! #DIV/0! #DIV/0! *If RQ > 1.0, the LOC is exceeded, resulting in potential for risk to that plant group.

185 Appendix H. KABAM

Table H1. Chemical characteristics of Picoxystrobin. Characteristic Value Comments/Guidance

Pesticide Name Picoxystrobin Required input

Required input Log KOW 3.6 Enter value from acceptable or supplemental study submitted by registrant or available in scientific literature. No input necessary. This value is calculated automatically KOW 3981 from the Log KOW value entered above.

Required input K (L/kg Input value used in PRZM/EXAMS to derive EECs. Follow OC 799 OC) input parameter guidance for deriving this parameter value (USEPA 2002). Time to steady state No input necessary. This value is calculated automatically 3 (TS; days) from the Log KOW value entered above. Required input Enter value generated by PRZM/EXAMS benthic file. PRZM/EXAMS EEC represents the freely dissolved concentration of the pesticide in the pore water of the sediment. The appropriate averaging period of the EEC is dependent on the specific pesticide being modeled and is Pore water EEC 3.70 based on the time it takes for the chemical to reach (µg/L) steady state. Select the EEC generated by PRZM/EXAMS which has an averaging period closest to the time to steady state calculated above. In cases where the time to steady state exceeds 365 days, the user should select the EEC representing the average of yearly averages. The peak EEC should not be used. Required input Enter value generated by PRZM/EXAMS water column file. PRZM/EXAMS EEC represents the freely dissolved concentration of the pesticide in the water column. The Water Column EEC appropriate averaging period of the EEC is dependent on 8.92 (µg/L) the specific pesticide being modeled and is based on the time it takes for the chemical to reach steady state. The averaging period used for the water column EEC should be the same as the one selected for the pore water EEC (discussed above).

186 Table H2. Input parameters for rate constants. "calculated" indicates that model will calculate rate constant.

kD k1 k2 (kg - food/kg - kE k M* Trophic level (L/kg*d) (d-1) org/d) (d-1) (d-1) phytoplankton calculated calculated 0* 0* 0 zooplankton calculated calculated calculated calculated 0 benthic invertebrates calculated calculated calculated calculated 0 filter feeders calculated calculated calculated calculated 0 small fish calculated calculated calculated calculated 0 medium fish calculated calculated calculated calculated 0 large fish calculated calculated calculated calculated 0 * Default value is 0. k1 and k2 represent the uptake and elimination constants respectively, through respiration. kD and kE represent the uptake and elimination constants, respectively, through diet. kM represents the metabolism rate constant.

Table H3. Mammalian and avian toxicity data for Picoxystrobin. These are required inputs.

If selected species is "other," enter body Measure of weight (in Animal effect (units) Value Species kg) here.

Avian LD50 (mg/kg-bw) 486 other 0.014 LC50 (mg/kg- diet) 5200 mallard duck NOAEC (mg/kg- diet) 157 mallard duck Default value for all species is 1.15 (for chemical specific Mineau Scaling values, see Mineau et al. Factor 1.15 1996).

Mammalian LD50 (mg/kg-bw) 5000 laboratory rat LC50 (mg/kg- diet) N/A other Chronic laboratory rat Endpoint 50

units of chronic ppm endpoint* *ppm = mg/kg-diet

187

Table H4. Abiotic characteristics of the model aquatic ecosystem. Characteristic Value Guidance* Concentration of Particulate Organic 0.00E+00 Carbon (XPOC; kg OC/ L) When using EECs generated by PRZM/EXAMS, use a value of Concentration of “0” for both POC and DOC. Dissolved Organic 0.00E+00 Carbon (XDOC; kg OC/L)

Concentration of Default value is 5.0 mg O /L when using EECs generated by Dissolved Oxygen 5.0 2 PRZM/EXAMS. (COX; mg O2/L) Value is defined by the average water temperature of the Water Temperature (T; EXAMS pond when using EECs generated by PRZM/EXAMS. o 15 C) Model user should consult output file of EXAMS to define this value.

Concentration of -5 Default value is 3.00x10 kg/L when using EECs generated by Suspended Solids 3.00E-05 PRZM/EXAMS. (CSS; kg/L)

Sediment Organic Default value is 4.0% when using EECs generated by Carbon 4.0% PRZM/EXAMS. (OC; %)

*When using pesticide concentrations from monitoring data or mesocosm studies, consult Appendix B of the User’s Guide for specific guidance on selecting values for these parameters.

Table H5. Characteristics of aquatic biota of the model ecosystem.

Do organisms in trophic level respire Wet Weight some pore Trophic Level (kg) % lipids % NLOM % Water water? sediment* N/A 0.0% 4.0% 96.0% N/A phytoplankton N/A 2.0% 8.0% 90.0% no zooplankton 1.0E-07 3.0% 12.0% 85.0% no benthic invertebrates 1.0E-04 3.0% 21.0% 76.0% yes filter feeders 1.0E-03 2.0% 13.0% 85.0% yes small fish 1.0E-02 4.0% 23.0% 73.0% yes medium fish 1.0E-01 4.0% 23.0% 73.0% yes large fish 1.0E+00 4.0% 23.0% 73.0% no

188 *Note that sediment is not a trophic level. It is included in this table because it is consumed by aquatic organisms of the KABAM foodweb. N/A = not applicable

Table H6. Diets of aquatic biota of the model ecosystem. Diet for: Benthic Filter Small Medium Large Trophic level in diet Zoo plankton Invertebrates Feeder Fish Fish Fish sediment* 0.0% 34.0% 34.0% 0.0% 0.0% 0.0% phytoplankton 100.0% 33.0% 33.0% 0.0% 0.0% 0.0% zooplankton 33.0% 33.0% 50.0% 0.0% 0.0% benthic invertebrates 0.0% 50.0% 50.0% 0.0% filter feeders 0.0% 0.0% 0.0% small fish 50.0% 0.0% medium fish 100.0% Total 100.0% 100.0% 100.0% 100.0% 100.0% 100.0% *Note that sediment is not a trophic level. It is included in this table because it is consumed by aquatic organisms of the KABAM foodweb.

Table H7. Identification of mammals and birds feeding on aquatic biota of the model ecosystem. Body weight Mammal/Bird # Name (kg) Mammal 1 fog/water shrew 0.018 Mammal 2 rice rat/star-nosed mole 0.085 Mammal 3 small mink 0.45 Mammal 4 large mink 1.8 Mammal 5 small river otter 5 Mammal 6 large river otter 15 Bird 1 sandpipers 0.02 Bird 2 cranes 6.7 Bird 3 rails 0.07 Bird 4 herons 2.9 Bird 5 small osprey 1.25 Bird 6 white pelican 7.5

189 Table H8. Diets of mammals feeding on aquatic biota of the model ecosystem. Diet for: large fog/water rice rat/star- small large small river river Trophic level in diet shrew nosed mole mink mink otter otter phytoplankton 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% zooplankton 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% benthic invertebrates 100.0% 34.0% 0.0% 0.0% 0.0% 0.0% filter feeders 0.0% 33.0% 0.0% 0.0% 0.0% 0.0% small fish 0.0% 33.0% 0.0% 0.0% 0.0% 0.0% medium fish 0.0% 0.0% 100.0% 100.0% 100.0% 0.0% large fish 0.0% 0.0% 0.0% 0.0% 0.0% 100.0% Total 100.0% 100.0% 100.0% 100.0% 100.0% 100.0%

Table H9. Diets of birds feeding on aquatic biota of the model ecosystem. Diet for: small white Trophic level in diet sandpipers cranes rails herons osprey pelican phytoplankton 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% zooplankton 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% benthic invertebrates 33.0% 33.0% 50.0% 50.0% 0.0% 0.0% filter feeders 33.0% 33.0% 0.0% 0.0% 0.0% 0.0% small fish 34.0% 0.0% 50.0% 0.0% 0.0% 0.0% medium fish 0.0% 34.0% 0.0% 50.0% 100.0% 0.0% large fish 0.0% 0.0% 0.0% 0.0% 0.0% 100.0% Total 100.0% 100.0% 100.0% 100.0% 100.0% 100.0%

Table H10. Input parameters and calculations relevant to derivation of CB.

Phyto Zoo Benthic Filter Medium Parameter plankton plankton Invertebrates Feeders Small Fish Fish Large Fish Equation A1

CB 0.002369 0.00173915 0.001853 0.001223 0.002396 0.002414 0.00251

CBD 0.000000 0.00000236 0.000006 0.000004 0.000025 0.000047 0.000084

CBR 0.00236889 0.00173679 0.00184729 0.00121857 0.00237100 0.00236749 0.00242172

CS 0.000206

CWDP 0.00000646

CWTO 0.00001268 k1 693.704 41777.379 3723.413 1663.187 742.919 331.850 148.232 k2 3.613201 304.938470 24.913599 16.870540 3.868954 1.728198 0.771958 kD 0.000000 0.303388 0.107646 0.047097 0.053951 0.038194 0.027039 kE 0.000000 0.057776 0.014314 0.009494 0.005438 0.004767 0.003676 kG 0.100000 0.012559 0.003155 0.001991 0.001256 0.000792 0.000500

190 kM 0 0 0 0 0 0 0 mo 1 1 0.95 0.95 0.95 0.95 1 mp 0 0 0.05 0.05 0.05 0.05 0

Σ (Pi * CDi) 0 0.002368889 0.00142585 0.00142585 0.0017963 0.00212473 0.00241429 Ф 1.00000000 Equation A2

XPOC 0.0000000

XDOC 0.0000000

KOW 3981 Ф 1.00000000 Equation A4

CS 0.0002

CSOC 0.0052

CWDP 0.00001

KOC 799 OC 4% Equation A5

Cox N/A 5

EW N/A 0.529399054

GV N/A 0.007891472 0.703328201 3.14165167 14.0332425 62.6841919 280 k1 693.7037532 41777.37923 3723.412843 1663.18742 742.918533 331.849519 148.231735

KOW 3981

WB N/A 0.0000001 0.0001 0.001 0.01 0.1 1 Equation A6 k1 693.7037532 41777.37923 3723.412843 1663.18742 742.918533 331.849519 148.231735 k2 3.613201435 304.9384703 24.9135992 16.87054 3.86895436 1.72819843 0.77195788

KBW 191.9914419 137.0026523 149.4530282 98.5853104 192.020495 192.020495 192.020495

KOW 3981

VLB 0.02 0.03 0.03 0.02 0.04 0.04 0.04

VNB 0.08 0.12 0.21 0.13 0.23 0.23 0.23

VWB 0.9 0.85 0.76 0.85 0.73 0.73 0.73 Β 0.35 0.035 Equation A7 kG 0.1 0.012559432 0.003154787 0.00199054 0.00125594 0.00079245 0.0005 T 15

WB N/A 0.0000001 0.0001 0.001 0.01 0.1 1 Equation A8

Cox N/A N/A N/A 5 N/A N/A N/A

CSS N/A N/A N/A 3.00E-05 N/A N/A N/A

ED N/A 0.499701598

191 GD N/A 6.07E-08 2.15E-05 9.42E-05 1.08E-03 7.64E-03 5.41E-02

GV N/A N/A N/A 3.14 N/A N/A N/A kD 0 3.03E-01 1.08E-01 4.71E-02 5.40E-02 3.82E-02 2.70E-02

KOW 3981 T N/A 15

WB N/A 0.0000001 0.0001 0.001 0.01 0.1 1 Equation A9

Cox N/A N/A N/A 5 N/A N/A N/A

CSS N/A N/A N/A 3.00E-05 N/A N/A N/A

ED N/A 0.4997

GD N/A 0.0000 0.0000 0.0000942 0.0011 0.0076 0.0541

GF N/A 0.000000 0.000015 0.000066 0.000726 0.004965 0.034777

GV N/A N/A N/A 3.1417 N/A N/A N/A kE 0 0.0578 0.0143 0.0095 0.0054 0.0048 0.0037

KGB N/A 0.2709 0.1894 0.2872 0.1500 0.1922 0.2115

KOW N/A 3981 T N/A 15

VLB N/A 0.03 0.03 0.02 0.04 0.04 0.04

VLD N/A 0.02 0.01650 0.0165 0.03 0.035 0.04

VLG N/A 0.007966 0.005876 0.005876 0.003571 0.004311 0.004979

VNB N/A 0.12 0.21 0.13 0.23 0.23 0.23

VND N/A 0.08 0.0796 0.0796 0.165 0.22 0.23

VNG N/A 0.03186 0.02835 0.02835 0.09819 0.13548 0.14315

VWB N/A 0.85 0.76 0.85 0.73 0.73 0.73

VWD N/A 0.9 0.9039 0.9039 0.805 0.745 0.73

VWG N/A 0.9602 0.9658 0.9658 0.8982 0.8602 0.8519

WB N/A 0.0000001 0.0001 0.001 0.01 0.1 1 Β N/A 0.035 0.035 0.035 0.035 0.035 0.035

εL N/A 0.72 0.75 0.75 0.92 0.92 0.92

εN N/A 0.72 0.75 0.75 0.6 0.6 0.6

εW N/A 0.25 0.25 0.25 0.25 0.25 0.25 Calculation of BCF values

CBCF 0.002434451 0.001737194 0.001848585 0.0012194 0.0023751 0.0023751 0.00243482

Table H11. Estimated concentrations of picoxystrobin in ecosystem components.

Lipid normalized Contributio Contributio Total concentratio n due to n due to concentratio n (µg/kg- diet (µg/kg- respiration Ecosystem Component n (µg/kg-ww) lipid) ww) (µg/kg-ww)

192 Water (total)* 9 N/A N/A N/A Water (freely dissolved)* 9 N/A N/A N/A Sediment (pore water)* 4 N/A N/A N/A Sediment (in solid)** 118 N/A N/A N/A Phytoplankton 1,666 83322 N/A 1,666.44 Zooplankton 1,223 40781 1.66 1,221.78 Benthic Invertebrates 1,297 43250 4.29 1,293.21 Filter Feeders 856 42792 2.77 853.07 Small Fish 1,677 41935 17.55 1,659.83 Medium Fish 1,690 42254 32.77 1,657.37 Large Fish 1,762 44062 58.88 1,703.61 * Units: µg/L; **Units: µg/kg-dw

Table H12. Total BCFand BAF values of picoxystrobin in aquatic trophic levels.

Total BCF Total BAF (µg/kg- (µg/kg- Trophic Level ww)/(µg/L) ww)/(µg/L) Phytoplankton 192 187 Zooplankton 137 137

193 Benthic Invertebrates 145 145 Filter Feeders 96 96 Small Fish 186 188 Medium Fish 186 189 Large Fish 192 198

Table H13. Lipid-normalized BCF, BAF, BMF and BSAF values of picoxystrobin in aquatic trophic levels. BMF BSAF BCF BAF (µg/kg- (µg/kg- (µg/kg- (µg/kg- lipid)/(µg/k lipid)/(µg/k Trophic Level lipid)/(µg/L) lipid)/(µg/L) g-lipid) g-OC) Phytoplankton 9600 9341 N/A 28 Zooplankton 4567 4572 0.49 14 Benthic Invertebrates 4836 4849 1.06 15 Filter Feeders 4785 4797 1.04 14 Small Fish 4660 4701 1.00 14 Medium Fish 4660 4737 0.99 14 Large Fish 4801 4940 1.04 15

Table H14. Calculation of EECs for mammals and birds consuming fish contaminated by picoxystrobin. Wildlife Species EECs (pesticide Biological Parameters intake) Body Dry Food Wet Food Drinking Dose Dietary Weight Ingestion Ingestion Water Based Based (kg) Rate (kg-dry Rate (kg-wet Intake (mg/kg- (ppm) food/kg- food/kg- (L/d) bw/d) bw/day) bw/day)

Mammalian fog/water shrew 0.02 0.140 0.585 0.003 0.761 1.30 rice rat/star-nosed 0.1 0.107 0.484 0.011 0.619 1.28 mole small mink 0.5 0.079 0.293 0.048 0.497 1.69 large mink 1.8 0.062 0.229 0.168 0.388 1.69 small river otter 5.0 0.052 0.191 0.421 0.324 1.69 large river otter 15.0 0.042 0.157 1.133 0.278 1.76 Avian sandpipers 0.0 0.228 1.034 0.004 1.3262 1.28 cranes 6.7 0.030 0.136 0.211 0.1749 1.29

194 rails 0.1 0.147 0.577 0.010 0.8600 1.49 herons 2.9 0.040 0.157 0.120 0.2355 1.49 small osprey 1.3 0.054 0.199 0.069 0.3375 1.69 white pelican 7.5 0.029 0.107 0.228 0.1883 1.76

Table H15. Calculation of toxicity values for mammals and birds consuming fish contaminated by picoxystrobin. Toxicity Values Acute Chronic Dose Dietary Dose Based Dietary Based Based (mg/kg -bw) Based (mg/kg- (mg/kg-diet) (mg/kg- Wildlife Species bw) diet) Mammalian fog/water shrew 10499.51 N/A 5.25 50 rice rat/star-nosed mole 7122.50 N/A 3.56 50 small mink 4695.52 N/A 2.35 50 large mink 3320.24 N/A 1.66 50 small river otter 2571.84 N/A 1.29 50 large river otter 1954.18 N/A 0.98 50 Avian sandpipers 512.71 5200.00 N/A 157 cranes 1226.39 5200.00 N/A 157 rails 618.70 5200.00 N/A 157 herons 1081.63 5200.00 N/A 157 small osprey 953.35 5200.00 N/A 157 white pelican 1247.32 5200.00 N/A 157

Table H16. Calculation of RQ values for mammals and birds consuming fish contaminated by picoxystorbin. Acute Chronic Dose Dietary Dose Based Dietary Wildlife Species Based Based Based

195 Mammalian fog/water shrew 0.000 N/A 0.145 0.026 rice rat/star-nosed 0.000 N/A 0.174 0.026 mole small mink 0.000 N/A 0.212 0.034 large mink 0.000 N/A 0.234 0.034 small river otter 0.000 N/A 0.252 0.034 large river otter 0.000 N/A 0.284 0.035

Avian sandpipers 0.003 0.000 N/A 0.008 cranes 0.000 0.000 N/A 0.008 rails 0.001 0.000 N/A 0.009 herons 0.000 0.000 N/A 0.010 small osprey 0.000 0.000 N/A 0.011 white pelican 0.000 0.000 N/A 0.011

196

Appendix I. SIP and STIR

Table 1. Inputs Parameter Value Chemical name Picoxystrobin Solubility (in water at 25oC; mg/L) 3

Mammalian LD50 (mg/kg-bw) 5000 Mammalian test species laboratory rat

Mammalian NOAEL (mg/kg-bw) 5.4 Mammalian test species laboratory rat

Avian LD50 (mg/kg-bw) 486 Avian test species other Body weight (g) of "other" avian species 30 Mineau scaling factor 1.15

Mallard NOAEC (mg/kg-diet) 157 Bobwhite quail NOAEC (mg/kg-diet) 1200

Table 2. Mammalian Results Parameter Acute Chronic Upper bound exposure (mg/kg-bw) 0.5160 0.5160 Adjusted toxicity value (mg/kg-bw) 3845.8028 4.1535 Ratio of exposure to toxicity 0.0001 0.1242 Drinking water exposure Drinking water exposure Conclusion* alone is NOT a potential alone is NOT a potential concern for mammals concern for mammals

Table 3. Avian Results Parameter Acute Chronic Upper bound exposure (mg/kg-bw) 2.4300 2.4300 Adjusted toxicity value (mg/kg-bw) 457.3225 7.7892 Ratio of exposure to acute toxicity 0.0053 0.3120 Drinking water exposure Drinking water exposure Conclusion* alone is NOT a potential alone is NOT a potential concern for birds 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.

197

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 Picoxystrobin Enter Chemical Use Fungicide 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) 367.3 Enter Chemical Vapor Pressure (mmHg) 4.14E-08 Enter Application Rate (lb a.i./acre) 0.195 Toxicity Properties Bird

Enter Lowest Bird Oral LD50 (mg/kg bw) 486 Enter Mineau Scaling Factor 1.15 Enter Tested Bird Weight (kg) 0.03 Mammal

Enter Lowest Rat Oral LD50 (mg/kg bw) 5000

Enter Lowest Rat Inhalation LC50 (mg/L) 3.19 Duration of Rat Inhalation Study (hrs) 4 Enter Rat Weight (kg) 0.35

Output Results Avian (0.020 kg ) Maximum Vapor Concentration in Air at Saturation (mg/m3) 8.18E-04 Maximum 1-hour Vapor Inhalation Dose (mg/kg) 1.03E-04 Adjusted Inhalation LD50 2.26E+00

Ratio of Vapor Dose to Adjusted Inhalation LD50 4.56E-05 Exposure not Likely Significant Maximum Post-treatment Spray Inhalation Dose (mg/kg) 1.87E-02 Ratio of Droplet Inhalation Dose to Adjusted Inhalation LD50 8.30E-03 Exposure not Likely Significant

Results Mammalian (0.015 kg ) Maximum Vapor Concentration in Air at Saturation (mg/m3) 8.18E-04 Maximum 1-hour Vapor Inhalation Dose (mg/kg) 1.29E-04 Adjusted Inhalation LD50 1.90E+02 Ratio of Vapor Dose to Adjusted Inhalation LD50 6.81E-07 Exposure not Likely Significant Maximum Post-treatment Spray Inhalation Dose (mg/kg) 2.35E-02 Ratio of Droplet Inhalation Dose to Adjusted Inhalation LD50 1.24E-04 Exposure not Likely Significant

198 Appendix J: Federally-listed endangered and threatened species

County Occurrence List by State and Taxa No species were excluded Minimum of 1 Acre All Medium Types Included Amphibian, Bird, Bivalve, Coral, Crustacean, Fish, Gastropod, Mammal, Reptile barley for grain, corn for grain, corn for silage or greenchop, corn-popcorn & sweet corn, corn- sweet for seed, sorghum for grain, sorghum for silage or greenchop, soybeans, wheat-all, beans- dry edible excluding limas, canola, dry beans, peas-austrian winter, peas-chinese (sugar and snow), peas-dry edible, peas-dry southern (cowpeas), peas-green (excluding southern), peas- green southern (cowpeas) - blackeyed, crowder, etc., peas-pigeon, buckwheat, oats for grain, rye for grain, beans-all other All States Selected Alabama Bivalve Bivalve Amphibian Fanshell Marion Cyprogenia stegaria Pickens Salamander, Frosted Flatwoods Colbert Shelby Ambystoma cingulatum Lauderdale Tuscaloosa Baldwin Winston Kidneyshell, Triangular Winston Covington Ptychobranchus greenii Mucket, Pink (Pearlymussel) Houston Lampsilis abrupta Bibb Lampsilis abrupta Mobile Colbert Blount Colbert Salamander, Red Hills Calhoun Jackson Phaeognathus hubrichti Cherokee Lauderdale Butler Cleburne Lawrence Conecuh Cullman Limestone Covington Etowah Madison Crenshaw Jefferson Marshall Monroe Lawrence Morgan Wilcox Shelby Mussel, Acornshell Southern Bivalve St. Clair Epioblasma othcaloogensis Bankclimber, Purple Talladega Shelby Elliptoideus sloatianus Walker St. Clair Lee Winston Mussel, Alabama Moccasinshell Combshell, Southern (=Penitent Mucket, Orange-nacre Medionidus acutissimus mussel) Lampsilis perovalis Greene Epioblasma penita Bibb Lamar Lamar Blount Lawrence Marion Dallas Pickens Combshell, Upland Fayette Shelby Epioblasma metastriata Greene Tuscaloosa Jefferson Jefferson Winston St. Clair Lamar Mussel, Coosa Moccasinshell Lawrence Medionidus parvulus 199 Bivalve Bivalve Bivalve Cherokee Madison Cullman Talladega Marshall Etowah Winston Mussel, Flat Pigtoe (=Marshall's Greene Mussel) Lamar Mussel, Cumberland Combshell Lamar Epioblasma brevidens Pleurobema marshalli Lee Colbert Pickens Macon Franklin Mussel, Georgia pigtoe Perry Pleurobema hanleyianum Pickens Mussel, Dark Pigtoe Pickens Pleurobema furvum Cherokee St. Clair Fayette Clay Sumter Lawrence Coosa Tuscaloosa Tuscaloosa Mussel, Gulf Moccasinshell Walker Winston Medionidus penicillatus Winston Houston Mussel, Ring Pink (=Golf Stick Pearly) Mussel, Fine-lined Pocketbook Mussel, Ring Pink (=Golf Stick Pearly) Lampsilis altilis Mussel, Heavy Pigtoe (=Judge Tait's Obovaria retusa Mussel) Bibb Pleurobema taitianum Colbert Blount Baldwin Lauderdale Calhoun Clarke Limestone Chambers Dallas Morgan Cherokee Greene Mussel, Rough Pigtoe Chilton Monroe Pleurobema plenum Clay Pickens Colbert Cleburne Sumter Lauderdale Coosa Wilcox Lawrence Cullman Limestone Mussel, Heelsplitter Inflated Dallas Potamilus inflatus Madison De Kalb Marshall Baldwin Elmore Morgan Choctaw Etowah Mussel, Shiny Pigtoe Clarke Mussel, Shiny Pigtoe Fayette Fusconaia cor Greene Jefferson Jackson Hale Lawrence Madison Marengo Lee Marshall Pickens Macon Mussel, Shiny-rayed Pocketbook Sumter Mussel, Shiny-rayed Pocketbook Shelby Lampsilis subangulata Tuscaloosa St. Clair Houston Washington Houston Talladega Russell Tallapoosa Mussel, Oval Pigtoe Pleurobema pyriforme Mussel, Southern Clubshell Tuscaloosa Pleurobema decisum Houston Walker Bibb Winston Mussel, Ovate Clubshell Calhoun Pleurobema perovatum Calhoun Mussel, Fine-rayed Pigtoe Bibb Cherokee Fusconaia cuneolus Cleburne Blount Jackson Dallas 200 Cherokee Bivalve Bivalve Fish Etowah Lauderdale Sculpin, Pygmy Greene Stirrupshell Cottus paulus (=pygmaeus) Lamar Quadrula stapes Calhoun Lee Greene Shiner, Blue Macon Pickens Cyprinella caerulea Pickens Sumter Calhoun Shelby Crustacean Cherokee St. Clair Shrimp, Alabama Cave Clay Talladega Palaemonias alabamae Coosa Tuscaloosa Colbert De Kalb Mussel, Southern Pigtoe Madison Shiner, Cahaba Pleurobema georgianum Fish Notropis cahabae Calhoun Bibb Clay Cavefish, Alabama Speoplatyrhinus poulsoni Blount Cleburne Jefferson Lauderdale Jefferson Coosa Perry Etowah Chub, Spotfin Shelby Erimonax monachus Shelby Shelby Shiner, Palezone Colbert Shiner, Palezone St. Clair Notropis albizonatus Lauderdale Talladega Jackson Darter, Boulder Pearlymussel, Alabama Lamp Etheostoma wapiti Sturgeon, Alabama Lampsilis virescens Scaphirhynchus suttkusi Limestone Jackson Autauga Darter, Goldline Pearlymussel, Cracking Percina aurolineata Baldwin Hemistena lata Clarke Bibb Colbert Dallas Jefferson Lauderdale Lowndes Shelby Limestone Monroe Darter, Slackwater Pearlymussel, Cumberland Etheostoma boschungi Wilcox Quadrula intermedia Sturgeon, Gulf Lauderdale Sturgeon, Gulf Limestone Acipenser oxyrinchus desotoi Limestone Pearlymussel, Orange-footed Madison Baldwin Plethobasus cooperianus Choctaw Marshall Darter, Snail Clarke Percina tanasi Pearlymussel, Pale Lilliput Madison Coffee Toxolasma cylindrellus Conecuh Marshall Jackson Covington Darter, Vermilion Dale Pearlymussel, Turgid-blossom Etheostoma chermocki Dale Epioblasma turgidula Escambia Jefferson Colbert Geneva Lauderdale Darter, Watercress Houston Etheostoma nuchale Pearlymussel, White Wartyback Jefferson Mobile Plethobasus cicatricosus Monroe Colbert Washington

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201 Fish Gastropod Mammal Wilcox Limestone Mouse, Alabama Beach Gastropod Snail, Lioplax Cylindrical Peromyscus polionotus ammobates Lioplax cyclostomaformis Baldwin Campeloma, Slender Baldwin Campeloma decampi Bibb Mouse, Perdido Key Beach Limestone Shelby Peromyscus polionotus trissyllepsis Madison Mammal Baldwin Elimia, Lacy Bat, Gray Reptile Elimia crenatella Myotis grisescens Turtle, Alabama Red-bellied Talladega Bibb Pseudemys alabamensis Hornsnail, rough Calhoun Baldwin Pleurocera foremani Colbert Mobile Elmore Conecuh Turtle, Flattened Musk Shelby De Kalb Sternotherus depressus Talladega Franklin Blount Pebblesnail, Flat Jackson Cullman Lepyrium showalteri Lauderdale Etowah Bibb Lawrence Jefferson Shelby Limestone Marshall Riversnail, Anthony's Madison Tuscaloosa Athearnia anthonyi Marshall Walker Colbert Monroe Winston Jackson Morgan Alaska Lauderdale Shelby Limestone Bat, Indiana Mammal Rocksnail, interrupted Myotis sodalis Whale, beluga Leptoxis foremani Bibb Delphinapterus leucas Cherokee Calhoun Anchorage Elmore Colbert Whale, Gray Rocksnail, Painted Conecuh Eschrichtius robustus Leptoxis taeniata De Kalb Aleutian Islands Calhoun Franklin Anchorage Chilton Jackson Fairbanks North Star Shelby Lauderdale Arizona Talladega Lawrence Amphibian Rocksnail, Plicate Limestone Leptoxis plicata Madison Frog, Chiricahua Leopard Blount Marshall Rana chiricahuensis Jefferson Monroe Apache Rocksnail, Round Morgan Cochise Leptoxis ampla Shelby Coconino Gila Bibb Manatee, West Indian Shelby Trichechus manatus Graham Snail, Armored Baldwin Greenlee Pyrgulopsis (=Marstonia) pachyta Mobile Navajo

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202 Amphibian Fish Fish Pima Graham La Paz Santa Cruz Greenlee Maricopa Yavapai Navajo Mohave Salamander, Sonora Tiger Pinal Pinal Ambystoma tigrinum stebbinsi Pupfish, Desert Yavapai Cochise Cyprinodon macularius Yuma Santa Cruz Cochise Topminnow, Gila (Yaqui) Fish Graham Poeciliopsis occidentalis Catfish, Yaqui La Paz Cochise Ictalurus pricei Maricopa Gila Cochise Pima Graham Pinal La Paz Chub, Bonytail Gila elegans Santa Cruz Maricopa La Paz Yavapai Pima Mohave Shiner, Beautiful Pinal Cyprinella formosa Santa Cruz Chub, Gila Gila intermedia Cochise Yavapai Cochise Spikedace Trout, Apache Gila Meda fulgida Oncorhynchus apache Graham Cochise Apache Greenlee Gila Coconino Maricopa Graham Gila Pima Greenlee Graham Pinal Navajo Greenlee Santa Cruz Pinal Navajo Yavapai Yavapai Trout, Gila Chub, Humpback Spinedace, Little Colorado Oncorhynchus gilae Gila cypha Lepidomeda vittata Gila Coconino Apache Greenlee Mohave Coconino Woundfin Navajo Plagopterus argentissimus Chub, Sonora Gila ditaenia Squawfish, Colorado Maricopa Santa Cruz Ptychocheilus lucius Mohave Chub, Virgin River Gastropod Gila Gastropod Gila seminuda (=robusta) Yavapai Ambersnail, Kanab Mohave Steelhead Oxyloma haydeni kanabensis Oncorhynchus (=Salmo) mykiss Coconino Chub, Yaqui Coconino Gila purpurea Santa Cruz Mammal Cochise Sucker, Razorback Bat, Lesser (=Sanborn's) Long-nosed Xyrauchen texanus Leptonycteris curasoae yerbabuenae Minnow, Loach Leptonycteris curasoae yerbabuenae Tiaroga cobitis Coconino Cochise Apache Gila Gila Cochise Graham Graham Gila Greenlee Greenlee 12/21/2011 2:57:15 PM Ver. 2.2.0 Page 5 of 64

203 Mammal Bivalve Bivalve Maricopa Mussel, Scaleshell Calhoun Pima Leptodea leptodon Clark Pinal Baxter Hempstead Santa Cruz Carroll Hot Spring Arkansas Clark Little River Crawford Ouachita Bivalve Franklin Sevier Fatmucket, Arkansas Fulton Crustacean Lampsilis powelli Lawrence Crayfish, Cave (Cambarus aculabrum) Clark Marion Cambarus aculabrum Grant Perry Benton Montgomery Sevier Washington Pike St. Francis Crayfish, Cave (Cambarus Polk Mussel, Speckled Pocketbook zophonastes) Saline Lampsilis streckeri Cambarus zophonastes Mucket, Pink (Pearlymussel) Van Buren Marion Lampsilis abrupta Fish Mussel, Winged Mapleleaf Fish Arkansas Quadrula fragosa Cavefish, Ozark Ashley Ashley Amblyopsis rosae Baxter Bradley Benton Bradley Calhoun Darter, Leopard Calhoun Clark Percina pantherina Clark Cleveland Polk Clay Ouachita Sevier Cleveland Pearlymussel, Curtis' Shiner, Arkansas River Dallas Epioblasma florentina curtisii Notropis girardi Grant Fulton Logan Hot Spring Lawrence Sturgeon, Pallid Independence Scaphirhynchus albus Pearlymussel, Fat Pocketbook Scaphirhynchus albus Jackson Potamilus capax Chicot Lawrence Craighead Crittenden Little River Crittenden Desha Marion Cross Lee Monroe Lee Mississippi Ouachita Mississippi Phillips Prairie Phillips St. Francis Randolph Poinsett Trout, Bull Saline St. Francis Salvelinus confluentus Scott Pearlymussel, Turgid-blossom Lincoln Sevier Epioblasma turgidula Mammal Sharp Sharp White Bat, Gray Rock-pocketbook, Ouachita Myotis grisescens Woodruff (=Wheeler's pm) Myotis grisescens Arkansia wheeleri Baxter Benton 12/21/2011 2:57:15 PM Ver. 2.2.0 Page 6 of 64

204 Mammal Amphibian Amphibian Boone Lake Amador Carroll Lassen Butte Independence Los Angeles Calaveras Izard Madera Colusa Lawrence Marin Contra Costa Madison Mendocino El Dorado Marion Merced Fresno Newton Monterey Kern Pope Napa Kings Searcy Nevada Madera Sharp Orange Marin Van Buren Placer Merced Washington Riverside Monterey Bat, Indiana Sacramento Napa Myotis sodalis San Benito Placer Benton San Bernardino Sacramento Independence San Diego San Benito Izard San Joaquin San Joaquin Madison San Luis Obispo San Luis Obispo Marion San Mateo San Mateo Newton Santa Barbara Santa Barbara Searcy Santa Clara Santa Clara Washington Santa Cruz Santa Cruz Bat, Ozark Big-eared Shasta Solano Corynorhinus (=Plecotus) townsendii Siskiyou Sonoma ingens Solano Stanislaus Benton Sonoma Sutter Marion Stanislaus Tulare Washington Sutter Tuolumne California Tehama Yolo Amphibian Trinity Yuba Tulare Salamander, Desert Slender Frog, California Red-legged Tuolumne Batrachoseps aridus Rana aurora draytonii Ventura Riverside Alameda Yolo Salamander, Santa Cruz Long-toed Amador Yuba Salamander, Santa Cruz Long-toed Ambystoma macrodactylum croceum Butte Frog, Mountain Yellow-legged Monterey Calaveras Rana muscosa Santa Cruz Colusa Los Angeles Toad, Arroyo Southwestern Contra Costa Toad, Arroyo Southwestern Riverside Bufo californicus (=microscaphus) El Dorado San Bernardino Los Angeles Fresno Glenn Salamander, California Tiger Monterey Ambystoma californiense Orange Kern Alameda Riverside Kings 12/21/2011 2:57:16 PM Ver. 2.2.0 Page 7 of 64

205 Amphibian Crustacean Crustacean San Bernardino Merced Calaveras San Diego Monterey Colusa San Luis Obispo Napa Contra Costa Santa Barbara Placer Fresno Ventura Sacramento Glenn Bird San Benito Kern Albatross, Short-tailed San Joaquin Kings Phoebastria (=Diomedea) albatrus San Luis Obispo Madera Humboldt Siskiyou Merced Los Angeles Solano Monterey Marin Stanislaus Napa Mendocino Sutter Placer Orange Tehama Riverside San Diego Ventura Sacramento San Mateo Yolo San Benito Sonoma Fairy Shrimp, Longhorn San Joaquin Branchinecta longiantenna San Luis Obispo Murrelet, Marbled Brachyramphus marmoratus Alameda Santa Barbara Humboldt Contra Costa Santa Clara Lake Kern Shasta Los Angeles Madera Siskiyou Marin Merced Solano Mendocino Monterey Stanislaus Monterey San Benito Sutter San Mateo San Joaquin Tehama Santa Barbara San Luis Obispo Tulare Santa Clara Santa Barbara Tuolumne Siskiyou Stanislaus Ventura Sonoma Fairy Shrimp, Riverside Yolo Trinity Streptocephalus woottoni Yuba Crustacean Los Angeles Shrimp, California Freshwater Orange Syncaris pacifica Crayfish, Shasta Pacifastacus fortis Riverside Lake San Diego Marin Lassen Ventura Mendocino Shasta Siskiyou Fairy Shrimp, San Diego Napa Branchinecta sandiegonensis Sonoma Fairy Shrimp, Conservancy Fairy Branchinecta conservatio Orange Tadpole Shrimp, Vernal Pool San Diego Lepidurus packardi Butte Colusa Fairy Shrimp, Vernal Pool Alameda Branchinecta lynchi Amador Contra Costa Glenn Alameda Butte Kern Amador Calaveras Mendocino Butte Colusa

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206 Crustacean Fish Fish Contra Costa San Luis Obispo Mendocino El Dorado San Mateo Napa Fresno Santa Barbara San Mateo Glenn Santa Clara Santa Cruz Kings Santa Cruz Siskiyou Madera Sonoma Sonoma Merced Ventura Trinity Placer Pupfish, Desert Smelt, Delta Sacramento Cyprinodon macularius Hypomesus transpacificus San Benito Imperial Contra Costa San Joaquin Riverside Lassen Shasta San Diego Napa Siskiyou Salmon, Chinook Sacramento Solano Oncorhynchus (=Salmo) tshawytscha San Joaquin Stanislaus Alameda Shasta Sutter Butte Siskiyou Tehama Colusa Solano Tulare Contra Costa Stanislaus Yolo Glenn Trinity Yuba Humboldt Yolo Fish Marin Squawfish, Colorado Chub, Bonytail Mendocino Ptychocheilus lucius Gila elegans Napa Imperial Imperial Nevada Riverside Riverside Placer San Bernardino San Bernardino Sacramento Steelhead Chub, Mohave Tui San Joaquin Oncorhynchus (=Salmo) mykiss Gila bicolor mohavensis San Mateo Alameda San Bernardino Santa Clara Amador Chub, Owens Tui Shasta Butte Gila bicolor snyderi Siskiyou Calaveras Mono Solano Colusa Sonoma Contra Costa Goby, Tidewater Contra Costa Eucyclogobius newberryi Sutter Fresno Alameda Tehama Glenn Contra Costa Trinity Humboldt Humboldt Yolo Kern Los Angeles Yuba Lake Marin Salmon, Coho Los Angeles Mendocino Oncorhynchus (=Salmo) kisutch Marin Monterey Glenn Mendocino Napa Humboldt Merced Orange Lake Monterey San Diego Marin Napa

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207 Fish Fish Gastropod Nevada Tehama Abalone, Black Placer Yolo Haliotis cracherodii Sacramento Yuba Los Angeles San Benito Sucker, Lost River Marin San Joaquin Deltistes luxatus Mendocino San Luis Obispo Modoc Monterey San Mateo Siskiyou Orange Santa Barbara Sucker, Modoc San Diego Santa Clara Catostomus microps San Luis Obispo Santa Cruz Lassen San Mateo Shasta Modoc Santa Barbara Solano Sucker, Razorback Santa Cruz Sonoma Xyrauchen texanus Sonoma Stanislaus Imperial Ventura Sutter Riverside Abalone, White Tehama San Bernardino Haliotis sorenseni Trinity Sucker, Santa Ana Marin Tuolumne Catostomus santaanae San Mateo Ventura Los Angeles Sonoma Yolo Orange Mammal Yuba Riverside Mountain Beaver, Point Arena Stickleback, Unarmored Threespine San Bernardino Aplodontia rufa nigra Gasterosteus aculeatus williamsoni Sucker, Shortnose Mendocino Los Angeles Chasmistes brevirostris Otter, Southern Sea San Bernardino Modoc Enhydra lutris nereis San Diego Siskiyou Los Angeles Santa Barbara Trout, Lahontan Cutthroat Monterey Ventura Oncorhynchus clarki henshawi Orange Sturgeon, North American green El Dorado San Diego Acipenser medirostris Fresno San Luis Obispo Alameda Madera San Mateo Butte Mono Santa Barbara Colusa Nevada Santa Cruz Contra Costa Placer Ventura Glenn Trout, Little Kern Golden Seal, Guadalupe Fur Marin Oncorhynchus aguabonita whitei Arctocephalus townsendi Napa Tulare Marin Sacramento Trout, Paiute Cutthroat San Mateo San Joaquin Oncorhynchus clarki seleniris Sonoma San Mateo Fresno Sea-lion, Steller Solano Madera Eumetopias jubatus Sonoma Mono Humboldt Stanislaus Tuolumne Marin Sutter Gastropod Mendocino 12/21/2011 2:57:16 PM Ver. 2.2.0 Page 10 of 64

208 Mammal Mammal Reptile San Mateo San Luis Obispo Snake, Giant Garter Sonoma San Mateo Thamnophis gigas Whale, Finback Santa Barbara Amador Balaenoptera physalus Santa Clara Butte Humboldt Santa Cruz Calaveras Marin Shasta Colusa Mendocino Siskiyou Contra Costa San Mateo Solano El Dorado Sonoma Sonoma Fresno Whale, Gray Stanislaus Glenn Eschrichtius robustus Sutter Kern Alameda Tehama Kings Amador Trinity Madera Butte Tulare Merced Calaveras Tuolumne Napa Colusa Ventura Placer Contra Costa Yolo Sacramento El Dorado Yuba San Joaquin Fresno Whale, Humpback San Luis Obispo Glenn Megaptera novaeangliae Solano Humboldt Humboldt Stanislaus Imperial Marin Sutter Kern Mendocino Tehama Kings San Mateo Tulare Lake Sonoma Tuolumne Lassen Whale, North Atlantic right Yolo Los Angeles Eubalaena glacialis (incl. australis) Yuba Madera Marin Snake, San Francisco Garter Marin San Mateo Thamnophis sirtalis tetrataenia Mendocino Sonoma San Mateo Merced Whale, Sei Santa Clara Modoc Balaenoptera borealis Santa Cruz Mono Humboldt Colorado Monterey Marin Napa Mendocino Bird Nevada San Mateo Crane, Whooping Orange Sonoma Grus americana Placer Whale, Sperm Adams Riverside Physeter catodon (=macrocephalus) Arapahoe Sacramento Humboldt Boulder San Benito Marin Denver San Bernardino Mendocino Douglas San Diego San Mateo El Paso San Joaquin Sonoma Elbert

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209 Bird Fish Fish Jefferson Delta Mesa Larimer Dolores Moffat Lincoln Eagle Montezuma Logan Garfield Montrose Morgan Grand Ouray Park La Plata Rio Blanco Sedgwick Mesa Rio Grande Teller Moffat Routt Washington Montezuma Saguache Weld Montrose San Miguel Fish Ouray Trout, Greenback Cutthroat Chub, Bonytail Rio Blanco Oncorhynchus clarki stomias Gila elegans Rio Grande Boulder Delta Routt Douglas Dolores Saguache El Paso Eagle San Miguel Huerfano Garfield Sturgeon, Pallid Lake Grand Scaphirhynchus albus Larimer Mesa Adams Park Moffat Arapahoe Pueblo Montrose Boulder Connecticut Ouray Denver Rio Blanco Douglas Bivalve Routt El Paso Mussel, Dwarf Wedge Saguache Elbert Alasmidonta heterodon San Miguel Jefferson Hartford Chub, Humpback Larimer Mammal Gila cypha Lincoln Bat, Indiana Delta Logan Myotis sodalis Dolores Morgan New Haven Eagle Park Reptile Garfield Sedgwick Turtle, Bog Grand Teller Clemmys muhlenbergii Mesa Washington Fairfield Moffat Weld Litchfield Montrose Sucker, Razorback Delaware Ouray Xyrauchen texanus Rio Blanco Archuleta Reptile Routt Delta Turtle, Bog Saguache Dolores Clemmys muhlenbergii San Miguel Eagle New Castle Squawfish, Colorado Garfield Florida Ptychocheilus lucius Grand Archuleta La Plata Amphibian

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210 Amphibian Bivalve Bivalve Salamander, Frosted Flatwoods Calhoun Jackson Ambystoma cingulatum Gadsden Leon Baker Gulf Wakulla Bay Jackson Slabshell, Chipola Bradford Leon Elliptio chipolaensis Calhoun Wakulla Calhoun Duval Mussel, Fat Threeridge Gulf Gulf Amblema neislerii Jackson Holmes Calhoun Coral Jackson Gadsden Coral, Elkhorn Okaloosa Gulf Acropora palmata Santa Rosa Jackson Miami-Dade Wakulla Mussel, Gulf Moccasinshell Coral, Staghorn Walton Medionidus penicillatus Acropora cervicornis Washington Bay Miami-Dade Salamander, Reticulated flatwoods Calhoun Crustacean Ambystoma bishopi Gadsden Bay Gulf Shrimp, Squirrel Chimney Cave Palaemonetes cummingi Calhoun Jackson Alachua Escambia Washington Fish Gulf Mussel, Ochlockonee Moccasinshell Holmes Medionidus simpsonianus Darter, Okaloosa Jackson Gadsden Etheostoma okaloosae Okaloosa Leon Okaloosa Santa Rosa Wakulla Walton Walton Mussel, Oval Pigtoe Sawfish, Smalltooth Washington Pleurobema pyriforme Pristis pectinata Bird Alachua Charlotte Crane, Whooping Bay Collier Grus americana Bradford Indian River Charlotte Calhoun Lee De Soto Columbia Martin Hardee Gadsden Miami-Dade Hendry Gulf Palm Beach Highlands Jackson Sarasota Indian River Leon Sturgeon, Gulf Martin Union Acipenser oxyrinchus desotoi Okeechobee Wakulla Bay Osceola Washington Calhoun Charlotte Palm Beach Mussel, Shiny-rayed Pocketbook Polk Lampsilis subangulata Citrus Bivalve Calhoun Collier Gadsden Columbia Bankclimber, Purple Dixie Elliptoideus sloatianus Gulf Dixie

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211 Fish Mammal Mammal Escambia Bay Bay Flagler Brevard Okaloosa Gadsden Charlotte Walton Gilchrist Citrus Mouse, Perdido Key Beach Gulf Clay Peromyscus polionotus trissyllepsis Hamilton Collier Escambia Hernando De Soto Mouse, Southeastern Beach Hillsborough Dixie Peromyscus polionotus niveiventris Holmes Duval Brevard Jackson Escambia Indian River Jefferson Flagler Martin Lafayette Gulf Palm Beach Lee Hendry Mouse, St. Andrew Beach Leon Hernando Peromyscus polionotus peninsularis Levy Highlands Bay Madison Hillsborough Gulf Manatee Indian River Vole, Florida Salt Marsh Miami-Dade Jefferson Microtus pennsylvanicus Okaloosa Lake Levy Pasco Lee Reptile Santa Rosa Levy Alligator, American Sarasota Manatee Alligator mississippiensis Suwannee Marion Charlotte Taylor Martin Collier Wakulla Miami-Dade De Soto Walton Nassau Hardee Washington Okaloosa Hendry Sturgeon, Shortnose Okeechobee Highlands Acipenser brevirostrum Palm Beach Indian River Clay Pasco Lee Duval Putnam Martin Putnam Santa Rosa Miami-Dade Mammal Sarasota Okeechobee Seminole Osceola Bat, Gray Osceola Myotis grisescens St. Johns Palm Beach Holmes Taylor Polk Jackson Volusia Sarasota Leon Wakulla Crocodile, American Washington Walton Crocodylus acutus Bat, Indiana Mouse, Anastasia Island Beach Charlotte Myotis sodalis Peromyscus polionotus phasma Collier Jackson St. Johns Indian River Manatee, West Indian Mouse, Choctawhatchee Beach Lee Trichechus manatus Peromyscus polionotus allophrys Martin

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212 Reptile Bivalve Bivalve Miami-Dade Crawford Murray Palm Beach Crisp Whitfield Sarasota Decatur Mussel, Fat Threeridge Snake, Atlantic Salt Marsh Dooly Amblema neislerii Nerodia clarkii taeniata Dougherty Baker Brevard Grady Decatur Indian River Harris Dougherty Volusia Lee Macon Georgia Macon Mussel, Fine-lined Pocketbook Mitchell Lampsilis altilis Amphibian Muscogee Chattooga Salamander, Frosted Flatwoods Sumter Haralson Ambystoma cingulatum Talbot Murray Baker Upson Walker Ben Hill Worth Whitfield Berrien Combshell, Upland Mussel, Georgia pigtoe Brooks Epioblasma metastriata Pleurobema hanleyianum Bryan Chattooga Fannin Burke Gordon Gilmer Charlton Murray Gordon Chatham Whitfield Murray Early Kidneyshell, Triangular Walker Effingham Ptychobranchus greenii Whitfield Emanuel Chattooga Mussel, Gulf Moccasinshell Evans Gordon Medionidus penicillatus Irwin Murray Baker Jefferson Whitfield Calhoun Lanier Mussel, Acornshell Southern Coweta Liberty Epioblasma othcaloogensis Crisp Long Chattooga Decatur McIntosh Gordon Dooly Miller Murray Dougherty Screven Whitfield Early Ware Mussel, Alabama Moccasinshell Fayette Worth Medionidus acutissimus Fulton Salamander, Reticulated flatwoods Chattooga Harris Ambystoma bishopi Gordon Lee Baker Murray Meriwether Miller Walker Mitchell Bivalve Whitfield Murray Bankclimber, Purple Mussel, Coosa Moccasinshell Muscogee Elliptoideus sloatianus Medionidus parvulus Pike Baker Chattooga Sumter Coweta Gordon Taylor

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213 Bivalve Bivalve Fish Terrell Coweta Pickens Upson Crisp Whitfield Webster Decatur Darter, Cherokee Worth Dooly Etheostoma scotti Mussel, Ochlockonee Moccasinshell Dougherty Bartow Medionidus simpsonianus Early Cherokee Colquitt Fayette Cobb Grady Fulton Dawson Thomas Grady Forsyth Mussel, Oval Pigtoe Lee Fulton Pleurobema pyriforme Macon Lumpkin Baker Meriwether Paulding Clayton Miller Pickens Colquitt Mitchell Darter, Etowah Coweta Muscogee Etheostoma etowahae Crisp Pike Bartow Decatur Seminole Cherokee Dooly Spalding Dawson Dougherty Sumter Forsyth Early Taylor Lumpkin Fayette Terrell Pickens Grady Thomas Darter, Goldline Lee Upson Percina aurolineata Macon Webster Gilmer Meriwether Worth Gordon Miller Mussel, Southern Clubshell Murray Muscogee Pleurobema decisum Pickens Spalding Gordon Darter, Snail Sumter Murray Percina tanasi Taylor Whitfield Catoosa Terrell Mussel, Southern Pigtoe Logperch, Conasauga Thomas Pleurobema georgianum Percina jenkinsi Upson Chattooga Murray Webster Gordon Whitfield Worth Murray Shiner, Blue Mussel, Ovate Clubshell Walker Cyprinella caerulea Pleurobema perovatum Whitfield Gilmer Murray Fish Gordon Whitfield Darter, Amber Murray Mussel, Shiny-rayed Pocketbook Percina antesella Pickens Lampsilis subangulata Cherokee Whitfield Baker Dawson Sturgeon, Shortnose Calhoun Forsyth Acipenser brevirostrum Colquitt Murray Appling

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214 Fish Mammal Reptile Brantley Manatee, West Indian GUAM Bryan Trichechus manatus Sea turtle, leatherback Burke Bryan Dermochelys coriacea Camden Camden GUAM Chatham Chatham Sea turtle, loggerhead Effingham Glynn Caretta caretta Glynn Liberty GUAM Jeff Davis McIntosh Hawaii Liberty Whale, Humpback Long Megaptera novaeangliae Bird McIntosh Bryan Duck, Hawaiian (Koloa) Montgomery Camden Anas wyvilliana Screven Chatham Hawaii Tattnall Glynn Kauai Telfair Liberty Maui Toombs McIntosh Oahu Wayne Whale, North Atlantic right Goose, Hawaiian (Nene) Wheeler Eubalaena glacialis (incl. australis) Branta (=Nesochen) sandvicensis Gastropod Bryan Hawaii Rocksnail, interrupted Camden Kauai Leptoxis foremani Chatham Maui Murray McIntosh Shearwater, Newell's Townsend's Whitfield Reptile Puffinus auricularis newelli Hawaii Snail, Lioplax Cylindrical Turtle, Bog Lioplax cyclostomaformis Clemmys muhlenbergii Kauai Bartow Rabun Oahu Floyd Towns Crustacean Mammal Union Amphipod, Kauai Cave Spelaeorchestia koloana Bat, Gray Guam Myotis grisescens Kauai Mammal Gastropod Bartow Gastropod Catoosa Bat, Little Mariana Fruit Snail, Newcomb's Chattooga Pteropus tokudae Erinna newcombi Clarke GUAM Kauai Dade Bat, Mariana Fruit (=Mariana Flying Fox) Mammal Floyd Pteropus mariannus mariannus Bat, Hawaiian Hoary Gordon GUAM Lasiurus cinereus semotus Polk Hawaii Reptile Hawaii Walker Kauai Sea turtle, green Bat, Indiana Maui Chelonia mydas Myotis sodalis Oahu GUAM Dade Seal, Hawaiian Monk Murray Sea turtle, hawksbill Monachus schauinslandi Eretmochelys imbricata Whitfield 12/21/2011 2:57:17 PM Ver. 2.2.0 Page 17 of 64

215 Mammal Fish Bivalve Hawaii Trout, Bull Massac Kauai Salvelinus confluentus Mussel, Clubshell Maui Ada Pleurobema clava Oahu Adams Vermilion Idaho Benewah Pearlymussel, Fat Pocketbook Blaine Potamilus capax Fish Bonner Gallatin Salmon, Chinook Boundary Lawrence Oncorhynchus (=Salmo) tshawytscha Butte Massac Adams Camas Pope Blaine Clearwater Wabash Clearwater Custer White Custer Elmore Pearlymussel, Higgins' Eye Idaho Gem Lampsilis higginsii Latah Idaho Henderson Lemhi Kootenai Jo Daviess Lewis Lemhi Mercer Nez Perce Lewis Rock Island Valley Nez Perce Pearlymussel, Orange-footed Salmon, Sockeye Owyhee Plethobasus cooperianus Oncorhynchus (=Salmo) nerka Payette Pulaski Blaine Valley Crustacean Custer Washington Idaho Gastropod Amphipod, Illinois Cave Gammarus acherondytes Lemhi Limpet, Banbury Springs Monroe Lewis Lanx sp. St. Clair Nez Perce Gooding Fish Steelhead Snail, Bliss Rapids Sturgeon, Pallid Oncorhynchus (=Salmo) mykiss Sturgeon, Pallid Taylorconcha serpenticola Scaphirhynchus albus Adams Elmore Scaphirhynchus albus Blaine Gooding Alexander Camas Jerome Jackson Clearwater Twin Falls Madison Custer Monroe Springsnail, Bruneau Hot Randolph Idaho Pyrgulopsis bruneauensis Randolph Latah St. Clair Owyhee Union Lemhi Union Lewis Illinois Mammal Nez Perce Bivalve Bat, Gray Valley Fanshell Myotis grisescens Sturgeon, White Cyprogenia stegaria Alexander Acipenser transmontanus White Hardin Boundary Mucket, Pink (Pearlymussel) Jackson Lampsilis abrupta Johnson

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216 Mammal Bivalve Mammal Pike Mussel, Clubshell Clay Pope Pleurobema clava Clinton Pulaski Carroll Crawford Bat, Indiana De Kalb De Kalb Myotis sodalis Fulton Dearborn Adams Kosciusko Decatur Alexander Marshall Delaware Bond Pulaski Dubois Ford Tippecanoe Elkhart Hardin White Fayette Henderson Mussel, Rough Pigtoe Floyd Jackson Pleurobema plenum Fountain Jersey Martin Franklin Johnson Pearlymussel, Fat Pocketbook Fulton La Salle Potamilus capax Gibson Lawrence Gibson Grant Macoupin Knox Greene Madison Posey Hamilton McDonough Pearlymussel, White Cat's Paw Hancock Monroe Epioblasma obliquata perobliqua Harrison Perry De Kalb Hendricks Pike Riffleshell, Northern Henry Pope Epioblasma torulosa rangiana Howard Pulaski De Kalb Huntington Saline Pulaski Jackson Schuyler Mammal Jasper Scott Jay Bat, Gray Union Myotis grisescens Jefferson Vermilion Clark Jennings Indiana Crawford Johnson Bivalve Floyd Knox Harrison Kosciusko Fanshell La Porte Cyprogenia stegaria Bat, Indiana Myotis sodalis Lagrange Carroll Lake Adams Lake Martin Lawrence Allen Lawrence Sullivan Madison Bartholomew Madison Tippecanoe Marion Benton Marion Wabash Marshall Blackford Marshall White Martin Boone Martin Brown Miami Mucket, Pink (Pearlymussel) Miami Lampsilis abrupta Monroe Carroll Monroe Posey Montgomery Cass Montgomery Clark Morgan

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217 Mammal Iowa Mammal Newton Adams Bivalve Adams Noble Appanoose Ohio Mussel, Dwarf Wedge Cass Alasmidonta heterodon Orange Clarke Owen Louisa Davis Parke Pearlymussel, Higgins' Eye Decatur Perry Lampsilis higginsii Des Moines Pike Allamakee Fremont Porter Clayton Henry Posey Clinton Iowa Pulaski Des Moines Jasper Putnam Dubuque Jefferson Randolph Jackson Johnson Ripley Louisa Keokuk Rush Muscatine Lee Scott Scott Louisa Shelby Fish Lucas Spencer Shiner, Topeka Madison St. Joseph Notropis topeka (=tristis) Mahaska Starke Buena Vista Marion Steuben Calhoun Mills Sullivan Carroll Monroe Switzerland Dallas Montgomery Tippecanoe Greene Muscatine Tipton Hamilton Page Union Humboldt Polk Vanderburgh Kossuth Pottawattamie Vermillion Lyon Poweshiek Vigo Osceola Ringgold Wabash Sac Scott Warren Webster Taylor Warrick Wright Union Washington Sturgeon, Pallid Van Buren Wayne Scaphirhynchus albus Wapello Wells Fremont Warren White Harrison Washington Whitley Mills Wayne Reptile Monona Kansas Pottawattamie Snake, Northern Copperbelly Water Bird Nerodia erythrogaster neglecta Woodbury Bird Kosciusko Mammal Crane, Whooping Grus americana St. Joseph Bat, Indiana Steuben Myotis sodalis Barber Adair Barton

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218 Bird Bird Fish Clark Stafford Pottawatomie Cloud Sumner Riley Comanche Trego Shawnee Decatur Fish Wabaunsee Edwards Madtom, Neosho Wallace Ellis Noturus placidus Sturgeon, Pallid Ellsworth Allen Scaphirhynchus albus Finney Chase Atchison Ford Cherokee Doniphan Gove Coffey Douglas Graham Labette Johnson Gray Lyon Leavenworth Harper Marion Wyandotte Harvey Morris Mammal Haskell Neosho Bat, Gray Hodgeman Woodson Myotis grisescens Jewell Shiner, Arkansas River Crawford Kingman Notropis girardi Kentucky Kiowa Clark Lane Comanche Bivalve Lincoln Gray Fanshell McPherson Haskell Cyprogenia stegaria Meade Kearny Allen Mitchell Kiowa Barren Ness Meade Boyd Norton Morton Boyle Osborne Pawnee Bracken Ottawa Sedgwick Butler Pawnee Seward Campbell Phillips Stevens Carter Pratt Cumberland Shiner, Topeka Cumberland Rawlins Notropis topeka (=tristis) Edmonson Reno Butler Fleming Republic Chase Green Rice Dickinson Greenup Rooks Douglas Hart Rush Geary Henderson Russell Greenwood Henry Saline Jefferson Jefferson Scott Lyon Kenton Sedgwick Marion Larue Seward Marshall Lawrence Sheridan Morris Livingston Smith Osage Lyon

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219 Bivalve Bivalve Bivalve Marion Mussel, Clubshell Wayne Mason Pleurobema clava Mussel, Cumberland Elktoe Mercer Allen Alasmidonta atropurpurea Monroe Bath Laurel Muhlenberg Boyle McCreary Nelson Bracken Rockcastle Nicholas Bullitt Whitley Ohio Butler Mussel, Oyster Owen Campbell Epioblasma capsaeformis Pendleton Cumberland Cumberland Powell Edmonson Laurel Russell Gallatin McCreary Spencer Grayson Pulaski Todd Green Russell Warren Harrison Wayne Wayne Hart Whitley Woodford Jefferson Mussel, Ring Pink (=Golf Stick Pearly) Mucket, Pink (Pearlymussel) Kenton Obovaria retusa Lampsilis abrupta Livingston Ballard Bath Lyon Boone Boone Marshall Butler Butler Mason Campbell Campbell McCreary Carroll Carroll Meade Cumberland Cumberland Mercer Edmonson Edmonson Nelson Greenup Greenup Owen Hart Hart Pendleton Henderson Henderson Pulaski Jefferson Jefferson Robertson Kenton Kenton Rockcastle Livingston Livingston Spencer Lyon Lyon Taylor Marshall Marshall Warren McCracken McCracken Woodford Mercer Monroe Mussel, Cumberland Combshell Monroe Ohio Epioblasma brevidens Pulaski Pendleton Cumberland Russell Pulaski Hart Todd Russell Laurel Trigg Spencer McCreary Warren Warren Pulaski Wayne Wayne Rockcastle Woodford Russell

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220 Bivalve Bivalve Bivalve Mussel, Rough Pigtoe Wayne Rockcastle Pleurobema plenum Pearlymussel, Cumberland Bean Todd Butler Villosa trabalis Wayne Campbell Clinton Pearlymussel, Orange-footed Clinton Cumberland Plethobasus cooperianus Cumberland Jackson Ballard Edmonson Laurel Bullitt Green Lincoln Butler Hart McCreary Campbell Kenton Pulaski Carroll Marshall Rockcastle Clinton Mercer Russell Crittenden Monroe Wayne Cumberland Pendleton Whitley Grayson Pulaski Pearlymussel, Dromedary Hancock Russell Dromus dromas Jefferson Taylor Clinton Kenton Warren Cumberland Livingston Wayne McCreary Lyon Woodford Monroe Marshall Mussel, Winged Mapleleaf Pulaski McCracken Quadrula fragosa Russell Monroe Kenton Wayne Ohio Lyon Pearlymussel, Fat Pocketbook Russell Oldham Potamilus capax Trigg Pendleton Butler Trimble Trigg Crittenden Warren Pearlymussel, Appalachian Edmonson Wayne Monkeyface Green Pearlymussel, Purple Cat's Paw Quadrula sparsa Hart Epioblasma obliquata obliquata Cumberland Henderson Butler Pulaski Jefferson Cumberland Pearlymussel, Cracking Livingston Hart Hemistena lata McCracken Henderson Carroll Taylor Kenton Cumberland Union Muhlenberg Edmonson Warren Ohio Hart Pulaski Pearlymussel, Little-wing Pulaski Jefferson Pegias fabula Warren Kenton Jackson Pearlymussel, Tubercled- blossom McCreary Laurel Epioblasma torulosa torulosa Monroe Logan Campbell Pulaski McCreary Edmonson Russell Pulaski Green

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221 Bivalve Bivalve Mammal Hart Logan Bullitt Henderson McCreary Calloway Kenton Pulaski Carter McCracken Russell Christian Nelson Simpson Clark Pendleton Wayne Clinton Taylor Crustacean Crittenden Warren Shrimp, Kentucky Cave Edmonson Pearlymussel, White Wartyback Palaemonias ganteri Fayette Plethobasus cicatricosus Barren Franklin Campbell Edmonson Garrard Carroll Hart Graves Gallatin Fish Grayson Henderson Green Dace, Blackside Kenton Phoxinus cumberlandensis Hardin Livingston Harlan Bell Todd Hart Harlan Pearlymussel, Yellow-blossom Knox Hopkins Epioblasma florentina florentina Jefferson Laurel Cumberland Letcher Jessamine Pulaski McCreary Lee Russell Pulaski Livingston Todd Whitley Logan Riffleshell, Northern Meade Darter, Relict Menifee Epioblasma torulosa rangiana Menifee Etheostoma chienense Bath Graves Metcalfe Edmonson Hickman Monroe Franklin Muhlenberg Shiner, Palezone Nelson Grayson Notropis albizonatus Nelson Green Pulaski Cumberland Hart Simpson McCreary Kenton Taylor Wayne Mercer Todd Nelson Sturgeon, Pallid Trigg Scaphirhynchus albus Pendleton Warren Ballard Rowan Wayne Hickman Spencer Bat, Indiana Mammal Bat, Indiana Taylor Myotis sodalis Warren Bat, Gray Adair Woodford Myotis grisescens Allen Adair Ballard Riffleshell, Tan Ballard Epioblasma florentina walkeri (=E. Allen Barren walkeri) Barren Bath Cumberland Breckinridge Breckinridge

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222 Mammal Mammal Fish Bullitt Corynorhinus (=Plecotus) townsendii Tangipahoa Caldwell Vermilion Calloway Estill Washington Carlisle Jackson Sturgeon, Pallid Carter Lee Scaphirhynchus albus Christian Menifee Ascension Daviess Morgan Avoyelles Edmonson Powell Bossier Elliott Rockcastle Caddo Estill Rowan Catahoula Fayette Wolfe Concordia Fulton Louisiana East Baton Rouge Grayson Bivalve East Carroll Hardin East Feliciana Harlan Mucket, Pink (Pearlymussel) Grant Lampsilis abrupta Hart Iberia Morehouse Henderson Iberville Hickman Mussel, Heelsplitter Inflated Madison Potamilus inflatus Jackson Natchitoches Ascension Jefferson Pointe Coupee East Baton Rouge Jessamine Rapides East Feliciana Lee Red River Livingston Letcher St. Charles St. Helena Livingston St. James Logan Pearlshell, Louisiana St. John the Baptist Margaritifera hembeli Mason St. Landry McCracken Grant St. Martin McCreary Rapides St. Mary Meade Fish Tensas Menifee Sturgeon, Gulf West Baton Rouge Montgomery Acipenser oxyrinchus desotoi West Feliciana Morgan Ascension Winn Pike Cameron Mammal Powell East Baton Rouge Manatee, West Indian Pulaski Iberia Trichechus manatus Rockcastle Iberville Ascension Rowan LaFourche Cameron Taylor Livingston East Baton Rouge Trigg St. Charles LaFourche Union St. Helena Livingston Warren St. James St. Charles Whitley St. John the Baptist St. James Wolfe St. Mary St. John the Baptist Bat, Virginia Big-eared St. Tammany St. Tammany 223 Mammal Reptile Bivalve Tangipahoa Turtle, Bog Wayne Reptile Clemmys muhlenbergii Mammal Turtle, Ringed Map Baltimore Bat, Indiana Graptemys oculifera Carroll Myotis sodalis St. Tammany Cecil Allegan Washington Harford Barry Maine Massachusetts Bay Fish Bivalve Benzie Berrien Salmon, Atlantic Mussel, Dwarf Wedge Branch Salmo salar Alasmidonta heterodon Calhoun Hancock Franklin Cass Kennebec Hampshire Clinton Knox Fish Eaton Lincoln Sturgeon, Shortnose Genesee Penobscot Acipenser brevirostrum Gratiot Sagadahoc Essex Hillsdale Waldo Franklin Huron Washington Hampden Ingham Sturgeon, Shortnose Hampshire Ionia Acipenser brevirostrum Middlesex Jackson Kennebec Mammal Kalamazoo Penobscot Bat, Indiana Kent Maryland Myotis sodalis Lapeer Bivalve Berkshire Leelanau Reptile Lenawee Mussel, Dwarf Wedge Livingston Alasmidonta heterodon Turtle, Bog Clemmys muhlenbergii Macomb Caroline Manistee Charles Berkshire Manistee Mason Queen Annes Turtle, Plymouth Red-bellied St. Marys Pseudemys rubriventris bangsi Monroe Fish Barnstable Montcalm Bristol Muskegon Darter, Maryland Plymouth Oakland Etheostoma sellare Oceana Harford Michigan Ottawa Mammal Bivalve Saginaw Bat, Indiana Mussel, Clubshell Sanilac Myotis sodalis Pleurobema clava Shiawassee Allegany Hillsdale St. Clair Carroll Riffleshell, Northern St. Joseph Garrett Epioblasma torulosa rangiana Tuscola Washington Monroe Van Buren Reptile Sanilac Washtenaw 12/21/2011 2:57:18 PM Ver. 2.2.0 Page 26 of 64

224 Mammal Bird Bivalve Wayne Crane, Mississippi Sandhill Lowndes Reptile Grus canadensis pulla Monroe Snake, Northern Copperbelly Water Jackson Pearlymussel, Fat Pocketbook Nerodia erythrogaster neglecta Bivalve Potamilus capax Branch Combshell, Southern (=Penitent Adams Calhoun mussel) Bolivar Cass Epioblasma penita Claiborne Eaton Itawamba Coahoma Hillsdale Lowndes De Soto St. Joseph Monroe Issaquena Minnesota Mucket, Orange-nacre Jefferson Lampsilis perovalis Sharkey Bivalve Itawamba Tunica Mussel, Winged Mapleleaf Lowndes Warren Quadrula fragosa Monroe Washington Chisago Mussel, Alabama Moccasinshell Wilkinson Washington Medionidus acutissimus Yazoo Pearlymussel, Higgins' Eye Lowndes Fish Lampsilis higginsii Monroe Darter, Bayou Chisago Mussel, Black (=Curtus' Mussel) Etheostoma rubrum Dakota Clubshell Claiborne Pleurobema curtum Goodhue Copiah Hennepin Itawamba Hinds Houston Monroe Sturgeon, Gulf Ramsey Mussel, Cumberland Combshell Acipenser oxyrinchus desotoi Wabasha Epioblasma brevidens Clarke Washington Tishomingo Copiah Winona Mussel, Heavy Pigtoe (=Judge Tait's Forrest Mussel) Forrest Fish Pleurobema taitianum George Shiner, Topeka Itawamba Greene Notropis topeka (=tristis) Lowndes Hancock Lincoln Monroe Harrison Murray Mussel, Heelsplitter Inflated Hinds Nobles Potamilus inflatus Jackson Pipestone Hancock Jones Rock Pearl River Lawrence Mississippi Mussel, Ovate Clubshell Marion Pleurobema perovatum Pearl River Amphibian Perry Itawamba Perry Frog, Dusky Gopher (Mississippi DPS) Lowndes Pike Rana capito sevosa Rankin Monroe Rankin Harrison Simpson Mussel, Southern Clubshell Jackson Pleurobema decisum Wayne Bird Itawamba 12/21/2011 2:57:18 PM Ver. 2.2.0 Page 27 of 64

225 Fish Reptile Bivalve Sturgeon, Pallid Simpson Pearlymussel, Curtis' Scaphirhynchus albus Turtle, Yellow-blotched Map Epioblasma florentina curtisii Adams Graptemys flavimaculata Bollinger Bolivar Clarke Butler Claiborne Forrest Ripley Coahoma George Wayne De Soto Greene Pearlymussel, Fat Pocketbook Issaquena Jackson Potamilus capax Jefferson Jones Clark Sharkey Perry Dunklin Tunica Stone Marion Warren Wayne Mississippi Washington Missouri Pike Wilkinson Ralls Yazoo Bivalve Pearlymussel, Higgins' Eye Mammal Mucket, Pink (Pearlymussel) Lampsilis higginsii Lampsilis abrupta Maries Bat, Gray Maries Myotis grisescens Butler Marion Tishomingo Cedar Fish Cole Bat, Indiana Cavefish, Ozark Myotis sodalis Franklin Cavefish, Ozark Amblyopsis rosae Gasconade Tishomingo Barry Jefferson Manatee, West Indian Greene Miller Trichechus manatus Jasper Osage Hancock Lawrence Ripley Harrison Newton St. Clair Jackson Stone St. Louis Reptile Wayne Darter, Niangua Etheostoma nianguae Turtle, Alabama Red-bellied Mussel, Scaleshell Benton Pseudemys alabamensis Leptodea leptodon Benton Harrison Crawford Camden Jackson Franklin Cedar Turtle, Ringed Map Gasconade Dallas Graptemys oculifera Jefferson Greene Copiah La clede Hickory Hinds Maries Miller Lawrence Osage Osage Leake Pulaski St. Clair Madison St. Louis Webster Marion Wright Madtom, Neosho Neshoba Noturus placidus Mussel, Winged Mapleleaf Jasper Pearl River Quadrula fragosa Jasper Rankin Franklin Shiner, Topeka Scott Notropis topeka (=tristis)

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226 Fish Gastropod Mammal Boone Cavesnail, Tumbling Creek Washington Clark Antrobia culveri Wright Cooper Taney Bat, Indiana Daviess Mammal Myotis sodalis Grundy Bat, Gray Adair Harrison Myotis grisescens Andrew Moniteau Barry Atchison Pettis Benton Audrain Putnam Boone Boone Sturgeon, Pallid Camden Buchanan Scaphirhynchus albus Carter Caldwell Andrew Christian Callaway Atchison Cole Camden Boone Crawford Carroll Buchanan Dade Chariton Callaway Dallas Christian Cape Girardeau Dent Clark Chariton Douglas Clay Clay Franklin Clinton Cole Greene Cooper Cooper Hickory Crawford Franklin Iron Daviess Gasconade Jasper De Kalb Holt Jefferson Franklin Howard La clede Gentry Jackson Lawrence Grundy Lafayette Maries Harrison Lewis McDonald Henry Livingston Miller Holt Mississippi Morgan Howard Moniteau Newton Iron Montgomery Oregon Jefferson New Madrid Osage Knox Osage Ozark La clede Pemiscot Phelps Lewis Perry Pike Lincoln Platte Pulaski Linn Polk Ralls Livingston Ray Reynolds Macon Saline Shannon Madison St. Charles St. Louis Marion St. Louis Stone Mercer Ste. Genevieve Taney Mississippi Warren Texas Monroe

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227 Mammal Fish Bird Montgomery Sturgeon, Pallid Box Butte Nodaway Scaphirhynchus albus Boyd Oregon Blaine Brown Phelps Chouteau Buffalo Pike Custer Chase Platte Dawson Cherry Pulaski Fergus Cheyenne Putnam Garfield Clay Ralls McCone Custer Randolph Petroleum Dawes Ray Phillips Dawson Schuyler Prairie Deuel Scotland Richland Dundy Shannon Roosevelt Fillmore Shelby Valley Franklin St. Charles Wibaux Frontier St. Francois Sturgeon, White Furnas St. Louis Acipenser transmontanus Garden Stone Lincoln Garfield Sullivan Trout, Bull Gosper Taney Salvelinus confluentus Grant Texas Deer Lodge Greeley Warren Flathead Hall Washington Glacier Hamilton Worth Granite Harlan Wright Lake Hayes Montana Lewis and Clark Hitchcock Lincoln Holt Bird Mineral Howard Crane, Whooping Missoula Kearney Grus americana Powell Keith Custer Ravalli Keya Paha Daniels Sanders Kimball Dawson Knox Nebraska Knox Fallon Lincoln McCone Bird Logan Phillips Crane, Whooping Loup Prairie Grus americana McPherson Richland Adams Merrick Roosevelt Antelope Morrill Sheridan Arthur Nance Valley Banner Nuckolls Wibaux Blaine Perkins Yellowstone Boone Phelps

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228 Bird Fish Fish Red Willow Chub, Virgin River Springfish, White River Rock Gila seminuda (=robusta) Crenichthys baileyi baileyi Saline Clark Lincoln Scotts Bluff Cui-ui Sucker, Razorback Sheridan Chasmistes cujus Xyrauchen texanus Sherman Washoe Clark Sioux Dace, Ash Meadows Speckled Sucker, Warner Thayer Rhinichthys osculus nevadensis Catostomus warnerensis Thomas Nye Washoe Valley Dace, Clover Valley Speckled Trout, Bull Webster Rhinichthys osculus oligoporus Salvelinus confluentus Wheeler Elko Elko York Dace, Desert Trout, Lahontan Cutthroat Fish Eremichthys acros Oncorhynchus clarki henshawi Shiner, Topeka Humboldt Carson City Notropis topeka (=tristis) Dace, Independence Valley Speckled Churchill Cherry Rhinichthys osculus lethoporus Clark Madison Elko Douglas Sturgeon, Pallid Dace, Moapa Elko Scaphirhynchus albus Moapa coriacea Humboldt Boyd Clark Lyon Burt Pupfish, Ash Meadows Amargosa Nye Cass Cyprinodon nevadensis mionectes Washoe Cedar Nye Woundfin Dakota Pupfish, Devils Hole Plagopterus argentissimus Dixon Cyprinodon diabolis Clark Douglas Clark New Hampshire Knox Nye Nemaha Pupfish, Warm Springs Bivalve Otoe Cyprinodon nevadensis pectoralis Mussel, Dwarf Wedge Richardson Nye Alasmidonta heterodon Sarpy Spinedace, Big Spring Cheshire Saunders Lepidomeda mollispinis pratensis Coos Thurston Lincoln Grafton Washington Spinedace, White River Sullivan Nevada Lepidomeda albivallis New Jersey Nye Bivalve Fish White Pine Bivalve Chub, Humpback Springfish, Hiko White River Mussel, Dwarf Wedge Gila cypha Crenichthys baileyi grandis Alasmidonta heterodon Clark Lincoln Bergen Sussex Chub, Pahranagat Roundtail Springfish, Railroad Valley Warren Gila robusta jordani Crenichthys nevadae Warren Lincoln Nye Mammal

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229 Mammal Amphibian Fish Bat, Indiana Socorro Shiner, Beautiful Myotis sodalis Crustacean Cyprinella formosa Bergen Amphipod, Noel's Grant Essex Gammarus desperatus Luna Hunterdon Chaves Shiner, Pecos Bluntnose Mercer Isopod, Socorro Notropis simus pecosensis Middlesex Thermosphaeroma thermophilus Chaves Morris Socorro De Baca Passaic Fish Eddy Somerset Spikedace Sussex Chub, Chihuahua Meda fulgida Gila nigrescens Union Catron Grant Catron Warren Grant Reptile Chub, Gila Hidalgo Gila intermedia Hidalgo Turtle, Bog Grant Squawfish, Colorado Clemmys muhlenbergii Ptychocheilus lucius Gambusia, Pecos Atlantic Gambusia nobilis San Juan Burlington Chaves Sucker, Razorback Camden Eddy Xyrauchen texanus Cape May San Juan Minnow, Loach Cumberland Tiaroga cobitis Topminnow, Gila (Yaqui) Gloucester Catron Poeciliopsis occidentalis Hunterdon Grant Grant Mercer Hidalgo Trout, Gila Middlesex Oncorhynchus gilae Minnow, Rio Grande Silvery Monmouth Hybognathus amarus Catron Morris Bernalillo Grant Ocean Dona Ana Sierra Passaic Rio Arriba Gastropod Salem Sandoval Snail, Pecos Assiminea Somerset Santa Fe Assiminea pecos Sussex Sierra Chaves Union Socorro Springsnail, Alamosa Warren Valencia Tryonia alamosae New Mexico Shiner, Arkansas River Socorro Amphibian Notropis girardi Springsnail, Roswell Colfax Pyrgulopsis roswellensis Frog, Chiricahua Leopard Chaves Harding Chaves Rana chiricahuensis Mora Springsnail, Socorro Catron Pyrgulopsis neomexicana Quay Pyrgulopsis neomexicana Grant San Miguel Socorro Hidalgo Union Mammal Luna Sierra

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230 Mammal Mammal Reptile Bat, Lesser (=Sanborn's) Long-nosed Clinton Seneca Leptonycteris curasoae yerbabuenae Columbia Sullivan Hidalgo Dutchess Tompkins Bat, Mexican Long-nosed Essex Ulster Leptonycteris nivalis Greene Warren Hidalgo Jefferson Wayne New York Lewis Westchester Madison North Carolina Bivalve Oneida North Carolina Mussel, Clubshell Onondaga Bivalve Pleurobema clava Orange Elktoe, Appalachian Cattaraugus Oswego Alasmidonta raveneliana Chautauqua Putnam Buncombe Mussel, Dwarf Wedge Rensselaer Graham Alasmidonta heterodon Rockland Haywood Delaware Saratoga Henderson Dutchess Schenectady Jackson Orange Schoharie Macon Sullivan Seneca Mitchell Fish St. Lawrence Swain Sturgeon, Shortnose Sullivan Transylvania Acipenser brevirostrum Ulster Yancey Albany Warren Mussel, Dwarf Wedge Columbia Washington Alasmidonta heterodon Dutchess Wayne Franklin Greene Westchester Granville Nassau Reptile Halifax Orange Turtle, Bog Johnston Putnam Clemmys muhlenbergii Nash Queens Albany Orange Rensselaer Cayuga Person Rockland Columbia Vance Suffolk Dutchess Wake Ulster Genesee Warren Westchester Monroe Wilson Gastropod Oneida Mussel, Heelsplitter Carolina Snail, Chittenango Ovate Amber Onondaga Lasmigona decorata Succinea chittenangoensis Ontario Anson Madison Orange Cabarrus Mammal Orleans Mecklenburg Oswego Richmond Bat, Indiana Union Myotis sodalis Otsego Union Albany Putnam Pearlymussel, Cumberland Bean Cayuga Rockland Villosa trabalis

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231 Bivalve Fish Mammal Cherokee Columbus Carteret Pearlymussel, Little-wing Sturgeon, Shortnose Craven Pegias fabula Acipenser brevirostrum Currituck Cherokee Anson Dare Macon Bertie Hyde Swain Bladen New Hanover Riffleshell, Tan Brunswick Onslow Epioblasma florentina walkeri (=E. Camden Pamlico walkeri) Carteret Pender Buncombe Currituck Pitt Cherokee Dare Reptile Spinymussel, James River Hyde Alligator, American Pleurobema collina New Hanover Alligator, American Alligator mississippiensis Caswell Onslow Bladen Rockingham Pamlico Brunswick Stokes Pasquotank Camden Spinymussel, Tar River Pender Carteret Elliptio steinstansana Mammal Columbus Edgecombe Craven Bat, Gray Craven Franklin Myotis grisescens Dare Halifax Duplin Buncombe Duplin Johnston Gates Haywood Gates Nash Hoke Madison Hoke Pitt Hyde Swain Hyde Warren Jones Fish Bat, Indiana Jones Myotis sodalis New Hanover Chub, Spotfin Cherokee Onslow Erimonax monachus Graham Pamlico Buncombe Haywood Pender Macon Jackson Robeson Madison Macon Sampson Swain Mitchell Scotland Logperch, Roanoke Rutherford Tyrrell Percina rex Swain Washington Rockingham Bat, Virginia Big-eared Turtle, Bog Shiner, Cape Fear Corynorhinus (=Plecotus) townsendii Clemmys muhlenbergii Notropis mekistocholas virginianus Alexander Chatham Avery Alleghany Harnett Watauga Ashe Lee Yancey Avery Moore Manatee, West Indian Buncombe Randolph Trichechus manatus Burke Silverside, Waccamaw Beaufort Caldwell Menidia extensa Brunswick Cherokee

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232 Reptile Bird Mammal Clay La Moure Tinian Island Davidson Logan Ohio Forsyth McHenry Gaston McIntosh Bivalve Graham McKenzie Fanshell Haywood McLean Cyprogenia stegaria Henderson Mercer Athens Iredell Morton Coshocton Jackson Mountrail Meigs Macon Oliver Morgan Madison Pierce Muskingum McDowell Renville Washington Mitchell Rolette Mucket, Pink (Pearlymussel) Surry Sheridan Lampsilis abrupta Swain Sioux Athens Transylvania Slope Gallia Watauga Stark Lawrence Wilkes Stutsman Meigs Yancey Towner Morgan North Dakota Ward Scioto Wells Washington Bird Williams Mussel, Clubshell Crane, Whooping Fish Pleurobema clava Grus americana Ashtabula Sturgeon, Pallid Adams Scaphirhynchus albus Champaign Barnes Burleigh Coshocton Benson Dunn Defiance Billings Emmons Delaware Bottineau McKenzie Fairfield Bowman McLean Franklin Burke Mercer Greene Burleigh Morton Hancock Cavalier Mountrail Hardin Dickey Oliver Madison Divide Sioux Pickaway Dunn Williams Pike Eddy Ross Emmons Northern Mariana Islands Scioto Foster Mammal Trumbull Golden Valley Bat, Mariana Fruit (=Mariana Flying Fox) Union Grant Williams Griggs Pteropus mariannus mariannus Pearlymussel, Purple Cat's Paw Hettinger Rota Island Epioblasma obliquata obliquata Kidder Saipan Island Coshocton

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233 Bivalve Mammal Mammal Pearlymussel, White Cat's Paw Defiance Perry Epioblasma obliquata perobliqua Delaware Pickaway Defiance Erie Pike Williams Fairfield Portage Riffleshell, Northern Fayette Preble Epioblasma torulosa rangiana Franklin Putnam Defiance Fulton Richland Franklin Gallia Ross Madison Geauga Sandusky Pickaway Greene Scioto Pike Guernsey Seneca Ross Hamilton Shelby Scioto Hancock Stark Union Hardin Summit Williams Harrison Trumbull Fish Henry Tuscarawas Highland Union Madtom, Scioto Noturus trautmani Hocking Van Wert Franklin Holmes Vinton Madison Huron Warren Pickaway Jackson Washington Union Jefferson Wayne Mammal Knox Williams Lake Wood Bat, Indiana Lawrence Wyandot Myotis sodalis Licking Reptile Adams Logan Snake, Lake Erie Water Allen Snake, Lake Erie Water Lorain Nerodia sipedon insularum Ashland Nerodia sipedon insularum Lucas Erie Ashtabula Erie Madison Ottawa Athens Ottawa Mahoning Snake, Northern Copperbelly Water Auglaize Snake, Northern Copperbelly Water Marion Nerodia erythrogaster neglecta Belmont Nerodia erythrogaster neglecta Medina Defiance Brown Defiance Meigs Hardin Butler Hardin Mercer Williams Carroll Williams Miami Champaign Oklahoma Monroe Clark Montgomery Bird Clermont Morgan Crane, Whooping Clinton Crane, Whooping Morrow Grus americana Columbiana Muskingum Alfalfa Coshocton Noble Atoka Crawford 234 Ottawa Beaver Cuyahoga Paulding Beckham Darke

Bird Bird Fish Bryan Rogers Ottawa Caddo Seminole Shiner, Arkansas River Canadian Stephens Notropis girardi Carter Texas Beaver Cleveland Tillman Blaine Coal Wagoner Caddo Comanche Washington Canadian Cotton Washita Cleveland Custer Woods Custer Dewey Woodward Dewey Ellis Bivalve Ellis Garfield Mussel, Scaleshell Grady Garvin Leptodea leptodon Harper Grady Choctaw Hughes Grant Le Flore Kingfisher Greer McCurtain Logan Harmon Pushmataha Major Harper Mussel, Winged Mapleleaf McClain Hughes Quadrula fragosa McIntosh Jackson Choctaw Pittsburg Jefferson Le Flore Pontotoc Johnston McCurtain Pottawatomie Kay Ottawa Roger Mills Kingfisher Pushmataha Seminole Kiowa Woods Rock-pocketbook, Ouachita Lincoln (=Wheeler's pm) Woodward Logan Arkansia wheeleri Mammal Love Le Flore Bat, Gray Major McCurtain Myotis grisescens Marshall Pushmataha Adair McClain Fish Cherokee McIntosh Cavefish, Ozark Craig Murray Amblyopsis rosae Delaware Muskogee Delaware Mayes Noble Mayes Muskogee Okfuskee Ottawa Ottawa Oklahoma Darter, Leopard Sequoyah Okmulgee Percina pantherina Wagoner Osage Le Flore Bat, Indiana Pawnee McCurtain Myotis sodalis Payne Pushmataha Adair Pontotoc Madtom, Neosho Delaware Pottawatomie Noturus placidus Le Flore Roger Mills Craig Pushmataha

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235 Mammal Fish Fish Sequoyah Lake Wasco Bat, Ozark Big-eared Chub, Oregon Washington Corynorhinus (=Plecotus) townsendii Oregonichthys crameri Wheeler ingens Benton Yamhill Adair Lane Salmon, Chum Cherokee Linn Oncorhynchus (=Salmo) keta Delaware Marion Clatsop Ottawa Polk Columbia Sequoyah Multnomah Dace, Foskett Speckled Multnomah Reptile Rhinichthys osculus ssp. Salmon, Coho Alligator, American Lake Oncorhynchus (=Salmo) kisutch Alligator mississippiensis Salmon, Chinook Benton McCurtain Oncorhynchus (=Salmo) tshawytscha Clackamas Oregon Baker Clatsop Benton Columbia Bird Clackamas Coos Albatross, Short-tailed Clatsop Curry Phoebastria (=Diomedea) albatrus Columbia Douglas Clatsop Coos Hood River Coos Crook Jackson Curry Curry Josephine Douglas Deschutes Klamath Lane Douglas Lane Lincoln Gilliam Lincoln Murrelet, Marbled Grant Marion Brachyramphus marmoratus Harney Multnomah Benton Hood River Polk Clatsop Jackson Wasco Coos Jefferson Washington Curry Josephine Yamhill Douglas Klamath Salmon, Sockeye Lane Lake Oncorhynchus (=Salmo) nerka Lincoln Lane Baker Polk Lincoln Benton Crustacean Linn Clackamas Fairy Shrimp, Vernal Pool Malheur Clatsop Branchinecta lynchi Marion Columbia Jackson Morrow Coos Fish Multnomah Curry Chub, Borax Lake Polk Douglas Gila boraxobius Sherman Gilliam Harney Umatilla Hood River Chub, Hutton Tui Union Jackson Gila bicolor ssp. Wallowa Josephine

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236 Fish Fish Mammal Lane Sucker, Shortnose Grant Lincoln Chasmistes brevirostris Harney Linn Klamath Hood River Marion Lake Jackson Morrow Sucker, Warner Jefferson Multnomah Catostomus warnerensis Josephine Polk Lake Klamath Sherman Trout, Bull Lake Umatilla Salvelinus confluentus Lane Union Baker Lincoln Wallowa Crook Linn Wasco Deschutes Malheur Washington Grant Marion Yamhill Harney Morrow Steelhead Hood River Multnomah Oncorhynchus (=Salmo) mykiss Jefferson Polk Benton Klamath Sherman Clackamas Lake Umatilla Clatsop Lane Union Columbia Linn Wallowa Crook Malheur Wasco Gilliam Umatilla Washington Grant Union Wheeler Hood River Wallowa Yamhill Jefferson Wasco Pennsylvania Linn Wheeler Marion Trout, Lahontan Cutthroat Bivalve Morrow Oncorhynchus clarki henshawi Mussel, Clubshell Multnomah Harney Pleurobema clava Polk Malheur Armstrong Sherman Mammal Clarion Umatilla Crawford Whale, Gray Erie Union Eschrichtius robustus Erie Wallowa Baker Forest Wasco Benton Mercer Washington Clackamas Venango Wheeler Clatsop Warren Yamhill Columbia Mussel, Dwarf Wedge Alasmidonta heterodon Sucker, Lost River Coos Deltistes luxatus Crook Pike Klamath Curry Wayne Sucker, Modoc Deschutes Riffleshell, Northern Catostomus microps Douglas Epioblasma torulosa rangiana Lake Gilliam Armstrong

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237 Bivalve Puerto Rico Coral Clarion Maunabo Amphibian Maunabo Crawford Mayaguez Erie Coqui, Golden Naguabo Eleutherodactylus jasperi Forest Patillas Mercer Adjuntas Penuelas Venango Cayey Ponce Warren Salinas Quebradillas Mammal Guajon Rincon Eleutherodactylus cooki Bat, Indiana Humacao Rio Grande Myotis sodalis Salinas Juncos Santa Isabel Adams Santa Isabel Las Piedras Vega Baja Armstrong Vega Baja Maunabo Yabucoa Beaver Yabucoa Patillas Yauco Bedford Yauco San Lorenzo Berks Coral, Staghorn Yabucoa Acropora cervicornis Blair Acropora cervicornis Centre Toad, Puerto Rican Crested Aguada Peltophryne lemur Fayette Anasco Arecibo Arecibo Greene Arecibo Coamo Camuy Huntingdon Camuy Guanica Carolina Lawrence Carolina Guayanilla Dorado Luzerne Dorado Isabela Guanica Mifflin Guanica Quebradillas Guayama Somerset Guayama Santa Isabel Guayanilla York Guayanilla Yauco Hatillo Reptile Coral Hatillo Humacao Turtle, Bog Clemmys muhlenbergii Coral, Elkhorn Isabela Acropora palmata Juana Diaz Adams Aguada Lajas Berks Anasco Manati Bucks Arecibo Maunabo Chester Camuy Mayaguez Cumberland Carolina Naguabo Delaware Dorado Patillas Franklin Guanica Penuelas Lancaster Guayama Ponce Lebanon Guayanilla Quebradillas Lehigh Hatillo Rincon 238 Monroe Humacao Rio Grande Montgomery Isabela Salinas Northampton Juana Diaz Santa Isabel Schuylkill Lajas Vega Baja York Manati Yabucoa

12/21/2011 2:57:20 PM Ver. 2.2.0 Page 40 of 64 Coral Reptile Fish Yauco Sea turtle, loggerhead Allendale Mammal Caretta caretta Barnwell Manatee, West Indian Puerto Rico Beaufort Trichechus manatus Rhode Island Berkeley Aguada Calhoun Fish Charleston Anasco Charleston Arecibo Sturgeon, Shortnose Chesterfield Acipenser brevirostrum Clarendon Camuy Clarendon Carolina Bristol Colleton Dorado Kent Darlington Guanica Newport Dillon Guayama Providence Dorchester Guayanilla Washington Florence Hatillo South Carolina Georgetown Humacao Amphibian Hampton Isabela Horry Juana Diaz Salamander, Frosted Flatwoods Jasper Ambystoma cingulatum Lexington Lajas Lexington Beaufort Marion Manati Marion Charleston Marlboro Maunabo Marlboro Jasper Orangeburg Mayaguez Orangeburg Orangeburg Richland Naguabo Richland Bivalve Sumter Patillas Sumter Penuelas Mussel, Heelsplitter Carolina Williamsburg Ponce Lasmigona decorata Mammal Quebradillas Abbeville Manatee, West Indian Rincon Chester Trichechus manatus Rio Grande Chesterfield Beaufort Salinas Edgefield Berkeley Santa Isabel Fairfield Charleston Vega Baja Greenwood Georgetown Yabucoa Kershaw Horry Yauco Lancaster Jasper Reptile Laurens Reptile Lexington Sea turtle, green McCormick Turtle, Bog Chelonia mydas Clemmys muhlenbergii Newberry Puerto Rico Greenville Richland Sea turtle, hawksbill Saluda Pickens Eretmochelys imbricata South Dakota York South Dakota Puerto Rico Fish Bird 239 Sea turtle, leatherback Dermochelys coriacea Sturgeon, Shortnose Crane, Whooping Acipenser brevirostrum Grus americana Puerto Rico Grus americana Aiken Aurora

12/21/2011 2:57:20 PM Ver. 2.2.0 Page 41 of 64 Bird Bivalve Fish Beadle Pearlymussel, Higgins' Eye Gregory Bennett Lampsilis higginsii Hughes Brule Yankton Potter Buffalo Fish Stanley Butte Shiner, Topeka Sully Campbell Notropis topeka (=tristis) Union Charles Mix Aurora Walworth Clark Beadle Yankton Codington Brookings Tennessee Corson Brown Dewey Clark Bivalve Douglas Clay Combshell, Upland Edmunds Codington Epioblasma metastriata Faulk Corson Bradley Gregory Davison Polk Haakon Deuel Elktoe, Appalachian Hand Dewey Alasmidonta raveneliana Hughes Grant Unicoi Hyde Hamlin Fanshell Jackson Hanson Cyprogenia stegaria Jerauld Hutchinson Anderson Jones Jerauld Decatur Kingsbury Kingsbury Hancock Lawrence Lake Hardin Lyman Lincoln Meigs McPherson McCook Rhea Meade Miner Kidneyshell, Triangular Mellette Minnehaha Ptychobranchus greenii Pennington Moody Bradley Perkins Sanborn Polk Potter Spink Mucket, Pink (Pearlymussel) Shannon Turner Lampsilis abrupta Spink Union Anderson Stanley Yankton Benton Sully Clay Sturgeon, Pallid Tripp Scaphirhynchus albus Decatur Walworth Bon Homme Grainger Ziebach Brule Greene Bivalve Buffalo Hamilton Mussel, Scaleshell Campbell Hancock Leptodea leptodon Charles Mix Hardin Clay Clay Humphreys Union Corson Jefferson Yankton Dewey Knox

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240 Bivalve Bivalve Bivalve Loudon Warren Decatur Marion White Hardin Meigs Mussel, Fine-lined Pocketbook Humphreys Montgomery Lampsilis altilis Trousdale Perry Bradley Mussel, Rough Pigtoe Pickett Polk Pleurobema plenum Rhea Mussel, Fine-rayed Pigtoe Anderson Roane Fusconaia cuneolus Cheatham Smith Anderson Claiborne Stewart Blount Davidson Sumner Claiborne Decatur Trousdale Cocke Dickson Wayne Franklin Grainger Wilson Grainger Hamilton Mussel, Alabama Moccasinshell Hamblen Hancock Medionidus acutissimus Hamilton Hardin Bradley Hancock Humphreys Mussel, Clubshell Hawkins Jefferson Pleurobema clava Jefferson Knox Hardin Knox Marion Mussel, Coosa Moccasinshell Moore Meigs Medionidus parvulus Roane Montgomery Bradley Sequatchie Perry Polk Sullivan Rhea Mussel, Cumberland Combshell Union Roane Epioblasma brevidens Mussel, Georgia pigtoe Sevier Claiborne Pleurobema hanleyianum Smith Davidson Polk Trousdale Hancock Mussel, Ovate Clubshell Union Jackson Pleurobema perovatum Wayne Marshall Bradley Mussel, Shiny Pigtoe Maury Mussel, Oyster Fusconaia cor Scott Epioblasma capsaeformis Anderson Trousdale Claiborne Campbell Mussel, Cumberland Elktoe Cocke Claiborne Alasmidonta atropurpurea Hamblen Franklin Claiborne Hancock Grainger Fentress Marshall Hancock Morgan Maury Hawkins Scott Scott Knox Mussel, Cumberland Pigtoe Sevier Lincoln Pleurobema gibberum Mussel, Ring Pink (=Golf Stick Pearly) Moore Grundy Obovaria retusa Roane Van Buren Benton Sullivan

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241 Bivalve Bivalve Bivalve Union Hancock Hamblen Mussel, Southern Pigtoe Hardin Hamilton Pleurobema georgianum Lincoln Hancock Bradley Wayne Jackson Polk Pearlymussel, Cumberland Bean Jefferson Pearlymussel, Alabama Lamp Villosa trabalis Knox Lampsilis virescens Bedford Marion Anderson Clay Meigs Franklin Cumberland Monroe Morgan Greene Montgomery Roane Hawkins Rhea Pearlymussel, Appalachian Knox Roane Monkeyface Pickett Smith Quadrula sparsa Polk Trousdale Claiborne Scott Pearlymussel, Green- blossom Grainger Union Epioblasma torulosa gubernaculum Hancock Anderson Pearlymussel, Cumberland Anderson Monroe Quadrula intermedia Campbell Roane Claiborne Claiborne Pearlymussel, Birdwing Franklin Grainger Conradilla caelata Grainger Greene Anderson Hamilton Hamblen Bedford Hancock Hancock Claiborne Hawkins Hawkins Giles Knox Jefferson Grainger Lincoln Knox Greene Marshall Sullivan Hamblen Maury Union Hancock Monroe Pearlymussel, Little-wing Hawkins Moore Pegias fabula Hickman Rhea Franklin Knox Roane Rutherford Lincoln Sullivan Scott Marshall Sullivan Pearlymussel, Dromedary Sullivan Maury Dromus dromas Van Buren Rhea Anderson Warren Roane Campbell Pearlymussel, Orange-footed Wayne Cheatham Plethobasus cooperianus Pearlymussel, Cracking Claiborne Anderson Hemistena lata Clay Bedford Anderson Davidson Benton Claiborne De Kalb Claiborne Giles Giles Clay Grainger Grainger Davidson

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242 Bivalve Bivalve Bivalve De Kalb Hamblen Franklin Decatur Hamilton Grainger Hamilton Knox Hancock Hardin Lincoln Jackson Humphreys Marshall Knox Jackson Sullivan Lincoln Knox Unicoi Marshall Loudon Washington Maury Marion Pearlymussel, Turgid-blossom Monroe Marshall Epioblasma turgidula Moore Maury Bedford Pickett Meigs Franklin Polk Montgomery Grainger Rutherford Perry Hawkins Smith Rhea Jefferson Purple Bean Roane Knox Villosa perpurpurea Sevier Lincoln Claiborne Smith Maury Cumberland Stewart Moore Hancock Trousdale Roane Hawkins Wayne Shelby Morgan Wilson Pearlymussel, White Wartyback Roane Pearlymussel, Pale Lilliput Plethobasus cicatricosus Rabbitsfoot, Rough Toxolasma cylindrellus Anderson Quadrula cylindrica strigillata Bedford Claiborne Claiborne Franklin Davidson Hancock Giles De Kalb Riffleshell, Tan Hickman Decatur Epioblasma florentina walkeri (=E. Lewis Grainger walkeri) Marion Hardin Anderson Marshall Jefferson Bedford Maury Marion Davidson Moore Meigs Franklin Perry Perry Grainger Wayne Rhea Jefferson Pearlymussel, Purple Cat's Paw Smith Knox Epioblasma obliquata obliquata Wayne Lincoln Smith Pearlymussel, Yellow-blossom Marshall Trousdale Epioblasma florentina florentina Maury Pearlymussel, Tubercled-blossom Anderson Monroe Epioblasma torulosa torulosa Bedford Montgomery Benton Cheatham Perry Davidson Claiborne Pickett Greene Clay Polk

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243 Bivalve Fish Fish Robertson Warren Madtom, Smoky Rutherford White Noturus baileyi Scott Darter, Boulder Blount Sullivan Etheostoma wapiti Monroe Crustacean Giles Madtom, Yellowfin Crayfish, Nashville Lincoln Noturus flavipinnis Orconectes shoupi Darter, Duskytail Anderson Davidson Etheostoma percnurum Blount Williamson Blount Claiborne Fish Monroe Hancock Scott Knox Chub, Slender Erimystax cahni Sullivan Monroe Anderson Darter, Slackwater Union Etheostoma boschungi Shiner, Blue Claiborne Shiner, Blue Grainger Lawrence Cyprinella caerulea Hamblen Lincoln Bradley Hancock Wayne Polk Union Darter, Snail Shiner, Palezone Percina tanasi Notropis albizonatus Chub, Spotfin Erimonax monachus Blount Campbell Blount Bradley Sturgeon, Pallid Claiborne Cocke Scaphirhynchus albus Cumberland Giles Dyer Fentress Greene Lake Hawkins Hamblen Gastropod Lewis Hamilton Riversnail, Anthony's Monroe Knox Athearnia anthonyi Morgan Loudon Anderson Rhea Marion Greene Roane McMinn Knox Sullivan Meigs Loudon Union Monroe Marion Polk Mammal Dace, Blackside Mammal Phoxinus cumberlandensis Sevier Bat, Gray Campbell Logperch, Conasauga Myotis grisescens Percina jenkinsi Claiborne Anderson Scott Bradley Bedford Polk Darter, Amber Benton Percina antesella Madtom, Pygmy Bledsoe Noturus stanauli Polk Campbell Hancock Darter, Bluemask (=jewel) Cannon Etheostoma sp. Hickman Cheatham Grundy Humphreys Claiborne Van Buren Clay 12/21/2011 2:57:20 PM Ver. 2.2.0 Page 46 of 64

244 Mammal Mammal Amphibian Cocke Toad, Houston De Kalb Bedford Bufo houstonensis Decatur Blount Austin Fentress Campbell Bastrop Franklin Cheatham Burleson Grainger Fentress Colorado Greene Franklin Lavaca Grundy Grainger Lee Hamilton Hawkins Leon Hancock Hickman Milam Hardeman Lincoln Robertson Hardin Marion Bird Hawkins Maury Crane, Mississippi Sandhill Hickman Monroe Grus canadensis pulla Houston Montgomery Hood Jackson Morgan Crane, Whooping Jefferson Perry Grus americana Knox Sevier Aransas Lawrence Shelby Archer Lincoln Stewart Atascosa Marion Van Buren Austin Maury Warren Bailey Meigs White Bastrop Montgomery Texas Baylor Moore Bee Overton Amphibian Bee Bell Perry Salamander, Barton Springs Bexar Putnam Eurycea sosorum Blanco Rhea Hays Bosque Roane Travis Brazoria Robertson Salamander, San Marcos Brazos Rutherford Eurycea nana Briscoe Sequatchie Comal Brown Smith Hays Burleson Stewart Kinney Burnet Sullivan Medina Caldwell Sumner Uvalde Calhoun Union Salamander, Texas Blind Callahan Van Buren Typhlomolge rathbuni Carson Warren Bexar Castro Wayne Hays Childress White Kinney Clay Wilson Medina Cochran Bat, Indiana Uvalde Coleman

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245 Bird Bird Bird Collin Kendall Travis Collingsworth Kent Uvalde Colorado King Victoria Comal Knox Waller Comanche Lamb Washington Concho Lampasas Wharton Coryell Lavaca Wheeler Cottle Lee Wichita Crosby Leon Wilbarger Dallas Limestone Williamson Dawson Lipscomb Wilson De Witt Live Oak Wise Deaf Smith Llano Yoakum Denton Lubbock Young Dickens Lynn Crustacean Donley Madison Amphipod, Peck's Cave Eastland Martin Stygobromus (=Stygonectes) pecki Ellis Matagorda Bexar Erath McCulloch Comal Falls McLennan Hays Fayette Milam Kinney Floyd Mills Medina Foard Montague Uvalde Fort Bend Motley Fish Freestone Navarro Garza Nueces Darter, Fountain Etheostoma fonticola Gillespie Oldham Bexar Goliad Palo Pinto Comal Gonzales Parker Hays Gray Parmer Kinney Grimes Potter Medina Guadalupe Randall Uvalde Hale Refugio Hall Robertson Gambusia, Big Bend Gambusia gaigei Hamilton San Patricio Brewster Hardeman San Saba Haskell Shackelford Gambusia, Clear Creek Gambusia heterochir Hays Somervell Menard Hemphill Stephens Hill Stonewall Gambusia, Pecos Gambusia nobilis Hockley Swisher Jeff Davis Jack Tarrant Pecos Jackson Terry Reeves Karnes Throckmorton

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246 Fish Mammal Fish Gambusia, San Marcos Nueces Duchesne Gambusia georgei Reptile Emery Bexar Snake, Concho Water Garfield Comal Nerodia paucimaculata Grand Hays Brown Kane Kinney Coke San Juan Medina Coleman Uintah Uvalde Irion Wayne Minnow, Devils River Lampasas Sucker, June Dionda diaboli McCulloch Chasmistes liorus Kinney Mills Box Elder Val Verde Mitchell Salt Lake Pupfish, Comanche Springs Runnels Utah Cyprinodon elegans San Saba Weber Jeff Davis Tom Green Sucker, Razorback Reeves Xyrauchen texanus Utah Uvalde Carbon Pupfish, Leon Springs Fish Duchesne Cyprinodon bovinus Chub, Bonytail Emery Pecos Gila elegans Garfield Shiner, Arkansas River Carbon Grand Notropis girardi Duchesne Kane Hemphill Emery San Juan Hutchinson Garfield Uintah Oldham Grand Wayne Potter San Juan Trout, Lahontan Cutthroat Roberts Uintah Oncorhynchus clarki henshawi Gastropod Wayne Box Elder Snail, Pecos Assiminea Chub, Humpback Woundfin Assiminea pecos Gila cypha Plagopterus argentissimus Pecos Carbon Washington Reeves Duchesne Gastropod Mammal Emery Ambersnail, Kanab Garfield Oxyloma haydeni kanabensis Bat, Mexican Long-nosed Grand Kane Leptonycteris nivalis Kane San Juan Mammal Brewster Mammal Uintah Presidio Prairie Dog, Utah Wayne Prairie Dog, Utah Manatee, West Indian Cynomys parvidens Trichechus manatus Chub, Virgin River Beaver Gila seminuda (=robusta) Aransas Garfield Washington Calhoun Iron Cameron Squawfish, Colorado Kane Ptychocheilus lucius Jackson Millard Carbon Kleberg Piute 12/21/2011 2:57:21 PM Ver. 2.2.0 Page 49 of 64

247 Mammal Bivalve Bivalve Sanpete Lee Washington Sevier Scott Wise Wayne Mussel, Dwarf Wedge Pearlymussel, Appalachian Vermont Alasmidonta heterodon Monkeyface Chesterfield Quadrula sparsa Bivalve Dinwiddie Lee Mussel, Dwarf Wedge Fauquier Scott Alasmidonta heterodon Franklin Pearlymussel, Birdwing Essex Greensville Conradilla caelata Orange Halifax Lee Windsor Hanover Russell Mammal King George Scott Bat, Indiana King William Washington Myotis sodalis Lunenburg Wise Addison Nottoway Pearlymussel, Cracking Bennington Prince William Hemistena lata Chittenden Spotsylvania Lee Rutland Stafford Russell Virgin Islands Sussex Scott Westmoreland Pearlymussel, Cumberland Bean Coral Mussel, Fine-rayed Pigtoe Villosa trabalis Coral, Elkhorn Fusconaia cuneolus Lee Acropora palmata Lee Russell St. Croix Russell Scott Coral, Staghorn Scott Tazewell Acropora cervicornis Tazewell Pearlymussel, Cumberland St. Croix Washington Quadrula intermedia Virginia Wise Lee Russell Amphibian Mussel, Oyster Scott Epioblasma capsaeformis Scott Salamander, Shenandoah Lee Washington Plethodon shenandoah Pearlymussel, Dromedary Russell Pearlymussel, Dromedary Madison Scott Dromus dromas Page Tazewell Lee Rappahannock Scott Mussel, Rough Pigtoe Bivalve Pleurobema plenum Pearlymussel, Green- blossom Fanshell Scott Epioblasma torulosa gubernaculum Cyprogenia stegaria Mussel, Shiny Pigtoe Scott Scott Fusconaia cor Pearlymussel, Little-wing Mucket, Pink (Pearlymussel) Lee Pegias fabula Lampsilis abrupta Russell Lee Scott Scott Russell Mussel, Cumberland Combshell Smyth Scott Epioblasma brevidens Tazewell Smyth

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248 Bivalve Bivalve Fish Tazewell Rockbridge Nottoway Washington Crustacean Patrick Purple Bean Isopod, Lee County Cave Pittsylvania Villosa perpurpurea Lirceus usdagalun Roanoke Lee Lee Southampton Russell Isopod, Madison Cave Sussex Scott Antrolana lira Madtom, Yellowfin Tazewell Augusta Noturus flavipinnis Washington Botetourt Lee Rabbitsfoot, Rough Page Russell Quadrula cylindrica strigillata Rockbridge Scott Lee Rockingham Smyth Russell Shenandoah Sturgeon, Shortnose Scott Warren Acipenser brevirostrum Tazewell Fish King George Washington Stafford Chub, Slender Riffleshell, Tan Erimystax cahni Mammal Epioblasma florentina walkeri (=E. walkeri) Lee Bat, Gray Russell Russell Myotis grisescens Smyth Scott Lee Tazewell Smyth Russell Washington Chub, Spotfin Scott Erimonax monachus Smyth Spinymussel, James River Tazewell Pleurobema collina Scott Tazewell Albemarle Smyth Washington Alleghany Washington Wise Amherst Dace, Blackside Bat, Indiana Bath Phoxinus cumberlandensis Myotis sodalis Botetourt Lee Albemarle Alleghany Carroll Darter, Duskytail Craig Etheostoma percnurum Amherst Floyd Scott Augusta Bath Fluvanna Logperch, Conasauga Franklin Percina jenkinsi Bedford Giles Greensville Bland Carroll Goochland Logperch, Roanoke Greene Percina rex Craig Henry Bedford Dickenson Highland Brunswick Floyd Nelson Dinwiddie Giles Patrick Franklin Grayson Pittsylvania Henry Greene Powhatan Mecklenburg Highland Montgomery Lee

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249 Mammal Bird Fish Madison Albatross, Short-tailed Grays Harbor Montgomery Phoebastria (=Diomedea) albatrus Island Nelson Clallam Jefferson Page Grays Harbor King Pulaski Jefferson Kitsap Rappahannock Pacific Kittitas Roanoke Murrelet, Marbled Klickitat Rockbridge Brachyramphus marmoratus Lewis Rockingham Chelan Lincoln Russell Clallam Mason Scott Cowlitz Okanogan Shenandoah Grays Harbor Pacific Smyth Island Pend Oreille Tazewell Jefferson Pierce Warren King San Juan Washington Kitsap Skagit Wise Kittitas Skamania Wythe Lewis Snohomish Bat, Ozark Big-eared Mason Spokane Corynorhinus (=Plecotus) townsendii Pacific Stevens ingens Pierce Thurston Augusta San Juan Wahkiakum Bath Skagit Walla Walla Bland Snohomish Whatcom Craig Thurston Whitman Giles Wahkiakum Yakima Highland Whatcom Salmon, Sockeye Montgomery Yakima Oncorhynchus (=Salmo) nerka Pulaski Fish Asotin Rockingham Benton Russell Salmon, Chinook Oncorhynchus (=Salmo) tshawytscha Chelan Smyth Clallam Adams Clallam Tazewell Clark Asotin Clark Reptile Benton Columbia Turtle, Bog Chelan Cowlitz Clemmys muhlenbergii Douglas Clallam Douglas Carroll Clark Franklin Floyd Columbia Garfield Grayson Cowlitz Grant Patrick Douglas Grays Harbor Washington Ferry Island Bird Franklin Jefferson Garfield King Grant Kitsap

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250 Fish Fish Fish Kittitas Skamania Whatcom Klickitat Snohomish Yakima Lewis Thurston Mammal Mason Walla Walla Killer whale, Southern Resident DPS Okanogan Whatcom Orcinus orca Pacific Whitman Clallam Pierce Yakima Island San Juan Trout, Apache Jefferson Skagit Oncorhynchus apache King Skamania Cowlitz Kitsap Snohomish Trout, Bull Mason Thurston Salvelinus confluentus Pierce Wahkiakum Asotin San Juan Walla Walla Benton Skagit Whatcom Chelan Snohomish Whitman Clallam Thurston Yakima Clark Whatcom Steelhead Columbia Whale, Gray Oncorhynchus (=Salmo) mykiss Douglas Eschrichtius robustus Adams Ferry Adams Asotin Franklin Asotin Benton Garfield Benton Chelan Grant Chelan Clallam Grays Harbor Clallam Clark Island Clark Columbia Jefferson Columbia Cowlitz King Cowlitz Douglas Kitsap Douglas Franklin Kittitas Ferry Garfield Klickitat Franklin Grant Lewis Garfield Grays Harbor Mason Grant Island Okanogan Grays Harbor Jefferson Pacific Island King Pend Oreille Jefferson Kitsap Pierce King Kittitas San Juan Kitsap Klickitat Skagit Kittitas Lewis Skamania Klickitat Mason Snohomish Lewis Okanogan Stevens Lincoln Pierce Thurston Mason San Juan Wahkiakum Okanogan Skagit Walla Walla Pacific

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251 Mammal Bivalve Bivalve Pend Oreille Tyler Dane Pierce Pearlymussel, Tubercled-blossom Grant San Juan Epioblasma torulosa torulosa Iowa Skagit Fayette La Crosse Skamania Riffleshell, Northern Pierce Snohomish Epioblasma torulosa rangiana Polk Spokane Kanawha Richland Stevens Spinymussel, James River Sauk Thurston Pleurobema collina St. Croix Wahkiakum Monroe Wyoming Walla Walla Crustacean Whatcom Amphibian Isopod, Madison Cave Whitman Antrolana lira Toad, Wyoming Yakima Jefferson Bufo baxteri (=hemiophrys) West Virginia Mammal Albany Bird Amphibian Bat, Indiana Myotis sodalis Crane, Whooping Salamander, Cheat Mountain Grus americana Plethodon nettingi Boone Albany Grant Fayette Carbon Pendleton Greenbrier Converse Pocahontas Mercer Fremont Randolph Monroe Goshen Tucker Pendleton Laramie Bivalve Pocahontas Natrona Preston Fanshell Randolph Niobrara Cyprogenia stegaria Platte Tucker Fayette Fish Kanawha Bat, Virginia Big-eared Corynorhinus (=Plecotus) townsendii Chub, Bonytail Wood virginianus Gila elegans Mucket, Pink (Pearlymussel) Fayette Carbon Lampsilis abrupta Grant Fremont Cabell Randolph Lincoln Fayette Tucker Sweetwater Kanawha Uinta Wisconsin Uinta Mason Chub, Humpback Wood Bivalve Gila cypha Mussel, Clubshell Mussel, Winged Mapleleaf Carbon Pleurobema clava Quadrula fragosa Fremont Braxton Polk Lincoln Clay Pearlymussel, Higgins' Eye Sweetwater Doddridge Lampsilis higginsii Uinta Lewis Buffalo Squawfish, Colorado Ritchie Crawford Ptychocheilus lucius

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252 Fish Carbon Fremont Lincoln Sweetwater Uinta Sturgeon, Pallid Scaphirhynchus albus Albany Carbon Converse Fremont Goshen Laramie Natrona Niobrara Platte Sucker, Razorback Xyrauchen texanus Carbon Fremont Lincoln Sweetwater Uinta

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253 310 Species Affected Inverse Name Taxon Medium Abalone, Black Haliotis cracherodii Gastropod Saltwater Abalone, White Haliotis sorenseni Gastropod Saltwater Albatross, Short-tailed Phoebastria (=Diomedea) albatrus Bird Terrestrial, Saltwater Alligator, American Alligator mississippiensis Reptile Terrestrial, Freshwater, Brackish Ambersnail, Kanab Oxyloma haydeni kanabensis Gastropod Terrestrial, Freshwater Amphipod, Illinois Cave Gammarus acherondytes Crustacean Freshwater, Subterraneous Amphipod, Kauai Cave Spelaeorchestia koloana Crustacean Freshwater, Subterraneous Amphipod, Noel's Gammarus desperatus Crustacean Freshwater Amphipod, Peck's Cave Stygobromus (=Stygonectes) pecki Crustacean Freshwater, Subterraneous Bankclimber, Purple Elliptoideus sloatianus Bivalve Freshwater Bat, Gray Myotis grisescens Mammal Terrestrial, Subterraneous Bat, Hawaiian Hoary Lasiurus cinereus semotus Mammal Terrestrial, Subterraneous Bat, Indiana Myotis sodalis Mammal Terrestrial, Subterraneous Bat, Lesser (=Sanborn's) Long- Leptonycteris curasoae Mammal Terrestrial, Subterraneous Bat, Little Mariana Fruit Pteropus tokudae Mammal Terrestrial, Subterraneous Bat, Mariana Fruit (=Mariana Pteropus mariannus mariannus Mammal Terrestrial, Subterraneous Flying Fox) Bat, Mexican Long-nosed Leptonycteris nivalis Mammal Terrestrial, Subterraneous Bat, Ozark Big-eared Corynorhinus (=Plecotus) Mammal Terrestrial, Subterraneous townsendii ingens Bat, Virginia Big-eared Corynorhinus (=Plecotus) Mammal Terrestrial, Subterraneous townsendii virginianus Campeloma, Slender Campeloma decampi Gastropod Freshwater Catfish, Yaqui Ictalurus pricei Fish Freshwater Cavefish, Alabama Speoplatyrhinus poulsoni Fish Freshwater Cavefish, Ozark Amblyopsis rosae Fish Freshwater Cavesnail, Tumbling Creek Antrobia culveri Gastropod Freshwater, Subterraneous Chub, Bonytail Gila elegans Fish Freshwater Chub, Borax Lake Gila boraxobius Fish Freshwater Chub, Chihuahua Gila nigrescens Fish Freshwater Chub, Gila Gila intermedia Fish Freshwater Chub, Humpback Gila cypha Fish Freshwater Chub, Hutton Tui Gila bicolor ssp. Fish Freshwater Chub, Mohave Tui Gila bicolor mohavensis Fish Freshwater Chub, Oregon Oregonichthys crameri Fish Freshwater Chub, Owens Tui Gila bicolor snyderi Fish Freshwater Chub, Pahranagat Roundtail Gila robusta jordani Fish Freshwater Chub, Slender Erimystax cahni Fish Freshwater Chub, Sonora Gila ditaenia Fish Freshwater Chub, Spotfin Erimonax monachus Fish Freshwater Chub, Virgin River Gila seminuda (=robusta) Fish Freshwater Chub, Yaqui Gila purpurea Fish Freshwater

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254 Combshell, Southern (=Penitent Epioblasma penita Bivalve Freshwater mussel) Combshell, Upland Epioblasma metastriata Bivalve Freshwater Coqui, Golden Eleutherodactylus jasperi Amphibian Terrestrial, Freshwater Coral, Elkhorn Acropora palmata Coral Saltwater Coral, Staghorn Acropora cervicornis Coral Saltwater Crane, Mississippi Sandhill Grus canadensis pulla Bird Terrestrial, Freshwater Crane, Whooping Grus americana Bird Terrestrial, Freshwater Crayfish, Cave (Cambarus Cambarus aculabrum Crustacean Freshwater aculabrum) Crayfish, Cave (Cambarus Cambarus zophonastes Crustacean Freshwater zophonastes) Crayfish, Nashville Orconectes shoupi Crustacean Freshwater Crayfish, Shasta Pacifastacus fortis Crustacean Freshwater Crocodile, American Crocodylus acutus Reptile Terrestrial, Freshwater Cui-ui Chasmistes cujus Fish Freshwater Dace, Ash Meadows Speckled Rhinichthys osculus nevadensis Fish Freshwater Dace, Blackside Phoxinus cumberlandensis Fish Freshwater Dace, Clover Valley Speckled Rhinichthys osculus oligoporus Fish Freshwater Dace, Desert Eremichthys acros Fish Freshwater Dace, Foskett Speckled Rhinichthys osculus ssp. Fish Freshwater Dace, Independence Valley Speckled Rhinichthys osculus lethoporus Fish Freshwater Dace, Moapa Moapa coriacea Fish Freshwater Darter, Amber Percina antesella Fish Freshwater Darter, Bayou Etheostoma rubrum Fish Freshwater Darter, Bluemask (=jewel) Etheostoma sp. Fish Freshwater Darter, Boulder Etheostoma wapiti Fish Freshwater Darter, Cherokee Etheostoma scotti Fish Freshwater Darter, Duskytail Etheostoma percnurum Fish Freshwater Darter, Etowah Etheostoma etowahae Fish Freshwater Darter, Fountain Etheostoma fonticola Fish Freshwater Darter, Goldline Percina aurolineata Fish Freshwater Darter, Leopard Percina pantherina Fish Freshwater Darter, Maryland Etheostoma sellare Fish Freshwater Darter, Niangua Etheostoma nianguae Fish Freshwater Darter, Okaloosa Etheostoma okaloosae Fish Freshwater Darter, Relict Etheostoma chienense Fish Freshwater Darter, Slackwater Etheostoma boschungi Fish Freshwater Darter, Snail Percina tanasi Fish Freshwater Darter, Vermilion Etheostoma chermocki Fish Freshwater Darter, Watercress Etheostoma nuchale Fish Freshwater Duck, Hawaiian (Koloa) Anas wyvilliana Bird Terrestrial, Freshwater Elimia, Lacy Elimia crenatella Gastropod Freshwater Elktoe, Appalachian Alasmidonta raveneliana Bivalve Freshwater

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255 Fairy Shrimp, Conservancy Fairy Branchinecta conservatio Crustacean Vernal pool Fairy Shrimp, Longhorn Branchinecta longiantenna Crustacean Vernal pool Fairy Shrimp, Riverside Streptocephalus woottoni Crustacean Vernal pool Fairy Shrimp, San Diego Branchinecta sandiegonensis Crustacean Vernal pool Fairy Shrimp, Vernal Pool Branchinecta lynchi Crustacean Vernal pool Fanshell Cyprogenia stegaria Bivalve Freshwater Fatmucket, Arkansas Lampsilis powelli Bivalve Freshwater Frog, California Red-legged Rana aurora draytonii Amphibian Terrestrial, Freshwater Frog, Chiricahua Leopard Rana chiricahuensis Amphibian Terrestrial, Freshwater Frog, Dusky Gopher (Mississippi Rana capito sevosa Amphibian Terrestrial, Freshwater DPS) Frog, Mountain Yellow-legged Rana muscosa Amphibian Terrestrial, Freshwater Gambusia, Big Bend Gambusia gaigei Fish Freshwater Gambusia, Clear Creek Gambusia heterochir Fish Freshwater Gambusia, Pecos Gambusia nobilis Fish Freshwater Gambusia, San Marcos Gambusia georgei Fish Freshwater Goby, Tidewater Eucyclogobius newberryi Fish Freshwater Goose, Hawaiian (Nene) Branta (=Nesochen) sandvicensis Bird Terrestrial, Freshwater Guajon Eleutherodactylus cooki Amphibian Terrestrial, Freshwater Hornsnail, rough Pleurocera foremani Gastropod Freshwater Isopod, Lee County Cave Lirceus usdagalun Crustacean Freshwater Isopod, Madison Cave Antrolana lira Crustacean Freshwater Isopod, Socorro Thermosphaeroma thermophilus Crustacean Freshwater Kidneyshell, Triangular Ptychobranchus greenii Bivalve Freshwater Killer whale, Southern Resident DPS Orcinus orca Mammal Saltwater Limpet, Banbury Springs Lanx sp. Gastropod Freshwater Logperch, Conasauga Percina jenkinsi Fish Freshwater Logperch, Roanoke Percina rex Fish Freshwater Madtom, Neosho Noturus placidus Fish Freshwater Madtom, Pygmy Noturus stanauli Fish Freshwater Madtom, Scioto Noturus trautmani Fish Freshwater Madtom, Smoky Noturus baileyi Fish Freshwater Madtom, Yellowfin Noturus flavipinnis Fish Freshwater Manatee, West Indian Trichechus manatus Mammal Saltwater Minnow, Devils River Dionda diaboli Fish Freshwater Minnow, Loach Tiaroga cobitis Fish Freshwater Minnow, Rio Grande Silvery Hybognathus amarus Fish Freshwater Mountain Beaver, Point Arena Aplodontia rufa nigra Mammal Terrestrial, Freshwater Mouse, Alabama Beach Peromyscus polionotus ammobates Mammal Terrestrial, Coastal Mouse, Anastasia Island Beach Peromyscus polionotus phasma Mammal Terrestrial, Coastal Mouse, Choctawhatchee Beach Peromyscus polionotus allophrys Mammal Terrestrial, Coastal Mouse, Perdido Key Beach Peromyscus polionotus trissyllepsis Mammal Terrestrial, Coastal Mouse, Southeastern Beach Peromyscus polionotus niveiventris Mammal Terrestrial, Coastal Mouse, St. Andrew Beach Peromyscus polionotus peninsularis Mammal Terrestrial, Coastal

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256 Mucket, Orange-nacre Lampsilis perovalis Bivalve Freshwater Mucket, Pink (Pearlymussel) Lampsilis abrupta Bivalve Freshwater Murrelet, Marbled Brachyramphus marmoratus Bird Terrestrial, Freshwater, Saltwater Mussel, Acornshell Southern Epioblasma othcaloogensis Bivalve Freshwater Mussel, Alabama Moccasinshell Medionidus acutissimus Bivalve Freshwater Mussel, Black (=Curtus' Mussel) Pleurobema curtum Bivalve Freshwater Clubshell Mussel, Clubshell Pleurobema clava Bivalve Freshwater Mussel, Coosa Moccasinshell Medionidus parvulus Bivalve Freshwater Mussel, Cumberland Combshell Epioblasma brevidens Bivalve Freshwater Mussel, Cumberland Elktoe Alasmidonta atropurpurea Bivalve Freshwater Mussel, Cumberland Pigtoe Pleurobema gibberum Bivalve Freshwater Mussel, Dark Pigtoe Pleurobema furvum Bivalve Freshwater Mussel, Dwarf Wedge Alasmidonta heterodon Bivalve Freshwater Mussel, Fat Threeridge Amblema neislerii Bivalve Freshwater Mussel, Fine-lined Pocketbook Lampsilis altilis Bivalve Freshwater Mussel, Fine-rayed Pigtoe Fusconaia cuneolus Bivalve Freshwater Mussel, Flat Pigtoe (=Marshall's Pleurobema marshalli Bivalve Freshwater Mussel) Mussel, Georgia pigtoe Pleurobema hanleyianum Bivalve Freshwater Mussel, Gulf Moccasinshell Medionidus penicillatus Bivalve Freshwater Mussel, Heavy Pigtoe (=Judge Pleurobema taitianum Bivalve Freshwater Tait's Mussel) Mussel, Heelsplitter Carolina Lasmigona decorata Bivalve Freshwater Mussel, Heelsplitter Inflated Potamilus inflatus Bivalve Freshwater Mussel, Ochlockonee Medionidus simpsonianus Bivalve Freshwater Mussel, Oval Pigtoe Pleurobema pyriforme Bivalve Freshwater Mussel, Ovate Clubshell Pleurobema perovatum Bivalve Freshwater Mussel, Oyster Epioblasma capsaeformis Bivalve Freshwater Mussel, Ring Pink (=Golf Stick Obovaria retusa Bivalve Freshwater Pearly) Mussel, Rough Pigtoe Pleurobema plenum Bivalve Freshwater Mussel, Scaleshell Leptodea leptodon Bivalve Freshwater Mussel, Shiny Pigtoe Fusconaia cor Bivalve Freshwater Mussel, Shiny-rayed Pocketbook Lampsilis subangulata Bivalve Freshwater Mussel, Southern Clubshell Pleurobema decisum Bivalve Freshwater Mussel, Southern Pigtoe Pleurobema georgianum Bivalve Freshwater Mussel, Speckled Pocketbook Lampsilis streckeri Bivalve Freshwater Mussel, Winged Mapleleaf Quadrula fragosa Bivalve Freshwater Otter, Southern Sea Enhydra lutris nereis Mammal Saltwater Pearlshell, Louisiana Margaritifera hembeli Bivalve Freshwater Pearlymussel, Alabama Lamp Lampsilis virescens Bivalve Freshwater Pearlymussel, Appalachian Quadrula sparsa Bivalve Freshwater Monkeyface Pearlymussel, Birdwing Conradilla caelata Bivalve Freshwater

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257 Pearlymussel, Cracking Hemistena lata Bivalve Freshwater Pearlymussel, Cumberland Bean Villosa trabalis Bivalve Freshwater Pearlymussel, Cumberland Quadrula intermedia Bivalve Freshwater Monkeyface Pearlymussel, Curtis' Epioblasma florentina curtisii Bivalve Freshwater Pearlymussel, Dromedary Dromus dromas Bivalve Freshwater Pearlymussel, Fat Pocketbook Potamilus capax Bivalve Freshwater Pearlymussel, Green-blossom Epioblasma torulosa Bivalve Freshwater Pearlymussel, Higgins' Eye Lampsilis higginsii Bivalve Freshwater Pearlymussel, Little-wing Pegias fabula Bivalve Freshwater Pearlymussel, Orange-footed Plethobasus cooperianus Bivalve Freshwater Pearlymussel, Pale Lilliput Toxolasma cylindrellus Bivalve Freshwater Pearlymussel, Purple Cat's Paw Epioblasma obliquata obliquata Bivalve Freshwater Pearlymussel, Tubercled-blossom Epioblasma torulosa torulosa Bivalve Freshwater Pearlymussel, Turgid-blossom Epioblasma turgidula Bivalve Freshwater Pearlymussel, White Cat's Paw Epioblasma obliquata perobliqua Bivalve Freshwater Pearlymussel, White Wartyback Plethobasus cicatricosus Bivalve Freshwater Pearlymussel, Yellow-blossom Epioblasma florentina florentina Bivalve Freshwater Pebblesnail, Flat Lepyrium showalteri Gastropod Freshwater Prairie Dog, Utah Cynomys parvidens Mammal Terrestrial, Subterraneous Pupfish, Ash Meadows Amargosa Cyprinodon nevadensis mionectes Fish Freshwater Pupfish, Comanche Springs Cyprinodon elegans Fish Freshwater Pupfish, Desert Cyprinodon macularius Fish Freshwater Pupfish, Devils Hole Cyprinodon diabolis Fish Freshwater Pupfish, Leon Springs Cyprinodon bovinus Fish Freshwater Pupfish, Warm Springs Cyprinodon nevadensis pectoralis Fish Freshwater Purple Bean Villosa perpurpurea Bivalve Freshwater Rabbitsfoot, Rough Quadrula cylindrica strigillata Bivalve Freshwater Riffleshell, Northern Epioblasma torulosa rangiana Bivalve Freshwater Riffleshell, Tan Epioblasma florentina walkeri (=E. Bivalve Freshwater walkeri) Riversnail, Anthony's Athearnia anthonyi Gastropod Freshwater Rock-pocketbook, Ouachita Arkansia wheeleri Bivalve Freshwater (=Wheeler's pm) Rocksnail, interrupted Leptoxis foremani Gastropod Freshwater Rocksnail, Painted Leptoxis taeniata Gastropod Freshwater Rocksnail, Plicate Leptoxis plicata Gastropod Freshwater Rocksnail, Round Leptoxis ampla Gastropod Freshwater Salamander, Barton Springs Eurycea sosorum Amphibian Terrestrial, Freshwater Salamander, California Tiger Ambystoma californiense Amphibian Terrestrial, Vernal pool Salamander, Cheat Mountain Plethodon nettingi Amphibian Terrestrial, Freshwater Salamander, Desert Slender Batrachoseps aridus Amphibian Terrestrial, Freshwater Salamander, Frosted Flatwoods Ambystoma cingulatum Amphibian Terrestrial, Freshwater, Vernal pool Salamander, Red Hills Phaeognathus hubrichti Amphibian Terrestrial, Freshwater

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258 Salamander, Reticulated flatwoods Ambystoma bishopi Amphibian Terrestrial, Freshwater Salamander, San Marcos Eurycea nana Amphibian Terrestrial, Freshwater Salamander, Santa Cruz Long-toed Ambystoma macrodactylum croceum Amphibian Terrestrial, Freshwater, Vernal pool Salamander, Shenandoah Plethodon shenandoah Amphibian Terrestrial, Freshwater Salamander, Sonora Tiger Ambystoma tigrinum stebbinsi Amphibian Terrestrial, Freshwater, Vernal pool Salamander, Texas Blind Typhlomolge rathbuni Amphibian Freshwater, Subterraneous Salmon, Atlantic Salmo salar Fish Freshwater, Brackish, Saltwater Salmon, Chinook Oncorhynchus (=Salmo) Fish Freshwater, Brackish, Saltwater Salmon, Chum Oncorhynchus (=Salmo) keta Fish Freshwater, Brackish, Saltwater Salmon, Coho Oncorhynchus (=Salmo) kisutch Fish Freshwater, Brackish, Saltwater Salmon, Sockeye Oncorhynchus (=Salmo) nerka Fish Freshwater, Brackish, Saltwater Sawfish, Smalltooth Pristis pectinata Fish Freshwater, Brackish, Saltwater Sculpin, Pygmy Cottus paulus (=pygmaeus) Fish Freshwater Sea turtle, green Chelonia mydas Reptile Saltwater Sea turtle, hawksbill Eretmochelys imbricata Reptile Saltwater, Coastal Sea turtle, leatherback Dermochelys coriacea Reptile Saltwater, Coastal Sea turtle, loggerhead Caretta caretta Reptile Saltwater, Coastal Seal, Guadalupe Fur Arctocephalus townsendi Mammal Saltwater, Coastal Seal, Hawaiian Monk Monachus schauinslandi Mammal Saltwater, Coastal Sea-lion, Steller Eumetopias jubatus Mammal Saltwater, Coastal Shearwater, Newell's Townsend's Puffinus auricularis newelli Bird Terrestrial, Saltwater Shiner, Arkansas River Notropis girardi Fish Freshwater Shiner, Beautiful Cyprinella formosa Fish Freshwater Shiner, Blue Cyprinella caerulea Fish Freshwater Shiner, Cahaba Notropis cahabae Fish Freshwater Shiner, Cape Fear Notropis mekistocholas Fish Freshwater Shiner, Palezone Notropis albizonatus Fish Freshwater Shiner, Pecos Bluntnose Notropis simus pecosensis Fish Freshwater Shiner, Topeka Notropis topeka (=tristis) Fish Freshwater Shrimp, Alabama Cave Palaemonias alabamae Crustacean Freshwater Shrimp, California Freshwater Syncaris pacifica Crustacean Freshwater Shrimp, Kentucky Cave Palaemonias ganteri Crustacean Freshwater Shrimp, Squirrel Chimney Cave Palaemonetes cummingi Crustacean Freshwater, Subterraneous Silverside, Waccamaw Menidia extensa Fish Freshwater Slabshell, Chipola Elliptio chipolaensis Bivalve Freshwater Smelt, Delta Hypomesus transpacificus Fish Freshwater, Brackish Snail, Armored Pyrgulopsis (=Marstonia) pachyta Gastropod Freshwater Snail, Bliss Rapids Taylorconcha serpenticola Gastropod Freshwater Snail, Chittenango Ovate Amber Succinea chittenangoensis Gastropod Terrestrial, Freshwater Snail, Lioplax Cylindrical Lioplax cyclostomaformis Gastropod Freshwater Snail, Newcomb's Erinna newcombi Gastropod Freshwater Snail, Pecos Assiminea Assiminea pecos Gastropod Freshwater Snake, Atlantic Salt Marsh Nerodia clarkii taeniata Reptile Terrestrial, Brackish, Saltwater

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259 Snake, Concho Water Nerodia paucimaculata Reptile Terrestrial, Freshwater Snake, Giant Garter Thamnophis gigas Reptile Terrestrial, Freshwater Snake, Lake Erie Water Nerodia sipedon insularum Reptile Terrestrial, Freshwater Snake, Northern Copperbelly Nerodia erythrogaster neglecta Reptile Terrestrial, Freshwater Snake, San Francisco Garter Thamnophis sirtalis tetrataenia Reptile Terrestrial, Freshwater Spikedace Meda fulgida Fish Freshwater Spinedace, Big Spring Lepidomeda mollispinis pratensis Fish Freshwater Spinedace, Little Colorado Lepidomeda vittata Fish Freshwater Spinedace, White River Lepidomeda albivallis Fish Freshwater Spinymussel, James River Pleurobema collina Bivalve Freshwater Spinymussel, Tar River Elliptio steinstansana Bivalve Freshwater Springfish, Hiko White River Crenichthys baileyi grandis Fish Freshwater Springfish, Railroad Valley Crenichthys nevadae Fish Freshwater Springfish, White River Crenichthys baileyi baileyi Fish Freshwater Springsnail, Alamosa Tryonia alamosae Gastropod Freshwater Springsnail, Bruneau Hot Pyrgulopsis bruneauensis Gastropod Freshwater Springsnail, Roswell Pyrgulopsis roswellensis Gastropod Freshwater Springsnail, Socorro Pyrgulopsis neomexicana Gastropod Freshwater Squawfish, Colorado Ptychocheilus lucius Fish Freshwater Steelhead Oncorhynchus (=Salmo) mykiss Fish Freshwater, Brackish, Saltwater Stickleback, Unarmored Gasterosteus aculeatus williamsoni Fish Freshwater Stirrupshell Quadrula stapes Bivalve Freshwater Sturgeon, Alabama Scaphirhynchus suttkusi Fish Freshwater Sturgeon, Gulf Acipenser oxyrinchus desotoi Fish Freshwater, Saltwater Sturgeon, North American green Acipenser medirostris Fish Freshwater, Saltwater Sturgeon, Pallid Scaphirhynchus albus Fish Freshwater Sturgeon, Shortnose Acipenser brevirostrum Fish Freshwater, Saltwater Sturgeon, White Acipenser transmontanus Fish Freshwater, Saltwater Sucker, June Chasmistes liorus Fish Freshwater Sucker, Lost River Deltistes luxatus Fish Freshwater Sucker, Modoc Catostomus microps Fish Freshwater Sucker, Razorback Xyrauchen texanus Fish Freshwater Sucker, Santa Ana Catostomus santaanae Fish Freshwater Sucker, Shortnose Chasmistes brevirostris Fish Freshwater Sucker, Warner Catostomus warnerensis Fish Freshwater Tadpole Shrimp, Vernal Pool Lepidurus packardi Crustacean Vernal pool Toad, Arroyo Southwestern Bufo californicus (=microscaphus) Amphibian Terrestrial, Freshwater Toad, Houston Bufo houstonensis Amphibian Terrestrial, Freshwater Toad, Puerto Rican Crested Peltophryne lemur Amphibian Terrestrial, Freshwater Toad, Wyoming Bufo baxteri (=hemiophrys) Amphibian Terrestrial, Freshwater Topminnow, Gila (Yaqui) Poeciliopsis occidentalis Fish Freshwater Trout, Apache Oncorhynchus apache Fish Freshwater Trout, Bull Salvelinus confluentus Fish Freshwater

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260 Trout, Gila Oncorhynchus gilae Fish Freshwater Trout, Greenback Cutthroat Oncorhynchus clarki stomias Fish Freshwater Trout, Lahontan Cutthroat Oncorhynchus clarki henshawi Fish Freshwater Trout, Little Kern Golden Oncorhynchus aguabonita whitei Fish Freshwater Trout, Paiute Cutthroat Oncorhynchus clarki seleniris Fish Freshwater Turtle, Alabama Red-bellied Pseudemys alabamensis Reptile Terrestrial, Freshwater Turtle, Bog Clemmys muhlenbergii Reptile Terrestrial, Freshwater Turtle, Flattened Musk Sternotherus depressus Reptile Terrestrial, Freshwater Turtle, Plymouth Red-bellied Pseudemys rubriventris bangsi Reptile Terrestrial, Freshwater Turtle, Ringed Map Graptemys oculifera Reptile Terrestrial, Freshwater Turtle, Yellow-blotched Map Graptemys flavimaculata Reptile Terrestrial, Freshwater Vole, Florida Salt Marsh Microtus pennsylvanicus Mammal Terrestrial, Brackish dukecampbelli Whale, beluga Delphinapterus leucas Mammal Saltwater Whale, Finback Balaenoptera physalus Mammal Saltwater Whale, Gray Eschrichtius robustus Mammal Saltwater Whale, Humpback Megaptera novaeangliae Mammal Saltwater Whale, North Atlantic right Eubalaena glacialis (incl. australis) Mammal Saltwater Whale, Sei Balaenoptera borealis Mammal Saltwater Whale, Sperm Physeter catodon (=macrocephalus) Mammal Saltwater Woundfin Plagopterus argentissimus Fish Freshwater No species were selected for exclusion. Dispersed species included in report. Marine Species

Coral (Anthozoa) Common name Scientific name Family Order Coral, Elkhorn Acropora palmata Acroporidae Scleractinia Coral, Staghorn Acropora cervicornis Acroporidae Scleractinia Fish (Actinopterygii) Common name Scientific name Family Order Salmon, Atlantic Salmo salar Salmonidae Salmoniformes Salmon, Chinook Oncorhynchus (=Salmo) tshawytscha Salmonidae Salmoniformes Salmon, Chum Oncorhynchus (=Salmo) keta Salmonidae Salmoniformes Salmon, Coho Oncorhynchus (=Salmo) kisutch Salmonidae Salmoniformes Salmon, Sockeye Oncorhynchus (=Salmo) nerka Salmonidae Salmoniformes Sawfish, Smalltooth Pristis pectinata Pristidae Pristiformes Steelhead Oncorhynchus (=Salmo) mykiss Salmonidae Salmoniformes Sturgeon, Gulf Acipenser oxyrinchus desotoi Acipenseridae Acipenseriformes Sturgeon, North American green Acipenser medirostris Acipenseridae Acipenseriformes Sturgeon, Shortnose Acipenser brevirostrum Acipenseridae Acipenseriformes Sturgeon, White Acipenser transmontanus Acipenseridae Acipenseriformes

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261 Gastropod (Gastropoda) Common name Scientific name Family Order Abalone, Black Haliotis cracherodii Haliotidae Vetigastropoda Abalone, White Haliotis sorenseni Haliotidae Vetigastropoda Mammal (Mammalia) Common name Scientific name Family Order Bear, polar Ursus maritimus Ursidae Carnivora Killer whale, Southern Resident DPS Orcinus orca Cervidae Artiodactyla Manatee, West Indian Trichechus manatus Trichechidae Sirenia Otter, Northern Sea Enhydra lutris kenyoni Mustelidae Carnivora Otter, Southern Sea Enhydra lutris nereis Mustelidae Carnivora Seal, Guadalupe Fur Arctocephalus townsendi Phocidae Carnivora Seal, Hawaiian Monk Monachus schauinslandi Phocidae Carnivora Sea-lion, Steller Eumetopias jubatus Otariidae Carnivora Whale, beluga Delphinapterus leucas Monodontidae Cetacea Whale, Blue Balaenoptera musculus Balaenopteridae Cetacea Whale, Bowhead Balaena mysticetus Balaenidae Cetacea Whale, Finback Balaenoptera physalus Balaenopteridae Cetacea Whale, Gray Eschrichtius robustus Eschrichtiidae Cetacea Whale, Humpback Megaptera novaeangliae Balaenopteridae Cetacea Whale, North Atlantic right Eubalaena glacialis (incl. australis) Balaenidae Cetacea Whale, North Pacific right Eubalaena japonica Balaenidae Cetacea Whale, Sei Balaenoptera borealis Balaenopteridae Cetacea Whale, Sperm Physeter catodon (=macrocephalus) Physeteridae Cetacea Reptile (Reptilia) Common name Scientific name Family Order Sea turtle, green Chelonia mydas Cheloniidae Testudines Sea turtle, hawksbill Eretmochelys imbricata Cheloniidae Testudines Sea turtle, Kemp's ridley Lepidochelys kempii Cheloniidae Testudines Sea turtle, leatherback Dermochelys coriacea Dermochelyidae Testudines Sea turtle, loggerhead Caretta caretta Cheloniidae Testudines Sea turtle, olive ridley Lepidochelys olivacea Cheloniidae Testudines Snake, Atlantic Salt Marsh Nerodia clarkii taeniata Colubridae Squamata

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262 Appendix K. Transformation Products Formed in Environmental Fate Studies

Final Code Name/ Maximum %AR Chemical Name Chemical Structure Study Type Synonym %AR (day) (study length) PARENT Picoxystrobin IUPAC Methyl(E)-2-{2-[6-

ZA1963 (trifluoromethyl)pyridin-2- yloxymethyl]phenyl}-3- methoxyacrylate

CAS: Methyl(E)-α- F (methoxymethylene)-2-[[[6- F N O (trifluoromethyl)-2- F pyridinyl]oxy]methyl]benzeneace O O H C CH tate (9Cl) 3 3 O CAS-no: 117428-22-5

Formula: C18H16F3NO4 MW: 367.32 g/mole MAJOR (>10%) TRANSFORMATION PRODUCTS ZA1963/02 (E)-2-{2-[6- Aerobic soil Sandy loam Pyridinyl label 16.8 (50) 1.5 (364) (trifluoromethyl)pyridin-2- (Hyde Farm) Phenylacrylate label 18.7 (29) 1.9 (364) F Compound 2 yloxymethyl]phenyl}-3- Sandy clay Pyridinyl label 9.4 (9) 4.0 (119) F N O methoxyacrylic acid loam Phenylacrylate label 9.1 (9) 2.7 (119) IN-QDY62 F HO O Sand Pyridinyl label 14.9 (50) 4.5 (119) CH 3 Phenylacrylate label 17.3 (29) 3.7 (119) R403092 O Sandy loam Pyridinyl label 26.1 (50) 17.3 (119)

(Frensham) Phenylacrylate label 26.3 (29) 13.5 (119)

263 Final Code Name/ Maximum %AR Chemical Name Chemical Structure Study Type Synonym %AR (day) (study length) Anaerobic soil Waiver requested

Aerobic Old Pyridinyl label Water 37.4 (120) 37.4 (120) aquatic Basing Sediment 29.8 (120) 29.8 (120) System 67.2 (120) 67.2 (120) Phenylacrylate Water 38.2 (120) 38.2 (120 label Sediment 30.7 (120) 30.7 (120) System 68.9 (120) 68.9 (120) Virginia Pyridinyl label Water 16.6 (83) 6.3 (120) Water Sediment 6.7 (51) 1.1 (120) System 22.5 (51) 7.4 (120) Phenylacrylate Water 16.4 (83) 6.0 (120) label Sediment 7.6 (51) 1.0 (120) System 20.6 (51) 7.0 (120) Anaerobic aquatic Pyridinyl Water 40.0 (360) 40.0 (360) label Sediment 33.3 (360) 33.3 (360) System 73.3 (360) 73.3 (360) Phenylacrylat Water 37.0 (360) 37.0 (360) e label Sediment 35.9 (220) 30.4 (360) System 69.4 (220) 67.4 (360) Hydrolysis pH 9 (50ºC) 32.1 (32) 32.1 (32) Aqueous photolysis Not identified but not major Soil photolysis Not identified but not major Field Terrestrial MRID 48073841 0.038 ppm (46, 0.0047 studies 60) ppm (447) MRID 48073842 0.035 ppm (60) na1 (363) MRID 48073843 0.085 ppm (48) na (357) MRID 48073844 0.143 ppm (43) na (372) MRID 48073846 Site 1 0.01 ppm (15, <0.01 ppm 62) (367) Site 2 0.02 ppm (27, 0.02 ppm 56, 98, 189, (365) 274, 367) MRID 48073847 0.03 ppm (364) 0.03 ppm (364) MRID 48073848 0.02 ppm (96) <0.01 ppm (365)

264 Final Code Name/ Maximum %AR Chemical Name Chemical Structure Study Type Synonym %AR (day) (study length) MRID 48073849 Site 1 <0.01 ppm <0.01 ppm (365) Site 2 <0.01 ppm <0.01 ppm (361) MRID 48073850 <0.01 ppm <0.01 ppm (391) MRID 48073851 0.01 ppm (56, <0.01 ppm 96, 284) (379) Aquatic MRID 48073838 Not analyzed ZA1963/03 6-(Trifluoromethyl)pyridin-2H-2- Aerobic soil Pyridinyl Sandy loam (Hyde 13.8 (50) 0.7 (364) Compound 3 one label Farm) Sandy clay loam 13.7 (21) 3.9 (119) IN-QDK50 Sand 9.4 (50) 5.8 (119)

R403814 Sandy loam 10.3 (50) 7.9 (119) (Frensham) Anaerobic soil Waiver requested Aerobic aquatic Pyridinyl Old Water 1.0 (83) 0.9 (120) label Basing Sediment 1.1 (120) 1.1 (120) System 2.0 (120) 2.0 (120) Virginia Water 4.5 (120) 4.5 (120) water Sediment 1.5 (120) 1.5 (120) F H System 6.0 (120) 6.0 (120) F N O Anaerobic aquatic Pyridinyl Water 0.8 (360) 0.8 (360) F label Sediment 0.6 (360) 0.6 (360) System 1.5 (360) 1.5 (360) Hydrolysis Not identified but not major

Aqueous photolysis Pyridinyl label 1.9 (17.9) 1.9 (17.9) Phenylacrylate label Not detected Soil photolysis Pyridinyl label 28.3 (3.8) 13.1 (19.8) Field Terrestrial MRID 48073841 0.051 ppm (29) 0.0045 studies ppm (447) MRID 48073842 0.015 ppm (11) na (363) MRID 48073843 0.013 ppm (16) na (357) MRID 48073844 0.016 ppm (30) na (372) MRID 48073846 Site 1 0.04 ppm (15, <0.01 ppm 28) (367) Site 2 0.03 ppm (98) <0.01 ppm (365)

265 Final Code Name/ Maximum %AR Chemical Name Chemical Structure Study Type Synonym %AR (day) (study length) MRID 48073847 0.03 ppm (94) 0.02 ppm (364) MRID 48073848 0.02 ppm (4, <0.01 ppm 15, 28) (365) MRID 48073849 Site 1 0.02 ppm (14, <0.01 ppm 28) (365) Site 2 0.02 ppm (13) <0.01 ppm (361) MRID 48073850 0.02 ppm (7, <0.01 ppm 14, 27) (391) MRID 48073851 0.05 ppm (7) <0.01 ppm (379) Aquatic MRID 48073838 Not analyzed ZA1963/04 Methyl (Z)-2-{2-[6- Aerobic soil Not identified but not major (trifluoromethyl)pyridin-2- F Anaerobic soil Waiver requested Compound 4 F yloxymethyl]phenyl}-3- N O Aerobic aquatic Not identified but not major methoxyacrylate F Anaerobic aquatic Not identified but not major O Hydrolysis Not identified but not major H3C Aqueous Pyridinyl label 14.2 (3.7) 8.3 (17.9) O O photolysis Phenylacrylate label 11.7 (3.7) 9.1(17.7) CH Soil photolysis Pyridinyl label 2.5 (0.8) 1.1 (19.8) 3 Phenylacrylate label 3.8 (3.8) 2.2 (20.7) Field studies Not analyzed ZA1963/07 2-{2-[6-(trifluoromethyl)pyridin- Aerobic soil Bands corresponding to Compound 7 2-yloxymethyl]phenyl}acetic F reference standards were acid F N O observed on the TLC plates IN-QFA35 but insufficient material was F available for a conclusive HO identification Anaerobic soil Waiver requested O Aerobic aquatic Old Basing Pyridinyl Water 2.3 (30) 0.2 (120) label Sediment 1.4 (120) 1.4 (120) System 1.6 (120) 1.6 (120) Phenylacry Water 0.4 (83) 0.2 (120) late label Sediment 2.9 (120) 2.9 (120) System 3.1 (120) 3.1 (120) Virginia water Pyridinyl Water 25.9 (120) 25.9 (120) label Sediment 12.8 (83) 12.4 (120)

266 Final Code Name/ Maximum %AR Chemical Name Chemical Structure Study Type Synonym %AR (day) (study length) System 38.3 (120) 38.3 (120) Phenylacry Water 24.2 (120) 24.2 (120) late label Sediment 14.2 (83) 12.2 (120) System 36.4 (120) 36.4 (120) Anaerobic Pyridinyl label Water <0.05 (0-360) aquatic Sediment 1.8 (360) 1.8 (360) System 1.8 (360) 1.8 (360) Phenylacrylate label Water <0.05 (0-360) Sediment 1.6 (360) 1.6 (360) System 1.6 (360) 1.6 (360) Hydrolysis pH 9 (50ºC) 37.9 (32) 37.9 (32) Aqueous photolysis Not identified but not major Soil photolysis Not identified but not major Field studies Not analyzed ZA1963/12 Methyl 2-hydroxy-{2-[6- Aerobic soil Not identified but not major F Compound 12 (trifluoromethyl)pyridin-2- Anaerobic soil Waiver requested yloxymethyl]phenyl}-acetate F N O Aerobic aquatic Not identified but not major F Anaerobic aquatic Not identified but not major O Hydrolysis Not identified but not major H3C OH Aqueous photolysis Pyridinyl label 15.3 (17.9) 15.3 (17.9) O Phenylacrylate label 14.5 (17.7) 14.5 (17.7) Soil photolysis Pyridinyl label 1.4 (3.8) 0.9 (19.8) Phenylacrylate label 2.3 (6.9, 20.7) 2.3 (20.7) Field studies Not analyzed

267 Final Code Name/ Maximum %AR Chemical Name Chemical Structure Study Type Synonym %AR (day) (study length) Carbon dioxide Carbon dioxide Aerobic soil Sandy loam Pyridinyl label 33.9 (364) 33.9 (364) (Hyde Farm) Phenylacrylate label 59.9 (364) 59.9 (364) Formula: CO2 Sandy clay Pyridinyl label 32.5 (119) 32.5 (119) loam Phenylacrylate label 40.1 (119) 40.1 (119) Sand Pyridinyl label 22.8 (119) 22.8 (119) Phenylacrylate label 33.6 (119) 33.6 (119) Sandy loam Pyridinyl label 20.1 (119) 20.1 (119) (Frensham) Phenylacrylate label 29.9 (119) 29.9 (119) Anaerobic soil Waiver requested Aerobic aquatic Old Basing Pyridinyl label 2.9 (120) 2.9 (120) O C O Phenylacrylate label 2.9 (120) 2.9 (120) Virginia water Pyridinyl label 5.8 (120) 5.8 (120) Phenylacrylate label 6.1 (120) 6.1 (120) Anaerobic aquatic Pyridinyl label 0.7 (360) 0.7 (360) Phenylacrylate label 0.2 (360) 0.2 (360) Hydrolysis Not analyzed Aqueous photolysis Pyridinyl label 6.4 (17.9) 6.4 (17.9) Phenylacrylate label 2.5 (17.7) 2.5 (17.7) Soil photolysis Pyridinyl label 32.2 (19.8) 32.2 (19.8) Phenylacrylate label 22.0 (20.7) 22.0 (20.7) Field studies Not analyzed

268 Minor Environmental Degradates of Picoxystrobin

Final Maximum %AR Code Chemical name Chemical structure Study Type %AR (study (day) length) ZA1963/08 2-[6-(Trifluoromethyl)pyridin-2- Aerobic soil Likely present at minor yloxymethyl]-benzoic acid F concentrations Compound 8 F N O Anaerobic soil Waiver requested

IN-QDY63 F Aerobic Old Basing Pyridinyl label Water 2.7 (120) 2.7 (120) R408509 aquatic Sediment 0.6 (83) 0.2 (120) O System 2.9 (120) 2.9 (120) OH Phenylacrylate Water 1.1 (83) 0.9 (120) label Sediment 0.8 (83) Not detected (120) System 1.9 (83) 0.9 (120) Virginia Pyridinyl label Water 8.4 (120) 8.4 (120) Water Sediment 2.7 (120) 2.7 (120) System 11.1 (120) 11.1 (120) Phenylacrylate Water 8.5 (120) 8.5 (120) label Sediment 2.9 (120) 2.9 (120) System 11.4 (120) 11.4 (120) Anaerobic aquatic Pyridinyl label Water 0.4 (220) <0.05 (360) Sediment 0.7 (120) 0.3 (360) System 0.7 (120) 0.3 (360) Phenylacrylate Water <0.05 (0-360) label Sediment 0.4 (91) <0.05 (360) System 0.4 (91) <0.05 (360) Hydrolysis Not identified Aqueous photolysis Not identified Soil photolysis Pyridinyl label 2.4 (0.8) 2.3 (19.8) Phenylacrylate label 3.0 (6.9-13.7) 2.9 (20.7) Field studies Terrestrial MRID 48073841 0.055 ppm (46) 0.0053 ppm (447) MRID 48073842 0.161 ppm (5) na (363) MRID 48073843 0.065 ppm (30) na (357)

269 Final Maximum %AR Code Chemical name Chemical structure Study Type %AR (study (day) length) MRID 48073844 0.138 ppm (43) na (372) MRID Site 1 0.09 ppm (7, <0.01 ppm 48073846 28) (367) Site 2 0.06 ppm (14) <0.01 ppm (365) MRID 48073847 0.08 ppm (28) 0.02 ppm (364) MRID 48073848 0.03 ppm (28, <0.01 ppm 63) (365) MRID Site 1 0.03 ppm (6, <0.01 ppm 48073849 14) (365) Site 2 0.07 ppm (13) <0.01 ppm (361) MRID 48073850 0.07 ppm (14) <0.01 ppm (391) MRID 48073851 0.06 ppm (28, <0.01 ppm 56) (379) Aquatic MRID 48073838 Not analyzed ZA1963/13 Methyl 2-oxo-{2-[6- Aerobic soil Not identified (trifluoromethyl)pyridin-2- F Anaerobic soil Waiver requested Compound 13 yloxymethyl]phenyl}-acetate F N O Aerobic aquatic Not identified F Anaerobic aquatic Not identified Hydrolysis Not identified O H C O Aqueous photolysis Not identified 3 Soil photolysis Pyridinyl label 2.0 (0.8) 0.9 (19.8) O Phenylacrylate label 2.1 (0.7-3.8) 1.2 (20.7) Field studies Not analyzed ZA1963/15 Phthalic acid Aerobic soil Not identified Anaerobic soil Waiver requested Compound 15 Aerobic aquatic Not identified O Anaerobic aquatic Not identified Hydrolysis Not identified OH O Aqueous photolysis Not identified Soil photolysis Phenylacrylate label 5.8 (13.7) 5.2 (20.7) OH Field studies Not analyzed Compound 26 2-Methoxy-6- Aerobic soil Pyridinyl Sandy loam 6.9 (364) 6.9 (364 (trifluoromethyl)pyridine label (Hyde Farm)

270 Final Maximum %AR Code Chemical name Chemical structure Study Type %AR (study (day) length) Sandy clay loam 8.2 (119) 8.2 (119) Sand 8.2 (119) 8.2 (119) Sandy loam 5.7 (119) 5.7 (119) F (Frensham) F N O F CH3

Anaerobic soil Waiver requested Aerobic aquatic Not identified Anaerobic aquatic Not identified Hydrolysis Not identified Aqueous photolysis Not identified Soil photolysis Not identified Field studies Not analyzed

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