1

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, aquaticphase 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

DuPontTM 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

. 
2

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 
3

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/R99/064 (OSCPP 850.1770, in prep.);

• Test Method 100.5: Life-cycle Test for Measuring the Effects of Sedimentassociated 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/R99/064 (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.
4

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

Assessment Endpoint Use Patterns with LOC 

Exceedances

Summarized Risk Characterization

Acute Risk to Freshwater 

Fish and Aquatic-phase 

Amphibians

Use on sorghum and soybean, 

sweet corn, field corn, popcorn 

and seed 

Use on cereal grain, excluding 

rice, canola, legume vegetables, 

dried shelled beans, and pea 

(aerial application only)

Acute LOCs Exceeded: Restricted Use and Listed Species. 

Using the peak EECs from the MS soybean and MS corn scenarios, 

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 

from the MI bean and ND wheat scenarios, there is an exceedance 

of the acute listed species LOC for listed freshwater fish and 

aquatic-phase amphibians following the proposed labeled use of 

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 

Estuarine/marine Fish

None No acute LOC exceedances for non-listed and listed 

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 

Freshwater Fish, 

Aquatic-phase 

Amphibians and 

Marine/Estuarine Fish

None No chronic LOC exceedance for non-listed and listed fish and 

aquatic-phase amphibians following picoxystrobin applications. 

Highest RQ = 0.27. A comparison of the 60-day EECs in surface 

water to the chronic toxicity value using the lowest fish NOAEC to 

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 

Invertebrates

All Proposed Uses Acute LOCs Exceeded: Restricted Use and Listed Species. 

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. 
5

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

Assessment Endpoint Use Patterns with LOC 

Exceedances

Summarized Risk Characterization

Acute Risk to 

Estuarine/Marine 

Invertebrates

All Proposed Uses Acute LOCs Exceeded: Acute Risk, Restricted Use and Listed 

Species. Using the peak EECs from the exposure scenarios 

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 

Freshwater Invertebrates

All Proposed Uses Chronic LOC Exceeded: Chronic and Listed Species. Using 21-

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 

Estuarine/Marine 

Invertebrates

Use on sorghum, soybean, 

sweet corn, field corn, seed, 

popcorn 

Chronic LOC Exceeded: Chronic and Listed Species. Using 21-

day EECs from the exposure scenarios modeled for soybean and 

corn, the RQs of 1.9-2.0 exceed the chronic risk LOC of 1 for nonlisted 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 

Invertebrates

All Proposed Uses Acute LOCs Exceeded: Acute Risk, Restricted Use and Listed 

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 soildwelling 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 soildwelling invertebrates.
6

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

Assessment Endpoint Use Patterns with LOC 

Exceedances

Summarized Risk Characterization

Chronic Risk to Benthic 

Invertebrates

Assumed for all proposed uses Laboratory data 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 

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 

Plants

None At the peak surface water EECs, there is no exceedance of the nonlisted 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.
7

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

Assessment Endpoint Use Patterns with LOC 

Exceedances

Summarized Risk Characterization

Risk to Aquatic Nonvascular Plants

Use on sorghum, soybean, 

sweet corn, field corn, seed, 

popcorn 

Use on canola, legume 

vegetables, dried shelled bean, 

cereal grains (excluding rice) 

and pea

Plant LOC Exceeded: Non-listed and Listed. There are 

exceedances of the non-listed and listed plant LOCs for nonvascular 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. 

Plant LOC Exceeded: Listed. There is an exceedance of the listed 

plant LOC for non-vascular aquatic plants. The RQs of 1.2-1.6 

exceed the LOC of 1 for potential risk to listed non-vascular 

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.
8

Table I.2. Summary of Environmental Risk Conclusions for Terrestrial Animals and Plants

Risk Conclusion Use Patterns with LOC 

Exceedances

Summarized Risk Characterization

Acute Risk to all Birds 

and smaller Passerines 

Species (including 

terrestrial-phase 

amphibians and reptiles) 

Assumed for all proposed uses In assessing the potential acute risk to birds, the lowest avian 

toxicity value of 486 mg a.i./kg-bw was compared to the highest 

EEC of 140 mg a.i./kg (maximum dose-based residue on short 

grass following applications on soybean and sorghum). In this 

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 

(including terrestrialphase amphibians and 

reptiles) 

None Using the dietary-based NOAEC and Kenaga EECs, the chronic 

risk LOC is not exceeded for potential chronic exposure to birds 

consuming any of the selected feed items modeled at the maximum 

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. 
9

Table I.2. Summary of Environmental Risk Conclusions for Terrestrial Animals and Plants

Risk Conclusion Use Patterns with LOC 

Exceedances

Summarized Risk Characterization

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 

to Soil-dwelling 

Invertebrates

None Using the estimated soil EEC and the toxicity values for earthworm 

to assess potential acute and chronic exposures to soil-dwelling 

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.
10

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 

Acute Exposures

Direct Effects from 

Chronic Exposures

Indirect Effects a

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 
11

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.
12

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.
13

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
14

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 

APROACHTM 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

DuPontTM is seeking registration for the use of the new chemical fungicide picoxystrobin 

(APROACHTM 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 
15

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 soilborne 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.
16

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

Birds1

[Oral] Bobwhite quail (Colinus virginianus)

[Oral] Zebra finch (Poephila guttata)

Practically non-toxic

Uncertain

[Dietary] Mallard duck (Anas platyrhynchos) 

[Dietary] Bobwhite quail (Colinus virginianus) All practically non-toxic

Mammals Laboratory rat (Rattus norvegicus) Practically non-toxic

Beneficial insects Honey bee (Apis mellifera L.) Practically non-toxic

Soil-dwelling 

invertebrates Earthworm (Eisenia fetida) Not classified

Freshwater fish2

Bluegill sunfish (Lepomis macrochirus)

Rainbow trout (Oncorhynchus mykiss)

Fathead minnow (Pimephales promelas)

Mirror Carp (Cyprinus carpio)

Three-spined stickleback (Gasterosteus aculeatus)

Very highly toxic to 

highly toxic 

Freshwater 

invertebrates Water flea (Daphnia magna) Very highly toxic

Estuarine/marine fish Sheepshead minnow (Cyprinodon variegatus) Highly toxic

Estuarine/marine 

invertebrates

Eastern Oyster (Crassostrea virginica)

Mysid (Americamysis bahia) All very highly toxic

Benthic Invertebrates Chironomids (Chironomus dilutes)

Amphipods (Hyalella azteca) Not classified

Terrestrial plants

[Seedling Emergence and Vegetative Vigor] Monocot –

Corn, Onion, Ryegrass, Oat

[Seedling Emergence and Vegetative Vigor] Dicot –

Cucumber, Oilseed rape, Pea, Soybean, Sugar beet, Tomato

Not classified

Aquatic plants and 

algae

Vascular – Duckweed (Lemna gibba)

Non-Vascular - Green algae (Pseudokirchneriella 

subcapitata), Blue-green algae (Anabaena flos-aquae), 

Freshwater diatom (Navicula pelliculosa), Marine diatom 

(Skeletonema costatum)

Not classified

1

Birds 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.
17

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 
18

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.
19

Figure II.2. Conceptual diagram for effects of picoxystrobin uses on non-target aquatic organisms.
20

Stressor

Source

Attribute

Change

Picoxystrobin applied to use site

Direct

application Spray drift

Terrestrial 

vertebrates

Terrestrial 

invertebrates

Individual organisms

Reduced survival

Reduced growth

Reduced reproduction

Food chain

Reduction in prey and food

Modification of PCEs 

related to prey availability

Habitat integrity

Reduction in primary productivity

Reduced cover

Community change

Modification of PCEs related

to habitat

Runoff

Exposure Media Dew (formed on 

terrestrial plants)

Atmospheric 

transport

Receptors

Puddles (formed on 

treated fields)

Inhalation Ingestion

Air

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 
21

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 semiaquatic 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 
22

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 
23

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-in10 year 60-day mean concentration is used for assessing chronic exposure for fish (and aquaticphase 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 
24

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*

Assessment Endpoint Surrogate Species and Measures of Ecological 

Effect1 Measures of Exposure

Birds, terrestrialphase 

amphibians and 

reptiles2

Survival

Lowest acute oral LD50

(zebra finch) and subacute dietary LC50 (Northern 

bobwhite quail and mallard duck)

Upper bound residues on 

food items 

Reproduction 

and growth Lowest reproduction NOAEC (duck)

Mammals

Survival Laboratory rat acute oral LD50 

Reproduction 

and growth Laboratory rat reproduction NOAEC

Freshwater fish, 

aquatic-phase 

amphibians3

Survival Lowest acute LC50 (fathead minnow) Peak EEC4

Reproduction 

and growth Lowest reproduction NOAEC (fathead minnow) 60-day average EEC4

Freshwater

invertebrates

Survival Water flea acute EC50 Peak EEC4

Reproduction 

and growth Water flea reproduction NOAEC 21-day average EEC4

Estuarine/marine fish

Survival Sheepshead minnow acute LC50 Peak EEC4

Reproduction 

and growth Sheepshead minnow reproduction NOAEC 60-day average EEC4

Estuarine/marine 

invertebrates

Survival Lowest acute EC50/LC50 (Eastern oyster) Peak EEC4

Reproduction 

and growth Mysid shrimp reproduction NOAEC 21-day average EEC4

Benthic invertebrates

Survival Eastern oyster and daphnid acute EC50

Peak sediment 

porewater EEC

Reproduction 

and growth Daphnid and mysid reproduction NOAECs 

21-day sediment 

porewater EEC

Terrestrial plants5 Survival and 

growth

Lowest EC25 for non-listed plants and corresponding 

NOAEC (or EC05) for listed plants from seedling 

emergence (monocot- ryegrass; dicot- soybean) and 

vegetative vigor (monocot- onion; dicot- cucumber) 

studies

Estimates of runoff and 

spray drift to non-target 

areas
25

Table II.3. Summary of Assessment Endpoints and Measures of Ecological Effects*

Assessment Endpoint Surrogate Species and Measures of Ecological 

Effect1 Measures of Exposure

Insects

Survival (not 

quantitatively 

assessed)

Honeybee acute contact LD50 

Maximum application 

rate

Soil-dwelling 

invertebrates

Survival Earthworm subchronic LC50 Estimates of soil 

concentration

Reproduction Earthworm subchronic NOAEC

Aquatic plants and 

algae

Survival and 

growth

Lowest EC50 for non-listed plants and corresponding 

NOAEC (or EC05) for listed plants for algal (marine 

diatom) and vascular plant (duckweed) 

Peak EEC4

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

DuPontTM 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. 
26

Table III.1. Picoxystrobin Application Information

Method of 

Application Crop

Maximum 

Application 

Rate

lb a.i./A

Maximum Number of Applications

Maximum 

Seasonal 

Use Rate 

(lb a.i./A)

Broadcast 

Foliar Spray 

(ground & 

aerial)

Field corn, 

sweet, seed, 

popcorn

Variable1

Early season application

1 application (4 fl oz) and 

Additional applications

1st application (12 fl oz) 

2nd application (12 fl oz) 

3rd application (8 fl oz) A 0.585

Cereal grains 

(except rice) Variable1

Sorghum 0.195 3 applications (7-day interval)

Soybean

(grain) 0.195 3 applications (7-day interval)

Canola 0.195

2 applications

(7-day interval) Legume 0.39

vegetables,

Dried shelled 

beans, peas

0.195

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.
27

Table III.2 General Physical and Chemical Properties of Picoxystrobin

Parameter Value Reference

PC code 129200 --

CAS No. 117428-22-5 --

Structure --

Chemical name 

(IUPAC)

Methyl(E)-2-{2-[6-(trifluoromethyl)pyridin-2-

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, 

pH 7)

3 mg/L MRID# 48073834

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 

partitioning coefficient 

Log KOW (20oC, pH 7)

3.6 MRID#48073710

Dissociation Constant 

(pKa)

N/A (No dissociation) MRID#48073710

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),

N

F

F

F

O

O

CH3

O

H3C

O
28

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 

Guideline

Data Requirement Data Summary Source

835.2120 Hydrolysis t1/2 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 

(combined radio-label half-life)*

73.7 days (sandy loam)

29.4 days (clay loam)

38.3 days (sand)

34.7 days (sandy loam)

MRID 48073837

835.4200 Anaerobic Soil Metabolism t1⁄2 at 

20°C

Waived MRID 48073838

835.4300 Aerobic aquatic metabolism t1/2 at 

20°C (sandy clay loam sediment 

system and sand system, 2 radiolabels)

39.2 days (the total system)

47.5 days (the total system)

MRID 48073839

835.4400 Anaerobic aquatic metabolism t1/2* at 

20°C (,sandy loam soil system 

combined labels)

83.5 days (the total system) MRID 48073840

835.1230 Organic carbon partitioning 

coefficient 

(Koc, mL/g oc)

837 (sandy loam)

1089 (silty clay loam)

741 (sandy loam)

933 (sandy loam)

1067 (sand)

878 (Sandy clay loam)

MRID 48073832

Freundlich adsorption value, Kf , 

mL/g oc (1/n)

4.9 (sandy loam)

22.4 (silty clay loam)

22.4 (sandy loam)

15.7 (sandy loam)

3.5 (sand)

14 (Sandy clay loam)

MRID 48073838

835.6100 Terrestrial field dissipation DT50

US soils

41.3 days (Porterville, California/Sandy loam)

34.7 days (Arkansaw, Wisconsin/Sandy loam-loamy)

MRID 48073842

MRID 48073843

Terrestrial field dissipation DT50

Foreign soils

151 days (Manitoba, Canada/Clay loam-loam)

39.4 days (Prince Edward Island, Canada/Sandy loam)

62 days (Grissoles, France/Silty clay loam)

108 days (Maidenhead, UK/Sandy clay loam)

94 days (Saxe-Anhalt, Germany/Sandy clay loam)

80 days (Cessac, France/Clay loam)

53 days (Schleswig-Holstein, Germany/Sandy loam)

80 days (Bracknell, Berkshire, UK/Sandy clay loam)

MRID 48073841

MRID 48073844

MRID 48073846

MRID 48073847

MRID 48073848

MRID 48073849

MRID 48073850

MRID 48073851

850.1730 Fish bioconcentration 

(steady state BCF ) μg/kg

1400 in viscera,

110 in flesh and

170 in the carcass.

290 in whole fish 

MRID 48073776
29

Table III.3 Environmental Fate Data Summary for Picoxystrobin

OPPTS 

Guideline

Data Requirement Data Summary Source

*: 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 halflife of 83.5 days (MRID# 48073840).
30

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.
31

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/kgorganic 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. 
32

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).
33

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

Picoxystrobin.

Input Parameter Value Source /Comment

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

Vapor Pressure at 25°C 

(torr) 4.14 X 10-8 MRID# 48073840

Solubility in Water at 

20oC, pH7 (mg·L-1) 3 MRID# 48073834

Organic carbon partition 

coefficient (Koc, mL/g oc) 799 Mean of six Koc values: 837, 1089, 741, 933, 1067, and 878; Input parameter guidance V. 2.1. ( 2009). MRID# 48073832.

Aerobic Soil Metabolism 

Half-life (days) 60.5

The 90th percentile of the upper confidence bound on the 

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 

Metabolism Half-life 

(days)

43.8

The 90th percentile of the upper confidence bound on the 

mean of 2 half-life values: 39.2, 41.5 days. Input parameter 

guidance V. 2.1. ( 2009). MRID# 48073839.

Anaerobic Aquatic 

Metabolism Half-life 

(days)

250 Single value of 83.5 days multiplied by 3; Input parameter 

guidance V. 2.1. ( 2009). MRID# 48073840.

Hydrolysis Half-lives 

(days) Stable (0) Stable. Input parameter guidance V. 2.1. ( 2009). MRID# 48073834

Aqueous Photolysis

Half-life (days) 28.9 MRID# 48073835. Input parameter guidance V. 2.1. ( 2009).

CAM 2 Input parameter guidance V. 2.1. ( 2009).

Application Efficiency 0.95 Aerial

(0.99 Ground) Input parameter guidance V. 2.1. ( 2009).

Spray Drift Fraction 0.05 Aerial

(0.01 Ground) Input parameter guidance V. 2.1. ( 2009).

*: 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.
34

Table III.5 PRZM/EXAMS Model Input Parameters for Picoxystrobin.

Use Scenario Application Rate in lbs a.i./A 

(kg a.i./ha)

Applications 

per Year

Application 

Interval 

(days) 

Application 

Method 

Field corn, 

sweet, seed, 

popcorn1

MSCornstdSTD.txt

Early season application

1 application @0.065 (0.073) 

Additional applications

1st application @ 0.195 (0.218) 

2nd application @ 0.195 (0.218) 

3rd application @ 0.13 (0.146)

4 44, 7, 7, 7 Aerial/ground

Cereal grains 

(except rice) 2 NDWheatSTD.txt 4 18, 7, 7, 7 Aerial/ground

Sorghum, 

Soybean MSsoybeanSTD.txt 0.195(0.585) 3 7 Aerial/ground

Canola,

Legume 

vegetables

Dried shelled 

beans, peas

MIbeansSTD.txt 0.195

(0.390) 2 7 Aerial/ground

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
35

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 
36

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.

Uses # of App. x App. Rate Food Items Upper Bound EEC1

(mg a.i./kg diet)

Sorghum, Soybean 

3 applications at 

0.195 lb a.i./A with 7-day 

intervals

Short Grass

Tall Grass

Broadleaf Plants

Fruits, Pods, Seeds

Arthropods

123.01

56.38

69.19

7.69

48.18

Cereal grains (except 

rice)

4 applications; first app at 

0.065 lb a.i/A, after 18 days 

2nd, 3rd, 4th app at 

0.195, 0.195, 0.13 lb a.i./A 

with 7-day intervals

Short Grass

Tall Grass

Broadleaf Plants

Fruits, Pods, Seeds

Arthropods

115.69

53.02

65.07

7.23

45.31

Sweet corn, Field corn, 

seed, popcorn

4 applications; first app at 

0.065 lb a.i/A, after 44 days 

2nd, 3rd, 4th app at 

0.195, 0.195, 0.13 lb a.i./A 

with 7-day intervals 

Short Grass

Tall Grass

Broadleaf Plants

Fruits, Pods, Seeds

Arthropods

112.36

51.50

63.20

7.02

44.01

Canola,

Legume vegetables,

Dried shelled beans, peas

2 applications at 

0.195 lb a.i./A with 7-day 

intervals

Short Grass

Tall Grass

Broadleaf Plants

Fruits, Pods, Seeds

Arthropods

87.54

40.12

49.24

5.47

34.29 1 Used to determine the potential risk to non-target wildlife and the need to consider regulatory action.
37

Table III.9. Terrestrial Dose-Based EECs (Birds) Following Picoxystrobin Spray Application.

Uses # of App. x App. 

Rate Food items

Avian Classes and Body Weights

small mid large

20 g 100 g 1000 g

Upper Bound EEC (mg a.i./kg bw)1

Sorghum, Soybean 

3 applications at 

0.195 lb a.i./A with 

7-day intervals

Short Grass 140.10 79.89 35.77

Tall Grass 64.21 36.62 16.39

Broadleaf Plants 78.80 44.94 20.12

Fruits, Pods 8.76 4.99 2.24

Arthropods 54.87 31.29 14.01

Seeds 1.95 1.11 0.50

Cereal grains (except 

rice)

4 applications; first 

app at 0.065 lb a.i/A, 

after 18 days 2nd, 3rd, 

4th app at 

0.195, 0.195, 0.13 lb 

a.i./A with 7-day 

intervals

Short Grass 131.76 75.13 33.64

Tall Grass 60.39 34.44 15.42

Broadleaf Plants 74.11 42.26 18.92

Fruits, Pods 8.23 4.70 2.10

Arthropods 51.60 29.43 13.17

Seeds 1.83 1.04 0.47

Sweet corn, Field corn, 

seed, popcorn

4 applications; first 

app at 0.065 lb a.i/A, 

after 44 days 2nd, 3rd, 

4th app at 

0.195, 0.195, 0.13 lb 

a.i./A with 7-day 

intervals 

Short Grass 127.96 72.97 32.67

Tall Grass 58.65 33.44 14.97

Broadleaf Plants 71.98 41.05 18.38

Fruits, Pods 8.00 4.56 2.04

Arthropods 50.12 28.58 12.80

Seeds 1.78 1.01 0.45

Canola,

Legume vegetables,

Dried shelled beans, 

peas

2 applications at 

0.195 lb a.i./A with 

7-day intervals

Short Grass 99.70 56.85 25.45

Tall Grass 45.70 26.06 11.67

Broadleaf Plants 56.08 31.98 14.32

Fruits, Pods 6.23 3.55 1.59

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.
38

Table III.10. Terrestrial Dose-Based EECs (Mammalian) Following Picoxystrobin Spray Application.

Uses # of App. x App. 

Rate Food items

Mammalian Classes and Body 

Weights

small mid large

15 g 35 g 1000 g

Upper Bound EEC (mg a.i./kg bw)1

Sorghum, Soybean 

3 applications at 

0.195 lb a.i./A with 

7-day intervals

Short Grass 117.28 81.06 18.79

Tall Grass 53.75 37.15 8.61

Broadleaf Plants 65.97 45.59 10.57

Fruits, Pods 7.33 5.07 1.17

Arthropods 45.93 31.75 7.36

Seeds 1.63 1.13 0.26

Cereal grains (except 

rice)

4 applications; first 

app at 0.065 lb a.i/A, 

after 18 days 2nd, 3rd, 

4th app at 

0.195, 0.195, 0.13 lb 

a.i./A with 7-day 

intervals

Short Grass 110.30 76.23 17.67

Tall Grass 50.55 34.94 8.10

Broadleaf Plants 62.04 42.88 9.94

Fruits, Pods 6.89 4.76 1.10

Arthropods 43.20 29.86 6.92

Seeds 1.53 1.06 0.25

Sweet corn, Field corn, 

seed, popcorn

4 applications; first 

app at 0.065 lb a.i/A, 

after 44 days 2nd, 3rd, 

4th app at 

0.195, 0.195, 0.13 lb 

a.i./A with 7-day 

intervals 

Short Grass 107.12 74.04 17.17

Tall Grass 49.10 33.93 7.87

Broadleaf Plants 60.26 41.65 9.66

Fruits, Pods 6.70 4.63 1.07

Arthropods 41.96 29.00 6.72

Seeds

1.49 1.03 0.24

Canola,

Legume vegetables,

Dried shelled beans, 

peas

2 applications at 

0.195 lb a.i./A with 

7-day intervals

Short Grass 83.46 57.69 13.37

Tall Grass 38.25 26.44 6.13

Broadleaf Plants 46.95 32.45 7.52

Fruits, Pods 5.22 3.61 0.84

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 
39

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. 
40

TABLE III.11. EECs for Terrestrial Plants Located Adjacent to Picoxystrobin (broadcast spray 

application) Treated Sites. 

Sites

Application 

Method

(Non-granular)

Concentration (lbs a.i./A)

Total Loading to 

Areas Adjacent to 

Treated Areas1

Total Loading to SemiAquatic Areas Adjacent 

to Treated Areas2

Drift to 

Adjacent Areas3

All Proposed Uses Ground Unincorp. 4

Aerial 5

0.0039

0.0117

0.02145

0.02925

0.00195

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 
41

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 Meanmeasured

LC50 (μg a.i./L)

Toxicity 

Category

MRID No.

Author/Year

Study 

Classification

Rainbow trout

(Oncorhynchus mykiss) 96.6 70 A Very highly 

toxic

48073769 

Kent & Shillabeer. 

(1996)

Acceptable

Bluegill sunfish

(Lepomis macrochirus) 93.3 77 B Very highly 

toxic

48073770

Kent & Shillabeer. 

(1997)

Acceptable

Mirror carp 

(Cyprinus carpio)

93.3 160C Highly 

toxic

48258010

Kent, Shillabeer & 

Long. (1997)

Acceptable

Fathead minnow 

(Pimephales promelas) 93.3 65D Very highly 

toxic

48258008

Kent & Shillabeer. 

(1997)

Acceptable

Three-spined 

stickleback 

(Gasterosteus 

aculeatus)

93.3 100 E Highly 

toxic

48258012

Kent & Shillabeer. 

(1997)

Acceptable

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. 
42

Table III.13. Freshwater Fish Acute Toxicity with Picoxystrobin Transformation Products.

Species Transformation 

Product

% Nominal

LC50 (mg deg/L)

Toxicity 

Category

MRID No.

Author/Year

Study 

Classification

Fathead minnow 

(Pimephales 

promelas)

Compound # 7 >99 >10

No more 

than 

slightly 

toxic

48258014 

Magor &

Shillabeer. 

(1997)

Acceptable

Compound # 3 100 >10

No more 

than 

slightly 

toxic

48258016

Magor & 

Shillabeer. 

(1998)

Acceptable

Compound # 2 99 >10

No more 

than 

slightly 

toxic

48258018

Magor & 

Shillabeer. 

(1998)

Acceptable

Compound # 8 100 >10

No more 

than 

slightly 

toxic

48258020

Magor & 

Shillabeer. 

(1998)

Acceptable

Rainbow trout

(Oncorhynchus 

mykiss)

Compound # 26 98 >10

No more 

than 

slightly 

toxic

48258022

Magor & 

Shillabeer. 

(1999)

Acceptable

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

LC50 (μg a.i./L)

Toxicity 

Category

MRID No.

Author/Year

Study 

Classification

Rainbow trout

(Oncorhynchus mykiss) 93.3

51A

(220 μg 

product/L)

Very highly

toxic

48073771 

Kent & Shillabeer. 

(1997)

Acceptable

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.
43

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 % 

a.i.

48-hour Meanmeasured EC50

(μg a.i./L)

Toxicity 

Category

MRID No.

Author/Year

Study 

Classification

Water flea

(Daphnia magna) 93.3 24 A Very highly 

toxic

48073764

Kent & Shillabeer. 

(1997)

Acceptable

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 

Product

% Nominal

EC50

(mg deg/L)

Toxicity 

Category

MRID No. 

Author/Year

Study 

Classification

Water flea

(Daphnia 

magna)

Compound # 7 >99 >10 No more than 

slightly toxic

48258015 

Magor & 

Shillabeer. 

(1998)

Acceptable

Compound # 3 100 >10 No more than 

slightly toxic

48258017 

Magor & 

Shillabeer. 

(1998)

Acceptable

Compound # 2 99 >10 No more than 

slightly toxic

48258019 

Magor & 

Shillabeer. 

(1998)

Acceptable

Compound # 8 100 >10 No more than 

slightly toxic

48258021 

Magor & 

Shillabeer. 

(1998)

Acceptable

Compound # 26 98 8.0A No more than 

slightly toxic

48258023 

Magor & Acceptable
44

Table III.16. Freshwater Invertebrate Acute Toxicity with Picoxystrobin Transformation 

Products.

Species Transformation 

Product

% Nominal

EC50

(mg deg/L)

Toxicity 

Category

MRID No. 

Author/Year

Study 

Classification

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 Meanmeasured

EC50 (μg a.i./L)

Toxicity 

Category

MRID No.

Author/Year

Study 

Classification

Water flea

(Daphnia magna) 93.3

20A

(86 μg 

product/L)

Very highly 

toxic

48073765

Kent & Shillabeer. 

(1997)

Acceptable

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.

Species % a.i.

96-hour Meanmeasured LC50

(μg a.i./L)

Toxicity 

Category

MRID No.

Author/Year

Study 

Classification

Sheepshead minnow

(Cyprinodon variegatus)

99.3 330* Highly toxic 48073768

Fournier. 2009. Acceptable

* Minnow 95% C.I. = 200-520 μg a.i./L; Probit slope = N/A (binomial method)
45

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 

Species % a.i.

96-hour Meanmeasured

LC50/EC50

(μg a.i./L)

Toxicity 

Category

MRID No.

Author/Year

Study 

Classification

Eastern oyster

(shell deposition)

(Crassostrea virginica)

99.3 EC50 = 5.7 A Very highly 

toxic

48073766

Duncan and York. 2009. Acceptable

Mysid

(Americamysis bahia) 99.3 LC50 = 33 B Very highly 

toxic

48073767

Fournier. 2009. Acceptable

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.
46

Table III.20. Freshwater Fish Early Life-Stage Toxicity with Picoxystrobin TGAI 

Species % 

a.i.

Meanmeasured 

NOAEC 

(μg a.i./L)

Meanmeasured 

LOAEC 

(μg a.i./L)

Endpoints 

Affected

MRID No.

Author/Year

Study 

Classification

Fathead minnow

(Pimephales 

promelas)

93.3 36 73

Embryo 

hatching and 

larval survival 

and growth

48073775

Kent and 

Shillabeer. 1997.

acceptable

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 % 

a.i.

Meanmeasured 

NOAEC 

(μg a.i./L)

Meanmeasured 

LOAEC 

(μg a.i./L)

Endpoints 

Affected

MRID No.

Author/Year

Study 

Classification

Water flea

(Daphnia magna) 96.6 1 2 Length

48073772

Kent, 

Shallabeer. 

1996.

Acceptable

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.
47

Table III.22. Estuarine/marine Fish Early Life-Stage Toxicity with Picoxystrobin TGAI 

Species % 

a.i.

Meanmeasured 

NOAEC 

(μg a.i./L)

Meanmeasured 

LOAEC 

(μg a.i./L)

Endpoints 

Affected

MRID No.

Author/Year

Study 

Classification

Sheepshead minnow

(Cyprinodon 

variegatus)

99.3 21 49

Growth 

(length and 

weight)

48073774

Lee. 2009. Acceptable

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 % 

a.i.

Meanmeasured 

NOAEC 

(μg a.i./L)

Meanmeasured 

LOAEC 

(μg a.i./L)

Endpoints 

Affected

MRID No.

Author/Year

Study 

Classification

Mysid

(Americamysis 

bahia)

99.3 3.6 7.6 Offspring per 

adult

48073773

Lee. 2010. Acceptable

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.
48

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 nonvascular 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 % 

a.i.

Meanmeasured 

EC50

(μg a.i./L)

Meanmeasured 

NOAEC 

(μg a.i./L)

MRID No.,

Author/Year

Study 

Classification

VASCULAR PLANTS

Duckweed

Lemna gibba 99.3 210 A 20 48073803

Softcheck. 2010. Acceptable

NON-VASCULAR PLANTS

Marine diatom

Skeletonema costatum 99.3 4 B 2.3 48073804

Softcheck. 2010. Acceptable

Freshwater blue-green algae

Anabaena flos-aquae

99.3 >3000 C 3000 48073805

Dengler. 2010. Acceptable

Freshwater diatom

Navicula pelliculosa 99.3 N/A N/A 48073806

Softcheck. 2010. Invalid1

Freshwater green algae

Pseudokirchneriella 

subcapitata

96.6 26 D 4.4

48258024

Smyth, Kent, 

Shillabeer. 1999.

Acceptable
49

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

Species % 

a.i.

Meanmeasured 

EC50

(μg a.i./L)

Meanmeasured 

NOAEC 

(μg a.i./L)

MRID No.,

Author/Year

Study 

Classification

VASCULAR PLANTS

Duckweed

Lemna gibba 99.3 210 A 20 48073803

Softcheck. 2010. Acceptable

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.
50

Table III.25. Toxicity of Picoxystrobin Transformation Products to Nontarget Aquatic Non-Vascular 

Plants - Tier I.

Species Transformation 

Product

% Nominal 

EC50

(mg deg/L)

Nominal 

NOAEC

(mg deg/L)

MRID No. 

Author/Year

Study 

Classification

Freshwater 

green algae

(P.subcapitata)

Compound #3 100 >10 <10

48258026 

Smyth, Magor & 

Shillabeer. 

(1998)

Supplemental1

Compound #7 >99 >10 <10

48258027 

Smyth, Magor & 

Shillabeer. 

(1998)

Supplemental1

Compound #2 99 >10 10

48258028 

Smyth, Magor & 

Shillabeer. 

(1998)

Acceptable

Compound #8 100 >10 <10

48258029 

Smyth, Magor & 

Shillabeer. 

(1998)

Supplemental1

Compound #26 98 >10 <10

48258030

Smyth, Magor & 

Shillabeer. 

(1999)

Supplemental1

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.
51

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

Species % 

a.i.

Meanmeasured 

EC50

(μg a.i./L)

Meanmeasured 

NOAEC 

(μg a.i./L)

MRID No.,

Author/Year

Study 

Classification

Freshwater green algae

Pseudokirchneriella 

subcapitata

93.3

40 A

(160 μg 

product/L)

10

(45 μg 

product/L)

48258025

Smyth, Kent, 

Shillabeer. 1997.

Acceptable

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.
52

Table III.27. Avian Acute Oral Toxicity with Picoxystrobin TGAI

Species % a.i. Nominal 

LD50

(mg a.i./kg 

bw)

Toxicity 

Category

MRID No.

Author/Year

Study 

Classification

Zebra finch 

(Poephila guttata) 99.3 >486 Uncertain 48073780

Hubbard & Beavers. 2009. Supplemental1

Northern bobwhite 

quail

(Colinus virginianus)

98.4 >2250 A Practically 

nontoxic

48073781

Gallagher et al. 1998. Acceptable2

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 LC50

(mg a.i./kg-diet)

Toxicity 

Category

MRID No.

Author/Year

Study 

Classification 

Northern bobwhite 

quail

(Colinus virginianus)

98.4 >5200 A Practically 

nontoxic

48073782

Gallagher et al. 

1998.

Acceptable

Mallard duck

(Anas platyrhynchos) 98.4 >5200 A Practically 

nontoxic

48073783

Gallagher et al. 

1998.

Acceptable

A The LD50 was greater than the highest concentration; therefore, it was not possible to calculate a probit slope and 95% 

confidence intervals.
53

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/kgbw) 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. 

Species % a.i. Test Type

Nominal LD50

(mg a.i./kg 

bw)

Affected 

Endpoints

MRID No.

Author, Year

Toxicity 

Category

Picoxystrobin TGAI

Rat

(Sprague-Dawley) 98 acute oral Females 

>50001 Mortality 48073718 Practically 

nontoxic

Picoxystrobin 250 g/L SC

Rat 23 acute oral >460 Mortality 48073720 Practically 

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 
54

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 

LD50/LC50

(μg a.i./bee)

Toxicity 

Category*

MRID No. Study 

Classification

Picoxystrobin TGAI

Honey bee 93.3

>200 (contact) Practically nontoxic 48073786

Gough and 

Jackson. 1997.

Acceptable

Not able to test1 

(oral) Not categorized Supplemental †

Picoxystrobin 250 g/L SC

Honey bee 22.5

>200 (contact) Practically nontoxic

48073787

Gough and 

Jackson. 1997.

Acceptable

>200 (oral) Not categorized 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 Meanmeasured LC50

(mg a.i./kg-soil)

56-D Meanmeasured 

NOAEC

(mg a.i./kgsoil)

MRID No.

Author/Year

Study 

Classification 

Earthworm

(Eisenia fetida) 22.34 >5A 2.5 48073811Friedrich. 2003. Acceptable

A The LD50 was greater than the highest concentration; therefore, it was not possible to calculate a probit slope 

and 95% confidence intervals.
55

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 % 

a.i.

Meanmeasured 

NOAEC 

(mg a.i./kgdiet)

Meanmeasured 

LOAEC 

(mg a.i./kgdiet)

Affected 

endpoints

MRID no.

Author/Year

Study 

classification

Northern 

bobwhite quail

(Colinus 

virginianus)

99.3 1200 >1200 None

46073784

Temple et al. 

2010.

Acceptable

Mallard duck

(Anas 

platyrhynchos)

98.4 157 481 Egg 

reproduction 

48073785

Frey et al. 

1998.

Acceptable

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.
56

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

Species % 

a.i.

Test

Type

Toxicity 

ppm (mg a.i./kg bw/day)

Affected 

Endpoints MRID No.

Rat

(Sprague 

Dawley)

99.3

Parental

NOAEL = 1000 (55.6 in P 

males; 70.3 in P females)

LOAEL = 2500 (137.5 in P 

males; 173.4 in P females)

Decreased body 

weight, body 

weight gains, 

food

consumption and 

lymphoid 

atrophy

48073739 Reproductive

NOAEL = 2500 (137.5 in 

males; 173.4 in females)

LOAEL >2500

None

Offspring

NOAEL = 1000 (55.6 in P 

males; 70.3 in P females)

LOAEL = 2500 (137.5 in P 

males; 173.4 in P females)

Decreased mean 

pup body 

weight/litter, 

body weight 

gains, and organ 

weights 

93.3 2-generation

Parental NOAEL = 50 (5.4)

LOAEL = 200 (21.5)

Decreased body 

weight, body 

weight gains, 

and food 

consumption 48073740

Reproductive NOAEL = 750 (87.2)

LOAEL = >750 None

Offspring NOAEC = 200 (21.5)

LOAEC = 750 (80)

Decreased body 

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.
57

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. 
58

Terrestrial Plants, Seedling Emergence

Table III.34. Summary of Tier I Seedling Emergence Results for Picoxystrobin 250 g/L SC *

Species Most sensitive 

endpoint

% 

Inhibition

t-Test1,2

(p-value)

Significant 

Effect?

(yes or no)

Nominal 

EC25

(lb a.i./A)

Nominal 

NOAEC

(lb a.i./A)

Study 

Classification

Corn Emergence 13 0.09 No >0.45 0.45 Supplemental3

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 *

Species Most sensitive 

endpoint

% 

Inhibition

t-Test1,2

(p-value)

Significant 

Effect?

(yes or no)

Nominal 

EC25

(lb a.i./A)

Nominal 

NOAEC

(lb a.i./A)

Study 

Classification

Corn None 0 n/a No >0.45 0.45

Supplemental3

Oat Dry weight 4 n/a No >0.45 0.45

Onion Dry weight 8 0.031 Yes A >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

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
59

* 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 

Ingredient

LD50, 

LC50, or 

EC50

(LOAEC) 

/ NOAEC

MRID No.

Author/Year

Endpoint Affected or Comments

Earthworm TGAI (mg a.i./kg soil)

Earthworm 

(Eisenia fetida) 93.3 6.7 (5.6) / 3.2 48073819Jackson & Coulson. 1997. Mortality and body weight

Earthworm TEP (mg a.i./kg soil)

Earthworm 

(Eisenia fetida) 22.34 0.89 (0.7) / 

0.47

48073812

Friedrich. 2002. Mortality and body weight

Earthworm Transformation Products (mg degradate/kg soil)

Earthworm 

(Eisenia fetida)

99% 

R403092 >1000 (1000) / 100

48073817

Lees & Gough. 1999. Body weight

100% 

R403814 320 (1000) / 100

48073816

Lees & Gough. 1998. Mortality and body weight

100% 

R408509 320 (1000) / 100

48073815

Lees & Gough. 1998. Mortality and body weight

Earthworm Field Studies with Formulated Product (g a.i./ha)

Earthworm 

populations

93.3 N/A N/A

48073807

Blake et al. Mortality higher when soil wetter

Not reported

No 

significant 

effects

N/A

48073808

Coulson et al. 2003.

14% sites where mortality exceeded 

5/m2

Not reported

No 

significant 

effects

N/A 48073809

Coulson et al. 2003.

Picoxystrobin applied up to 2 x 250 g 

a.i./ha is not expected to cause 

unacceptable effects on earthworm 

populations in the field.

Not reported 168.5 g 

a.i./ha

(<62.5) / 

<62.5g 

a.i./ha

48073810

Klein. 2004.

Recovery of total earthworm 

populations occurred 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. At a rate of 500 

g a.i./ha, a reduction in the number of 

earthworms was observed one year 
60

Table III.36. Summary of Non-Guideline Studies

Species % of 

Ingredient

LD50, 

LC50, or 

EC50

(LOAEC) 

/ NOAEC

MRID No.

Author/Year

Endpoint Affected or Comments

after application, which is probably 

resulting from a slight reduction in 

juveniles.

Not reported

No 

significant 

effects

N/A 48073813

Krück. 2003.

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.

Not reported N/A (>500) / 

500

48073814

Krück. 2003.

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.

Not reported

No 

significant 

effects

N/A 48073818

Travis and Coulson. 1999.

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.

Not reported

No 

significant 

effect

N/A 48073820

Forster and Pease. 2003.

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. 

Parasite TGAI 

Parasitic wasp

Aphidius 

rhopalosiphi

Not reported N/A N/A 48073821

Austin. 1997.

Mortality (100% in 250 and 500 g 

a.i./ha groups). No LR50 could be 

estimated with two test 

concentrations.
61

Table III.36. Summary of Non-Guideline Studies

Species % of 

Ingredient

LD50, 

LC50, or 

EC50

(LOAEC) 

/ NOAEC

MRID No.

Author/Year

Endpoint Affected or Comments

Parasite Field Study with Formulated Product

Parasitic wasp

Aphidius 

rhopalosiphi

Not reported N/A N/A

48073822

Austin. 1999.

Mortality (68.8 and 77.1% on fresh 

residues (day 0) in 250 g a.i./ha 

treatments applied once and twice, 

respectively). No LR50 could be 

estimated with two test 

concentrations.

Predator TGAI

Predatory mite

Typhlodromus pyri Not reported N/A N/A 48073824Gill & Austin. 1997.

Mortality (56 and 49% at 250 and 

500 g a.i./ha, respectively). No LR50

could be estimated with two test 

concentrations.

Predator Field Study with Formulated Product

Green Lacewing

Chrysoperla 

carnea

Not reported N/A N/A

48073823

Brown. 1999.

Mortality (32.6 and 25.9% on fresh 

residues in 250 g a.i./ha treatments 

applied once and twice, respectively)

Sediment Studies

Chironomids

Chironomus 

riparius

93.3

19 mg 

a.i./kg dry 

weight

5 mg 

a.i./kg dry 

weight

48073777

Gentle. 1997. Total adult emergence

93.3 56.4 (46.7) / 

19.6

48073778

Gentle & Rapley. 1997. Total adult emergence

Fathead minnow

Pimephales 

promelas

93.3 56.8 49 48258009

Kent & Shillabeer. 1998. Mortality

Microcosm Study with Formulated Product

Freshwater 

organisms 

population

Not reported N/A 12 μg 

a.i./litre

48073779

Cole et al. 1999.

No adverse effects on freshwater 

organisms following three 

applications at spray drift deposition 

rates up to 100 g a.i./ha. Reductions 

of macroinvertebrates were observed 

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

Oncorhynchus 

mykiss

93.3 27 10

48258011

Kent & Shillabeer. 1997.

28-Day Subchronic LC50 for 

mortality

Aquatic 

invertebrates 

(platyhelminthes, 

rotatoria, mollusca, 

annelida, insecta 

and crustacea)

95.3 Range: 5 to 

>4000 N/A 482548013

Farrelly & Prevo. 1996. Mortality
62

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 nontarget 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:
63

Table IV.1. Risk Presumptions for Terrestrial Animals 

Risk Presumption RQ LOC

Birds:

Acute Risk EEC1/LC50 or LD50/sqft2 or LD50/day3 ≥0.5

Acute Restricted Use EEC/LC50 or LD50/sqft or LD50/day (or LD50 < 50 

mg a.i./kg) ≥0.2

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

Acute Restricted Use EEC/LC50 or LD50/sqft or LD50/day

(or LD50 < 50 mg a.i./kg) ≥0.2

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

Acute Risk EEC1/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:

Non-Listed Plant Species EEC1/EC25 ≥1

Listed Plant Species EEC/NOAEC or EC05

3 ≥1

Aquatic Plants:

Non-Listed Plant Species EEC2/EC50 ≥1

Listed Plant Species EEC/NOAEC or EC05

3 ≥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 
64

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 

Scenario

Species Exposure 

Duration

Toxicity Endpoint 

Value

Endpoint Reference 

(Classification)

Freshwater Fish

Acute

Fathead minnow

Pimephales promelas

96 hour LC50 = 65 μg a.i./L Survival MRID 48258008

(Acceptable)

Chronic Early Life 

Stage NOAEC = 36 μg a.i./L

Survival, 

Reproduction, 

and Growth

MRID 48073775

(Acceptable)

Freshwater Invertebrates

Acute Water flea

Daphnia magna

48 hour EC50 = 24 μg a.i./L Immobility MRID 448073764

(Acceptable)

Chronic Life-cycle NOAEC = 1 μg a.i./L Growth MRID 48073772

(Acceptable)

Estuarine/Marine Fish

Acute Sheepshead minnow

Cyprinodon variegatus

96 hour LC50 = 330 μg a.i./L Survival MRID 48073768

(Acceptable)

Chronic Early Life 

Stage NOAEC = 21 μg a.i./L Growth MRID 48073774(Acceptable)

Estuarine/Marine Invertebrates

Acute

Eastern oyster

Crassostrea virginia

(shell deposition)

96 hour EC50 = 5.7 μg a.i./L Growth MRID 48073766

(Acceptable)

Chronic Mysid

Americamysis bahia Life Cycle NOAEC = 3.6 μg a.i./L Reproduction MRID 48073773(Acceptable)

Aquatic Plants

Nonvascular Marine diatom

Skeletonema costatum 72 hour EC50 = 4 μg a.i./L; NOAEC = 2.3 μg a.i./L Growth MRID 48073804(Acceptable)

Vascular Duckweed

Lemna gibba 7 day EC50 = 210 μg a.i./L; NOAEC = 20 μg a.i./L Growth MRID 48073803(Acceptable)
65

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.
66

Table IV.5. Picoxystrobin Acute Risk Quotients for Freshwater Fish.

Crop PRZM 

Scenario

Max. 

Single 

Rate (lb 

a.i./A)

No. 

of 

Apps

Peak 

PRZM/EXAMS

EEC

(μg a.i./L)

Freshwater Fish

Acute RQ 1

(LC50= 65 μg 

a.i./L)

Estuarine/marine 

Fish 

Acute RQ 1

(LC50= 330 μg a.i./L) 

Sorghum, 

Soybean

MS 

soybean 0.195 3 8.92 (aerial) 0.1** 0.03

8.90 (ground) 0.1** 0.03

Sweet 

Corn, field 

corn, seed, 

popcorn

MS corn Variable2 4

8.74 (aerial) 0.1** 0.03

8.34 (ground) 0.1** 0.03

Canola,

Legume 

vegetables

Dried 

shelled 

beans, peas

MI bean 0.195 2

3.62 (aerial) 0.06* 0.01

2.85 (ground) 0.04 <0.01

Cereal 

grains 

(except 

rice)

ND wheat Variable3 4

3.57 (aerial) 0.06* 0.01

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.
67

Table IV.6. Picoxystrobin Chronic Risk Quotients for Freshwater Fish.

Crop PRZM 

Scenario

Max. 

Single 

Rate 

(lb 

a.i./A)

No. 

of 

Apps

60-day 

PRZM/EXAMS

EEC

(μg a.i./L)

Freshwater Fish

Chronic RQ 1

(NOAEC = 36 

μg a.i./L)

Estuarine/marine 

Fish 

Chronic RQ 1

(NOAEC = 21 μg 

a.i./L) 

Sorghum 

and 

Soybean 

MS 

soybean 0.195 3

5.75 (aerial) 0.16 0.27

5.59 (ground) 0.16 0.27

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. 
68

Table IV.7. Picoxystrobin Acute Risk Quotients for Invertebrates.

Crop PRZM 

Scenario

Max. 

Single 

Rate (lb 

a.i./A)

No. 

of 

Apps

Peak 

PRZM/EXAMS 

EEC 

(μg a.i./L)

FW 

Invertebrates

Acute RQ 1

(EC50= 24 μg 

a.i./L)

E/M 

Invertebrates

Acute RQ1

(EC50=5.7 μg 

a.i./L) 

Sorghum, 

Soybean

MS 

soybean 0.195 3 8.92 (aerial) 0.4** 1.6***

8.90 (ground) 0.4** 1.6***

Sweet

Corn, field 

corn, seed, 

popcorn

MS corn Variable2 4 8.74 (aerial) 0.4** 1.6***

8.34 (ground) 0.4** 1.5***

Canola,

Legume 

vegetables

Dried 

shelled 

beans, peas

MI bean 0.195 2

3.62 (aerial) 0.2** 0.6***

2.85 (ground) 0.1** 0.5***

Cereal 

grains 

(except 

rice)

ND wheat Variable3 4 3.57 (aerial) 0.2** 0.6***

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.
69

Table IV.8. Picoxystrobin Chronic Risk Quotients for Freshwater Invertebrates.

Crop PRZM 

Scenario

Max. 

Single 

Rate (lb 

a.i./A)

No. 

of 

Apps

21-day 

PRZM/EXAMS

EEC

(μg a.i./L)

Freshwater 

Invertebrates

Chronic RQ 1

(NOAEC = 1 

μg a.i./L)

Estuarine/marine 

Invertebrates 

Chronic RQ 1

(NOAEC = 3.6 μg 

a.i./L) 

Sorghum, 

Soybean

MS 

soybean 0.195 3 7.31 (aerial) 7.3* 2.0*

7.29 (ground) 7.3* 2.0*

Sweet 

Corn, field 

corn, seed, 

popcorn

MS corn Variable2 4

7.12 (aerial) 7.1* 2.0*

6.75 (ground) 6.8* 1.9*

Canola,

Legume 

vegetables

Dried 

shelled 

beans, peas

MI bean 0.195 2

2.97 (aerial) 3.0* 0.8

2.55 (ground) 2.6* 0.7

Cereal 

grains 

(except 

rice)

ND 

wheat Variable3 4

3.06 (aerial) 3.1* 0.9

2.27 (ground) 2.3* 0.6

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 
70

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.

Crop PRZM 

Scenario

Max. 

Single 

Rate (lb 

a.i./A)

No. 

of 

Apps

Peak 

PRZM/EXAMS 

EEC

(μg a.i./L)

Non-Listed Plant RQs1

Duckweed

(EC50 = 210 

μg a.i./L)

Diatom 

(EC50 = 4 μg

a.i./L)

Sorghum, 

Soybean

MS 

soybean 0.195 3

8.92 (aerial) <0.1 2.2*

8.90 (ground) <0.1 2.2*

Sweet Corn, field 

corn, seed, 

popcorn

MS corn Variable2 4

8.74 (aerial) <0.1 2.2*

8.34 (ground) <0.1 2.1*

Canola,

Legume 

vegetables

Dried shelled 

beans, peas

MI bean 0.195 2

3.62 (aerial) <0.1 0.9

2.85 (ground) <0.1 0.7

Cereal grains 

(except rice)

ND 

wheat Variable3 4

3.57 (aerial) <0.1 0.9

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.
71

Table IV.10. Picoxystrobin Risk Quotients for Listed Aquatic Plants.

Crop PRZM 

Scenario

Max. 

Single 

Rate (lb 

a.i./A)

No. 

of 

Apps

Peak 

PRZM/EXAMS 

EEC

(μg a.i./L)

Listed Plant RQs

Duckweed

(NOAEC = 

20 μg a.i./L)

Diatom 

(NOAEC = 2.3 

μg a.i./L)

Sorghum, 

Soybean

MS 

soybean 0.195 3

8.92 (aerial) 0.4 3.9*

8.90 (ground) 0.4 3.9*

Sweet Corn, field 

corn, seed, 

popcorn

MS corn Variable2 4

8.74 (aerial) 0.4 3.8*

8.34 (ground) 0.4 3.6*

Canola,

Legume 

vegetables

Dried shelled 

beans, peas

MI bean 0.195 2

3.62 (aerial) 0.2 1.6*

2.85 (ground) 0.1 1.2*

Cereal grains 

(except rice)

ND 

wheat Variable3 4

3.57 (aerial) 0.2 1.6*

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: 
72

Table IV.11. Formulas Used to Calculate Dose-Based and Dietary-Based Risk Quotients

Duration Dose or 

Dietary RQ

Surrogate 

Organism

Equation

Acute Dose-based Birds and 

mammals

Acute Daily Exposure (mg/kg-bw) / adjusted LD50 (mg/kgbw)1,2

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

Chronic Dietary-based Birds and 

mammals

EEC (mg/kg-food item) / NOAEC (mg/kg-diet)

Dose-based Mammals only EEC (mg/kg-bw) / Adjusted NOAEL (mg/kg-bw)2

1 Adj. Bird LD50 = Bird LD50 (AW/TW) (a-1) 

2 Adj. Mammal LD50 or NOAEL = Mammal LD50 or NOAEL (TW/AW)0.25

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.
73

Table IV.12. Picoxystrobin Toxicity Endpoint Values Used for Assessing Risk to Terrestrial Animals

Exposure 

Scenario

Species Exposure 

Duration

Toxicity Endpoint Value Endpoint Reference 

(Classification)

Mammal

Acute Oral Laboratory 

ray 

Single Oral 

Dose LD50 >5000 mg a.i./kg bw Survival MRID 48073718(Acceptable)

Chronic

Reproduction

Laboratory 

rat

2-

generation

NOAEC = 50 mg a.i./kg-diet 

(5.4 mg a.i./kg bw/day). Parental toxicity MRID 48073740(Acceptable)

Birds

Acute Oral Zebra finch Single Oral 

Dose LD50 >486 mg a.i./kg bw1 None MRID 48073780

(Supplemental)2

Subacute 

Dietary

Mallard duck 

Anas 

platyrhynchos

8 days LC50 >5200 mg a.i./kg-diet None MRID 48073782

(Acceptable)

Chronic

Mallard duck 

Anas 

platyrhynchos

one 

generation

NOAEC = 157 mg a.i./kgdiet Egg reproduction MRID 48073785

(Acceptable)

Soil-dwelling Invertebrates

Subchronic Earthworm

Eisenia fetida 28 days LC50 >5 mg a.i./kg-soilNOAEC = 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.
74

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

Site

NOAEC 

(mg/kgdiet)

EECs and RQs

Short Grass Tall Grass Broadleaf 

Plants

Fruits/Pods/

Seeds Arthropods

EEC RQ EEC RQ EEC RQ EEC RQ EEC RQ

Sorghum, 

and 

Soybeans1

157

123 0.78 56 0.36 39 0.44 8 0.05 48 0.31

Cereal 

Grains2 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, 

and Canola4 88 0.56 40 0.26 49 0.31 5.5 0.03 34 0.03

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 
75

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

Site

NOAEC 

(mg/kgdiet)

EECs and RQs

Short Grass Tall Grass Broadleaf 

Plants

Fruits/Pods/

Seeds Arthropods

EEC RQ EEC RQ EEC RQ EEC RQ EEC RQ

Sorghum, 

and 

Soybeans1

50

123 2.5 56 1.1 69 1.4 7.7 0.2 48 0.96

Cereal 

Grains2 116 2.3 53 1.06 65 1.3 7.2 0.1 45 0.9

Corn3 112 2.3 52 1.03 63 1.3 7.0 0.1 44 0.9

Peas, 

Beans, and 

Canola4

88 1.8 40 0.8 49 0.98 5.5 0.1 34 0.7

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
76

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

Site

Size 

Class

(grams)

Adjusted 

NOAEL1

EECs and RQs

Short Grass Tall Grass Broadleaf 

Plants

Fruits/Pods/

Seeds Arthropods Granivores

EEC RQ EEC RQ EEC RQ EEC RQ EEC RQ EEC RQ

Sorghum, 

and 

Soybeans1

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

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

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

Cereal 

Grains2

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

35 9.60 76.23 7.94 34.94 3.64 42.88 4.47 4.76 0.50 29.86 3.11 1.06 0.11

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

Corn3

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

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, 

Beans, 

and 

Canola4

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

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

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.
77

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 nonlisted 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 

Scenario

Species Exposure 

Duration

Toxicity Endpoint 

Value

Endpoint Reference 

(Classification)

Terrestrial Plants

Seedling 

Emergence

Monocot –

ryegrass

21-day 

limit dose 

EC25 >0.45 lb a.i./A; 

NOAEC = 0.45 lb a.i./A None

MRID 48073801

(Supplemental) Dicot – 1

soybean 

EC25 >0.45 lb a.i./A; 

NOAEC <0.45 lb a.i./A

Significant 

difference 

observed in 

phytotoxicity

Vegetative 

Vigor

Monocot -

onion

EC25 >0.45 lb a.i./A; 

NOAEC = 0.45 lb a.i./A None

MRID 48073802

(Supplemental) 1 Dicot –

cucumber

EC25 >0.45 lb a.i./A; 

NOAEC <0.45 lb a.i./A

Significant 

difference 

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-
78

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

Scenario

Non-listed RQs Listed RQs

Terrestrial

Adjacent area

Semi-aquatic 

Adjacent area Drift TerrestrialAdjacent area

Semi-aquatic 

Adjacent area Drift

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 1

Detailed 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 
79

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 threespined 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 
80

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 aquaticphase 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). 
81

(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 
82

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 
83

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. 
84

(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.
85

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 
86

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 watersediment 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 sedimentdwelling 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/R99/064 (OSCPP 850.1770, in prep.);

• Test Method 100.5: Life-cycle Test for Measuring the Effects of Sedimentassociated Contaminants on Chironomus dilates (formerly known as C. tentans) 
87

in USEPA 2000 Methods for Measuring the Toxicity and bioaccumulation of 

Sediment-associated Contaminants with Freshwater Invertebrates EPA 600/R99/064 (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 
88

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 nonlisted 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). 
89

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 
90

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*

Size 

Class

(grams)

Adjusted

LD50

EECs and RQs

Short 

Grass Tall Grass Broadleaf Plants Fruits/Pods Arthropods Seeds

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 sublethal 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 
91

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 
92

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. 
93

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 dosebased EECs is not available.

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). 

0.0

20.0

40.0

60.0

80.0

100.0

120.0

140.0

0

Concentration (mg ai/kg dietary item)

Days

Terrestrial Residues (upper bound estimates)

vs

Mammalian Herbivore/Insectivore LOCs (as dietary 

concentrations

Short Grass Tall Grass Broadleaf plants

Fruits/pods/seeds Arthropods Chronic LOC

Time (days)
94

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.

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. 

0.0

20.0

40.0

60.0

80.0

100.0

120.0

0 15 30 45 60 75 90 105 120 135 150

Concentration (mg ai/kg dietary item)

Days

Terrestrial Residues (upper bound estimates)

vs

Mammalian LOCs (as dietary concentrations)

Short Grass Tall Grass Broadleaf plants

Fruits/pods/seeds Arthropods Chronic LOC

Time (days)
95

(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 picoxystrobintreated 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 limitdose 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 picoxystrobintreated 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 
96

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.
97

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.
98

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 
99

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 

Acute Exposures

Direct Effects from 

Chronic Exposures

Indirect Effects a

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 
100

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

Taxa (study type) Acute Effect

Slope (95% C.I.)

Chance of Individual Effect 

at Listed Species LOC 

(95% C.I.)

Chance of Individual Effect at 

Derived Acute RQ (95% 

C.I.)1,2,3

Bird oral dose

No mortality observed for 

upland game birds; 

uncertain for passerines

Not calculated; no mortality 

observed

Not calculated; no mortality 

observed

Bird dietary No mortality observed Not calculated; no mortality 

observed

Not calculated; no mortality 

observed

Fish

Mortality 

Default Slope = 4.5 

(2 – 9)

1 in 4.18E+08

(1 in 216 to 1 in 1.75E+31)

1 in 2.94E+5

(1 in 44 to 1 in 8.86E+18)A

1 in 5.22E+7

(1 in 138 to 1 in 5.04E+27)B

Freshwater 

Invertebrates

Immobilization 

Default Slope = 4.5 

(2 – 9)

1 in 4.18E+08

(1 in 216 to 1 in 1.75E+31)

1 in 27.3

(1 in 5 to 1 in 5850)C

1 in 121

(1 in 12.3 to 1 in 6.33E+8)D

Estuarine/marine 

Invertebrates

Shell deposition

Default Slope = 4.5 

(2 – 9)

1 in 4.18E+08

(1 in 216 to 1 in 1.75E+31)

1 in 1.22

(1 in 1.52 to 1 in 1.03)E

1 in 6.29

(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 
101

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.
102

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.
103
104

Appendix A

Major degradates of picoxystrobin (constituting greater than 10% of the applied radiation 

from environmental fate studies, or of toxicological concern)

Compound 2 (IN-QDY62 R403092)

Compound 3

(IN-QDK50 R403814)

Compound 4

N

F

F

F

O

O

CH3

HO

O

N O

F H

F

F

N

F

F

F

O

O

H3C

O O

CH3
105

Compound 7 (IN-QFA35)

Compound 12

Compound 8 (IN-QDY63)

N

F

F

F

O

HO

O

N

F

F

F

O

O

H3C

O

OH

N

F

F

F

O

O

OH
106

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 (<LOD), <0.40, 7.8, 14, 27, 49, 100 and 190 μg a.i./L (78-110% of nominal 

concentrations). Results are based on mean measured concentrations. There were no mortalities 

in the controls throughout the study. After 24 hours of exposure, 100% of the fish were dead in 

the 100 and 190 μg a.i./L mean measured test concentrations. At 72 hours, the lid of the mean 

measured 7.8 μg a.i./L test tank was observed to be incorrectly positioned. Three of the fish had 

jumped out of the tank the previous night and died. These mortalities were considered not to be 

treatment-related and did not affect the validity of the study. The 96-hour LC50 (reviewercalculated) and NOAEC for mortality, based on mean measured concentrations were 70 μg a.i./L 

and 49 μg a.i./L, respectively. The only general symptom of toxicity noted was dark 

discoloration, and was observed in one fish in the 27 μg a.i./L mean measured test concentration 

at 72 hours, and in one fish in the 49 μg a.i./L mean measured test concentration throughout the 

study period. The NOAEC for symptoms of toxicity (discoloration) was 14 μg a.i./L, based on 

mean measured concentrations.

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 

(<LOD), <1.0, 16, 26, 46, 83 and 170 μg a.i./L (81-94% of nominal concentrations; individual 

measurements ranged from 68-106% of nominal values). Results are based on mean measured 

concentrations. No mortalities were observed in the controls throughout the study. No mortalities 

were observed in the controls or in the test concentrations up to and including the mean 

measured 46 μg a.i./L test concentrations. In the mean measured 83 μg a.i./L test concentration, 

50% of the fish were dead after 24 hours, and 60% mortality was observed at 48, 72 and 96 

hours. All of the fish were dead after 24 hours in the mean measured 94 μg a.i./L test 

concentration. The reviewer-calculated 96-hour LC50 and NOAEC for mortality, based on mean 
107

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 

(<LOD), <1.2, 18, 32, 58, 100 and 180 μg a.i./L (98-104% of nominal concentrations; individual 

measurements ranged from 94-106% of nominal values). Results are based on nominal 

concentrations. No mortalities were observed in the controls or in the test concentrations up to 

and including the nominal 32 μg a.i./L test concentrations. In the 56 μg a.i./L test concentration, 

10% of the fish were dead after 24 hours, and 20% mortality was observed at 48, 72 and 96 

hours. All of the fish were dead after 24 hours in the 100 and 180 μg a.i./L test concentrations. 

The 96-hour LC50 and NOAEC (mortality), based on nominal concentrations were 65 μg a.i./L 

and 56 μg a.i./L (reviewer-calculated), respectively. No sublethal symptoms of toxicity were 

noted throughout the study period; the 96-hour EC50 and NOAEC (sublethal symptoms), based 

on nominal concentrations were >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 

(<LOD), <1.2, 24, 37, 63, 110, 190 and 340 μg a.i./L (106-131% of nominal concentrations; 

individual measurements ranged from 96-144% of nominal values). Results are based on mean 

measured concentrations. No mortalities were observed in the controls or in the test 

concentrations up to and including the mean measured 110 μg a.i./L test concentrations. In the 

mean measured 190 μg a.i./L test concentration, 90% of the fish were dead after 24, 48, 72 and 

96 hours. All of the fish were dead after 24 hours in the mean measured 340 μg a.i./L test 

concentration. The 96-hour LC50 and NOAEC for mortality, based on mean measured 

concentrations were 160 μg a.i./L and 110 μg a.i./L, respectively, when compared to pooled 

controls. No symptoms of toxicity, other than mortalities, were observed during the course of 

this study.

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 (<LOD), <0.75, 20, 35, 55, 91 and 180 μg a.i./L (91-110% of nominal 

concentrations; individual measurements ranged from 82-119% of nominal values). Results are 

based on nominal concentrations. No mortalities were observed in the controls or in the test 

concentrations up to and including the mean measured 55 μg a.i./L test concentrations. In the 

nominal 100 μg a.i./L test concentration, 30% of the fish were dead after 24 hours, and 40% 

mortality was observed at 48, 72 and 96 hours. All of the fish were dead after 24 hours in the 

nominal 180 μg a.i./L test concentration. The 96-hour LC50 and NOAEC for mortality, based on 
108

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 (<LOD) and 10 mg/L. Concentrations post-centrifugation were 

similar. Results are based on nominal concentrations. No mortalities or sublethal effects were 

observed in any test group throughout the study. The 96-hour LC50 was >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 (preand post centrifugation) were <0.022 (<LOD) and 11 mg/L. Results are based on nominal 

concentrations. No mortalities or sublethal effects were observed in any test group 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: 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 

(<LOD) and 11 mg/L. Concentrations post-centrifugation were similar. Results are based on 

nominal concentrations. No mortalities or sublethal effects were observed in any test group 

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: 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 (<LOD) and 11 mg/L. Concentrations post-centrifugation were similar. Results are based 

on nominal concentrations. No mortalities or sublethal effects were observed in any test group 
109

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 (<LOD) and 9.4 mg/L. The test vessels were sealed, as the test compound has been 

shown to volatilize under laboratory conditions. Results are based on nominal concentrations. No 

mortalities or sublethal effects were observed in the control or the nominal 10 mg/L test groups 

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).

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 treatmentrelated. 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 

(<LOQ, control), <0.58, 4.8, 10, 19, 27, 36 and 73 μg a.i./L (90-100% of nominal 

concentrations). The test system was maintained at 25 ± 1°C and a pH of 7.16-7.98. No

treatment-related effects on time to hatch or time to swim-up were observed during the study. 
110

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 
111

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 
112

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 (<LOD), <1.71, 67, 110, 200, 310 and 520 μg a.i./L (68-104% of 

nominal concentrations). Results are based on mean measured concentrations. After 96 hours of 

exposure, mortality of sheepshead minnow exposed to mean measured picoxystrobin 

concentrations of 67, 110, 200, 310 and 520 μg a.i./L was 0, 0, 0, 43 and 100%, respectively. 

There were no mortalities in the controls throughout the study. The 96-hour LC50 and NOAEC 

for mortality, based on mean measured concentrations were 330 μg a.i./L and 200 μg a.i./L, 

respectively. After 6 hours of exposure, one fish was observed at be on the bottom of the test 

vessel at the 310 μg a.i./L test concentration and one fish exhibited partial loss of equilibrium at 

the 520 μg a.i./L test concentration. After 24 hours of exposure, one fish was observed to be on 

the bottom of the test vessel at both the 310 and the 520 μg a.i./L test concentrations; however, 
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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 (<LOD), <0.06 (<LOD), 5.2, 11, 

21, 49 and 100 μg a.i./L. The test system was maintained at 24 to 28°C and a pH of 7.6 to 8.1. 

No treatment-related effects on time to hatch were observed during the study. The percent 

hatching success was 99, 98, 100, 99, 100 and 97% in the pooled controls, 5.2, 11, 21, 49 and 

100 μg a.i./L test concentrations, respectively. Larval survival at 28 days post hatch was 96% in 

the pooled controls, and 90, 98, 95, 93 and 0% in the 5.2, 11, 21, 49 and 100 μg a.i./L test 

concentrations, respectively. All of the live larvae in all treatments but the 100 μg a.i./L test 

concentration were observed to be normal at hatching. Mean total length of larvae at 28 days 

post hatch was 26.5, 26.6, 26.0, 26.2 and 25.0 mm in the pooled controls, 5.2, 11, 21, and 49 μg 

a.i./L test concentrations, respectively. Mean larval weight at 28 days post hatch was 0.0707, 

0.0727, 0.0682, 0.0686 and 0.0624 mg in the pooled controls, 5.2, 11, 21, and 49 μg a.i./L test 

concentrations, respectively. A significant difference in embryo hatching success, larval survival, 

percent of normal larvae at 28 days post hatch was observed at the mean measured 100 μg a.i./L 

test concentration, relative to the pooled controls. A significant difference in larval growth – total 

length and dry weight at test termination was observed among organisms exposed to the 49 μg 

a.i./L mean measured test concentration relative to the pooled control. The most sensitive 33-day 

NOAEC and LOAEC (based on mean measured concentrations) were 21 and 49 μg a.i./L, 

respectively, based on effects on larval growth – total length and dry weight at test termination. 

No sub-lethal clinical signs of toxicity were observed and reported.

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 <LOD, <LOD, 1.4, 2.3, 4.5, 7.7, and 12 

μg a.i./L. Mortality and shell deposition were observed daily. No mortality was observed in the 

dilution water control, solvent control or treatment groups. After 96 hours, the reviewercalculated mean percent inhibition in shell growth compared to pooled controls was 21, 30, 43, 

70 and 64% in the 1.4, 2.3, 4.5, 7.7, and 12 μg a.i./L test concentrations, respectively. The 96-

hour EC50 based on shell deposition and mean measured concentrations was 5.7 μg a.i./L, when 

compared to the blank control. The NOAEC based on inhibition of shell growth and mean 
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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; meanmeasured 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 

(<LOD, negative control), <0.006 (solvent control), 7.9, 20, 49, 160, 340 and 1000 μg a.i./L 

under static-renewal conditions. The percent inhibition of frond density compared to pooled 

controls after 7 days ranged from -7% (stimulation) at 7.9 μg a.i./L to 70% in the 1000 μg a.i./L 

test concentration. The percent inhibition of yield, calculated from frond density, compared to 

pooled controls after 7 days ranged from -8% at 7.9 μg a.i./L to 73% at 1000 μg a.i./L. The 
115

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 
116

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 
117

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 

(<LOD) and 11 mg R403814/L. Results are based on nominal concentrations. After 3 days, the 

percent inhibition in cell density relative to the control was 13%. The percent inhibition in 

biomass (0-3 days) expressed as area under the growth curve relative to the control was 14%. 

The percent inhibition in growth rate (0-3 days) relative to the control was 3%. Statistically 

significant differences were found for cell density, biomass and growth rate compared to the 

control. The 3-day NOAEC for cell density, biomass (as area under the curve), and average 

growth rate was <10 mg R403814/L, the only concentration tested. The LOAEC was 10 mg 

R403814/L. The EC50 could not be determined because only one concentration was tested. The 

EC50 was >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 

(<LOD) and 10 mg R408631/L. Results are based on nominal concentrations. After 3 days, the 

percent inhibition in cell density relative to the control was 21%. The percent inhibition in 

biomass (0-3 days) expressed as area under the growth curve relative to the control was 21%. 

The percent inhibition in growth rate (0-3 days) relative to the control was 4%. The 3-day 

NOAEC for cell density, biomass (as area under the curve), and average growth rate was <10 mg 

R408631/L the only concentration tested. The LOAEC was 10 mg R408631/L. The EC50 was 

>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 
118

<0.058 (<LOD) and 11 mg R403092/L. Results are based on nominal concentrations. After 3 

days, the percent inhibition in cell density relative to the control was -3% (amplification). The 

percent inhibition in biomass (0-3 days) expressed as area under the growth curve relative to the 

control was -7% (stimulation). The percent inhibition in growth rate (0-3 days) relative to the 

control was 0%. The 3-day NOAEC for cell density, biomass (as area under the growth curve) 

and average growth rate was 10 mg R403092/L, the only concentration tested. EC50s and 

LOAECs could not be determined because only one concentration was tested. They are >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 (<LOD) and 11 mg R408509/L. Results are based on nominal concentrations. After 3 

days, the percent inhibition in cell density relative to the control was 14%. The percent inhibition 

in biomass (0-3 days) expressed as area under the growth curve relative to the control was 16%. 

The percent inhibition in growth rate (0-3 days) relative to the control was 3%. The 3-day 

NOAEC for cell density, biomass (as area under the curve), and average growth rate was <10 mg 

R408509/L, the only concentration tested. The LOAEC was 10 mg R408509/L. The EC50 was 

>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 (<LOD) and 9.5 mg R413834/L. Results are based on nominal concentrations. After 3 

days, the percent inhibition in cell density relative to the control was 28%. The percent inhibition 

in biomass (0-3 days) expressed as area under the growth curve relative to the control was 22%. 

The percent inhibition in growth rate (0-3 days) relative to the control was 6%. The 3-day

NOAEC for cell density, biomass (as area under the curve), and average growth rate was <10 mg 

R413834/L the only concentration tested. The LOAEC was 10 mg R413834/L. The EC50 was 

>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 
119

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.
120

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 (reviewercalculated). 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 
121

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 <LOD (control), 294, 602, 1190 mg a.i./kg diet, respectively. Reproductive parameters 

were measured beginning at the onset of egg laying. There were no apparent treatment-related 

effects on adult mortality, signs of toxicity, behavior, body weight, feed consumption, 

reproductive performance, egg shell thickness or offspring body weight at any of the 

concentrations tested throughout the study. The NOAEC for northern bobwhite quail exposed to 

picoxystrobin in the diet was 1200 mg a.i./kg diet (1190 mg a.i./kg diet; mean-measured), the 

highest concentration tested. This is equivalent to 110.3 mg a.i./kg bw/day. 

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 <LOD (control), 157, 481, 1430 mg a.i./kg diet. Reproductive parameters 

were measured beginning at the onset of egg laying. The study author reported there may have 

been an initial aversion to diet containing the test substance in the 1350 mg a.i./kg diet group. 

Feed consumption was significantly reduced during the first week of the study in this group 

compared to the control, but subsequently increased during Weeks 3 to 7. There was also a 

transient loss of body weight observed at the 1350 mg a.i./kg diet treatment group during the first 

two weeks of the study; by adult termination, body weight in the 1350 mg a.i./kg diet group was 
122

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 DPXYT669 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 
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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 

Gains

Food 

Consumption

Food Efficiency

Males Females Males Females Males Females Males Females

P Generation

Pre-mating ↓4-

7%

↓5-7% ↓18% ↓26% ↓7% ↓8% ↓11% ↓19

Gestation ↓7-8% ↓8% ↓10% −

Lactation ↓7-8% ↑223% ↓16-

20%

−

F1 Parental Rats

Pre-mating 10-

26%↓

9-27%↓ ↓8% ↓5% ↓9% ↓9% − ↑5%

Gestation ↓8% ↓9% ↓8% −

Lactation ↓6-10% ↑304% ↓12% at 

LD 11-

15

↑64%

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) nongravid 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 
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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; precoital 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
125

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 
126

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 (reviewercalculated).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 (reviewercalculated). 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 
127

(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 
128

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 sedimentwater 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 (<LOD), <0.1, 1.2, 2.2, 5, 

9.1, 20, 40 and 77 mg a.i./kg on Day 0 and <0.1, <0.1, 0.96, 2.0, 4.2, 7.6, 17, 36 and 70 mg 

a.i./kg on Day 28. Measured water concentrations were <0.005 (<LOD), <0.005, 0.006, 0.021, 

0.054, 0.12, 0.27, 0.60 and 1.3 mg a.i./L on Day 0 and <0.0005, <0.0005, 0.004, 0.010, 0.026, 

0.057, 0.17, 0.41 and 0.83 mg a.i./L on Day 28. Results are based on Day 0 measured 

concentrations in the sediment phase. Emergence began on day 13 in untreated controls and in 

the 2.2 mg a.i./kg treatment; on day 14 in the test concentrations up to 9.1 mg a.i./kg and day 15 

in the 20 mg a.i./kg treatment. 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. No difference in 

development rate or in emerged sex ratio between the controls and any test concentrations were 

observed. The percent total emergence was 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. The 28-day EC50 for total emergence was 

19 mg a.i./kg (dry weight). The 28-day NOAEC and LOAEC, based on total emergence and day 

0 measured test concentrations were 5 mg a.i./kg and 9.1mg a.i./kg, respectively.

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 <LOD, <LOD, 24, 54, 118, 237, 494, 985 and 2020 μg a.i./L in 

the control, solvent control, 31.25, 62.5, 125, 250, 500, 1000, 2000 μg a.i./L (nominal) 

treatments, respectively (77-101% of nominal). Concentrations declined throughout the study, 

and were 1 to 46% on nominal values by Day 25. Average water concentrations over the 25day 

period were: 0, 0, 8.4, 19.6, 46.7, 106.5, 297.7, 667.0, and 1399 μg a.i./L in the control, solvent 

control, 31.25, 62.5, 125, 250, 500, 1000, 2000 μg a.i./L (nominal) treatments, respectively. 

Emergence began on day 11 in untreated controls, solvent controls and test concentrations up to 

and including 125 μg a.i./L and on day 12 in the 250 μg a.i./L treatment. On day 14 one adult 

emerged from one replicate in the 500 μg a.i./L treatment, no further emergence was observed at 

this test concentration. No emergence occurred in the two highest test concentrations. Total 

emergence in the untreated and solvent controls was 96 and 100% of the larvae introduced, 

respectively. Total emergence was similar in the test concentrations up to and including nominal 

62.5 μg a.i./L, ranging from 93-96%. At nominal 125, 250 and 500 μg a.i./L treatments, 

emergence was 64, 15 and 1%, respectively. Examination of the sediment from the replicates 
129

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 (<LOD), 

0.96, 6.4, 24 and 54 μg a.i./L for the control, 5, 30, 100 and 250 g a.i./ha treatments, respectively. 

Reviewer-calculated depth integrated mean measured concentrations for all three applications 

were <0.15 (<LOD), 0.54, 3.2, 12 and 29 μg a.i./L for the control, 5, 30, 100 and 250 g a.i./ha 

test rates, respectively. No effects were observed on phytoplankton or physicochemical 

parameters at any of the application rates. No adverse ecological effects on zooplankton and 

macroinvertebrate communities were observed at rates up to 100 g a.i./ha (mean concentration 

over all sampling intervals of 12 μg a.i./L). The only effect observed at 100 g a.i./ha was a 

reduction in numbers of Daphnia spp. (species diversity), although individual numbers 

(abundance) recovered rapidly within three weeks of the final application. Planktonic Crustacea 

(in particular cyclopoid copepods and Daphnia sp.) were reduced at 250 g a.i./ha but had 

recovered by the end of the study (126 days). Effects on macroinvertebrates were also observed 

at 250 g a.i./ha, most notably after the third application. Effects included reductions in 

gammarids, dipteran larvae and molluscs, and increases in turbellarians, all of which showed no 

evidence of recovery during the study period (126 days). ZA1963 is not expected to cause 

adverse ecological effects on freshwater aquatic organisms following three applications at spray 

drift deposition rates up to 100 g a.i./ha and the no observed adverse ecological effect 

concentration was 12 μg a.i./litre (based on reviewer-calculated mean measured concentrations 

for all applications), based on effects on zooplankton and macroinvertebrates.

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 
130

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 
131

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 MUK16, 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 
132

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 m

2 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 
133

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 RFR01, 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 RFR04) 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 
134

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 
135

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. 
136

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 
137

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 m

2 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 
138

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 
139

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. 
140

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 
141

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 
142

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 
143

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 
144

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 (<LOD), <0.54, 36, 49, 50, 76 and 140 μg a.i./L (100-127% 

of nominal concentrations). Concentrations at 96-hours were <0.54 (<LOD), <0.54, 12, 13, 12, 

23 and 41 μg a.i./L (24-40% of nominal concentrations). Mean measured concentrations were 

<0.54 (<LOD), <0.54, 24, 31, 31, 50 and 91 μg a.i./L (62-83% of nominal concentrations). As 

most of the fish mortalities (27 out of 29) were observed within the first 24 hours of the study, 
145

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 (<LOD), <1.5, 11, 19, 34, 36 and 100 μg a.i./L (64-110% of nominal concentrations). 

Results are based on nominal concentrations. There were no mortalities in the controls or in the 

nominal concentration of 10 μg a.i./L during the study. After 4 days of exposure, 100% of the 

fish were dead in the 56 and 100 μg a.i./L nominal test concentrations. The 28-day LC50 and 

NOEC for mortality, based on nominal concentrations were 27 and 10 μg a.i./L, respectively. 

The general symptoms of toxicity noted in this study were surfacing, dark discoloration,

sounding, loss of balance, reduced feeding, quiescence, haemorrhaging, skittering, gulping air, 

damaged fins, twitching, cataracts and irregular and rapid respiration. Individual fish in the 32 μg 

a.i./L test concentration were observed to be distressed and were terminated to prevent 

unnecessary suffering on days 12, 13, 20 and 22. Similarly, one fish in the 18 μg a.i./L test 

concentration was terminated on day 25. These removed fish were counted as mortalities. The

nominal 28-day NOEC for symptoms of toxicity was 10 μg a.i./L based on nominal 

concentrations.

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, 
146

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 nonGLP 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
147

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
148

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 
149

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 
150

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

-------------------------------------------------------------------------------------
151

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
152

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. 
153

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 NiefernOeschelbronn, 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 
154

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. ER97-32, 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. 
155

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.
156

Appendix D

Submitted environmental fate studies for picoxystrobin and its degradates

Guideline MRID Study Title Status

835.2120

(161-1)

48073834 Hydrolysis Study Acceptable

835.2240

(161-2)

48073835 Photodegradation in Water Acceptable

835.2410

(161-3)

48073836 Photodegradation on Soil Supplemental

835.4100

(162-1)

48073837 Aerobic Soil Metabolism Supplemental

835.4200

(162-2)

48073838 Anaerobic Soil Metabolism Waived

845.4300

(1 62-4)

48073839 Aerobic Aquatic Metabolism Supplemental

835.4400

(1 62-3)

48073840 Anaerobic Aquatic Metabolism Supplemental

835.1230

(163-1)

48073832 Mobility/

Adsorption/Desorption

Supplemental

835.1410

(163-2)

48073833 Laboratory Volatility Supplemental

835.6100

(164-1)

48073841

48073842

48073843

48073844

48073846

48073847

48073848

48073 849

48073850

48073851

Terrestrial Field Dissipation

(North America)

Terrestrial Field Dissipation

(Europe)

Supplemental

Supplemental

Supplemental

Supplemental

Supplemental

Supplemental

Supplemental

Supplemental

Supplemental

Supplemental

835.6200

(1 64-2)

48073838 (as an

attachment to the

anaerobic soil

waiver request)

Aquatic Field Dissipation Waived

835.1730

(165-4)

48073776 Fish Accumulation Acceptable

850.7100

850.7100

850.7100

850.7100

850.7100

850.7 100

850.7100

48073725

48073726

48073727

48073728

48073729

48073730

48073731

Validation of analytical method

Validation of analytical method

Validation of analytical method

Validation of analytical method

Validation of analytical method

Validation of analytical method

Validation of analytical method

Acceptable

Acceptable

Acceptable

Acceptable

Acceptable

Acceptable

Acceptable

N/A 48073845 Non-guideline 

Comparison of precipitation, 

temperature, and soils at European 

field testing sites to those at proposed 

use sited in the US and Canada

N/A
157

Appendix E

Summary of environmental fate studies

MRID 48073834 (Hydrolysis): The hydrolysis of [pyridinyl14C]-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 [pyridinyl14C]- and 

[phenylacrylate14C]-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 temperaturecontrolled 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.
158

MRID 48073837 (Aerobic Soil Metabolism): The biotransformation of [pyridinyl-5-

14C]- and [phenylacrylate2-

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-

14

C]- 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 reverseand normal-phase TLC. Based on nonlinear regression analyses, picoxystrobin (combined labels) dissipated with reviewercalculated 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.
159

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 

[pyridinyl14C]-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 [phenylacrylate14C]-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 
160

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, INQDY62, 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.
161

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 
162

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. 
163

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, 

K1, and the depuration rate constant, K2, were determined to be 181 day-1

and 0.63 day-1, 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
164

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
165

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
166

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
167

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
168

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
169

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
170

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
171

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
172

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
173

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
174

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 weightmwt 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: APPEFF0.99 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.
175

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

IPSCND1

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
176

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 weightmwt 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
177

Application Rate:TAPP 0.218 kg/ha

Application Efficiency: APPEFF0.95 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

IPSCND1

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
178

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 weightmwt 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
179

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: APPEFF0.95 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

IPSCND1

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
180

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 weightmwt 367.3 g/mol

Henry's Law Const. henry 6.6E-9 atm-m^3/mol
181

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: APPEFF0.99 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

IPSCND1

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)
182

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
183

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 weightmwt 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: APPEFF0.95 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

IPSCND1

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)
184

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.
185

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.
186

Appendix H. KABAM

Table H1. Chemical characteristics of Picoxystrobin.

Characteristic Value Comments/Guidance

Pesticide Name Picoxystrobin Required input

Log KOW 3.6

Required input 

Enter value from acceptable or supplemental study 

submitted by registrant or available in scientific literature.

KOW 3981 No input necessary. This value is calculated automatically

from the Log KOW value entered above.

KOC (L/kg 

OC) 799

Required input

Input value used in PRZM/EXAMS to derive EECs. Follow 

input parameter guidance for deriving this parameter 

value (USEPA 2002).

Time to steady state 

(TS; days) 3 No input necessary. This value is calculated automatically from the Log KOW value entered above.

Pore water EEC 

(μg/L) 3.70

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 

based on the time it takes for the chemical to reach 

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. 

Water Column EEC 

(μg/L) 8.92

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 

appropriate averaging period of the EEC is dependent on 

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). 
187

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

rate constant. 

Trophic level

k1 

(L/kg*d)

k2 

(d-1)

kD 

(kg-food/kgorg/d)kE 

(d-1)

kM* 

(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.

Animal

Measure of 

effect (units) Value Species

If 

selected 

species 

is 

"other," 

enter 

body 

weight (in 

kg) here.

Avian LD50 (mg/kg-bw) 486 other 0.014

LC50 (mg/kgdiet) 5200 mallard duck

NOAEC (mg/kgdiet) 157 mallard duck

Mineau Scaling 

Factor 1.15

Default value for all species 

is 1.15 (for chemical specific 

values, see Mineau et al. 

1996).

Mammalian LD50 (mg/kg-bw) 5000 laboratory rat

LC50 (mg/kgdiet) N/A other

Chronic 

Endpoint 50

laboratory rat

units of chronic 

endpoint*

ppm

*ppm = mg/kg-diet
188

Table H4. Abiotic characteristics of the model aquatic ecosystem.

Characteristic Value Guidance*

Concentration of 

Particulate Organic 

Carbon 

(XPOC; kg OC/ L)

0.00E+00

When using EECs generated by PRZM/EXAMS, use a value of 

“0” for both POC and DOC. Concentration of 

Dissolved Organic 

Carbon 

(XDOC; kg OC/L)

0.00E+00

Concentration of 

Dissolved Oxygen 

(COX; mg O2/L)

5.0 Default value is 5.0 mg O2/L when using EECs generated by 

PRZM/EXAMS.

Water Temperature (T; 

o

C) 15

Value is defined by the average water temperature of the 

EXAMS pond when using EECs generated by PRZM/EXAMS. 

Model user should consult output file of EXAMS to define this 

value.

Concentration of 

Suspended Solids 

(CSS; kg/L)

3.00E-05 Default value is 3.00x10-5 kg/L when using EECs generated by 

PRZM/EXAMS.

Sediment Organic 

Carbon 

(OC; %)

4.0% Default value is 4.0% when using EECs generated by 

PRZM/EXAMS.

*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.

Trophic Level

Wet Weight 

(kg) % lipids % NLOM % Water

Do 

organisms 

in trophic 

level 

respire 

some pore 

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
189

*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: 

Trophic level in diet Zoo plankton

Benthic 

Invertebrates

Filter 

Feeder

Small 

Fish

Medium 

Fish

Large 

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.

Mammal/Bird # Name

Body 

weight 

(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
190

Table H8. Diets of mammals feeding on aquatic biota of the model ecosystem.

Trophic level in diet

Diet for: 

fog/water 

shrew

rice rat/starnosed molesmall 

mink

large 

mink

small river 

otter

large 

river 

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: 

Trophic level in diet sandpipers cranes rails herons

small 

osprey

white 

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.

Parameter

Phyto 

plankton

Zoo 

plankton

Benthic 

Invertebrates

Filter 

Feeders Small Fish

Medium 

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
191

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
192

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.

Ecosystem Component

Total 

concentratio

n (μg/kg-ww)

Lipid 

normalized 

concentratio

n (μg/kglipid)

Contributio

n due to 

diet (μg/kgww)

Contributio

n due to 

respiration 

(μg/kg-ww)
193

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.

Trophic Level

Total BCF 

(μg/kgww)/(μg/L)

Total BAF 

(μg/kgww)/(μg/L)

Phytoplankton 192 187

Zooplankton 137 137
194

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.

Trophic Level

BCF 

(μg/kglipid)/(μg/L)

BAF 

(μg/kglipid)/(μg/L)

BMF 

(μg/kglipid)/(μg/k

g-lipid)

BSAF 

(μg/kglipid)/(μg/k

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

Biological Parameters

EECs (pesticide 

intake)

Body

Weight

(kg)

Dry Food 

Ingestion 

Rate (kg-dry 

food/kgbw/day)

Wet Food 

Ingestion 

Rate (kg-wet 

food/kgbw/day)

Drinking 

Water

Intake

(L/d)

Dose 

Based 

(mg/kgbw/d)

Dietary 

Based 

(ppm)

Mammalian

fog/water shrew 0.02 0.140 0.585 0.003 0.761 1.30

rice rat/star-nosed 

mole 0.1 0.107 0.484 0.011 0.619 1.28

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
195

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.

Wildlife Species

Toxicity Values

Acute Chronic

Dose 

Based 

(mg/kgbw)

Dietary 

Based 

(mg/kg-diet)

Dose Based 

(mg/kg-bw)

Dietary 

Based 

(mg/kgdiet)

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.

Wildlife Species

Acute Chronic

Dose 

Based

Dietary 

Based

Dose Based Dietary 

Based
196

Mammalian

fog/water shrew 0.000 N/A 0.145 0.026

rice rat/star-nosed 

mole 0.000 N/A 0.174 0.026

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
197

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

Conclusion*

Drinking water exposure 

alone is NOT a potential

concern for mammals

Drinking water exposure 

alone is NOT a potential 

concern for mammals

Table 3. Avian Results

Parameter Acute Chronic

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

Conclusion*

Drinking water exposure 

alone is NOT a potential 

concern for birds

Drinking water exposure 

alone is NOT a potential 

concern for birds

*Conclusion is for drinking water exposure alone. This does not combine all routes of exposure. 

Therefore, when aggregated with other routes (i.e., diet, inhalation, dermal), pesticide exposure through 

drinking water may contribute to a total exposure that has potential for effects to non-target animals.
198

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
199

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, cornsweet for seed, sorghum for grain, sorghum for silage or greenchop, soybeans, wheat-all, beansdry 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), peasgreen 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
200

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
201

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 lataClarke

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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202

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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203

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

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204

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

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205

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

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206

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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207

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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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

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209

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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210

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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211

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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212

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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213

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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214

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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215

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

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216

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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217

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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218

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

12/21/2011 2:57:17 PM Ver. 2.2.0 Page 20 of 64
219

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

12/21/2011 2:57:17 PM Ver. 2.2.0 Page 21 of 64
220

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

12/21/2011 2:57:17 PM Ver. 2.2.0 Page 22 of 64
221

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, Tubercledblossom

McCreary Laurel Epioblasma torulosa torulosa

Monroe Logan Campbell

Pulaski McCreary Edmonson

Russell Pulaski Green

12/21/2011 2:57:17 PM Ver. 2.2.0 Page 23 of 64
222

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

12/21/2011 2:57:18 PM Ver. 2.2.0 Page 24 of 64
223

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
224

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

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225

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

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226

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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227

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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228

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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229

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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230

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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231

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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232

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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233

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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234

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
235

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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236

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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237

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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238

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
239

Monroe

Humacao Rio Grande

Montgomery

Isabela Salinas

Northampton

Juana Diaz Santa Isabel

Schuylkill

Lajas Vega Baja

York

Manati Yabucoa

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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
240

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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241

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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242

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, Greenblossom

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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243

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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244

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
245

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

12/21/2011 2:57:20 PM Ver. 2.2.0 Page 47 of 64
246

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

12/21/2011 2:57:20 PM Ver. 2.2.0 Page 48 of 64
247

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
248

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, Greenblossom

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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249

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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250

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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251

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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252

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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253

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

12/21/2011 2:57:21 PM Ver. 2.2.0 Page 55 of 64
254

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 mariannusMammal 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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255

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 SpeckledRhinichthys 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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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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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 PocketbookLampsilis 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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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 PocketbookPotamilus 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-blossomEpioblasma 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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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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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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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) tshawytschaSalmonidae 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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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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Appendix K. Transformation Products Formed in Environmental Fate Studies

Code Name/ 

Synonym Chemical Name Chemical Structure Study Type Maximum %AR (day)

Final 

%AR 

(study 

length)

PARENT

Picoxystrobin

ZA1963

IUPAC Methyl(E)-2-{2-[6-

(trifluoromethyl)pyridin-2-

yloxymethyl]phenyl}-3-

methoxyacrylate

CAS: Methyl(E)-α-

(methoxymethylene)-2-[[[6-

(trifluoromethyl)-2-

pyridinyl]oxy]methyl]benzeneace

tate (9Cl) 

CAS-no: 117428-22-5

Formula: C18H16F3NO4

MW: 367.32 g/mole

MAJOR (>10%) TRANSFORMATION PRODUCTS

ZA1963/02

Compound 2

IN-QDY62

R403092

(E)-2-{2-[6-

(trifluoromethyl)pyridin-2-

yloxymethyl]phenyl}-3-

methoxyacrylic acid

Aerobic soil Sandy loam 

(Hyde Farm)

Pyridinyl label 16.8 (50) 1.5 (364)

Phenylacrylate label 18.7 (29) 1.9 (364)

Sandy clay 

loam

Pyridinyl label 9.4 (9) 4.0 (119)

Phenylacrylate label 9.1 (9) 2.7 (119)

Sand Pyridinyl label 14.9 (50) 4.5 (119)

Phenylacrylate label 17.3 (29) 3.7 (119)

Sandy loam 

(Frensham)

Pyridinyl label 26.1 (50) 17.3 (119)

Phenylacrylate label 26.3 (29) 13.5 (119)

N

F

F

F

O

O

CH3

O

H3C

O

N

F

F

F

O

O

CH3

HO

O
264

Code Name/ 

Synonym Chemical Name Chemical Structure Study Type Maximum %AR (day)

Final 

%AR 

(study 

length)

Anaerobic soil Waiver requested

Aerobic 

aquatic 

Old 

Basing

Pyridinyl label Water 37.4 (120) 37.4 (120)

Sediment 29.8 (120) 29.8 (120)

System 67.2 (120) 67.2 (120)

Phenylacrylate 

label

Water 38.2 (120) 38.2 (120

Sediment 30.7 (120) 30.7 (120)

System 68.9 (120) 68.9 (120)

Virginia 

Water

Pyridinyl label Water 16.6 (83) 6.3 (120)

Sediment 6.7 (51) 1.1 (120)

System 22.5 (51) 7.4 (120)

Phenylacrylate 

label

Water 16.4 (83) 6.0 (120)

Sediment 7.6 (51) 1.0 (120)

System 20.6 (51) 7.0 (120)

Anaerobic aquatic Pyridinyl 

label

Water 40.0 (360) 40.0 (360)

Sediment 33.3 (360) 33.3 (360)

System 73.3 (360) 73.3 (360)

Phenylacrylat

e label

Water 37.0 (360) 37.0 (360)

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 

studies

Terrestrial MRID 48073841 0.038 ppm (46, 

60)

0.0047 

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, 

62)

<0.01 ppm 

(367)

Site 2 0.02 ppm (27, 

56, 98, 189, 

274, 367)

0.02 ppm 

(365)

MRID 48073847 0.03 ppm (364) 0.03 ppm 

(364)

MRID 48073848 0.02 ppm (96) <0.01 ppm 

(365)
265

Code Name/ 

Synonym Chemical Name Chemical Structure Study Type Maximum %AR (day)

Final 

%AR 

(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, 

96, 284)

<0.01 ppm 

(379)

Aquatic MRID 48073838 Not analyzed

ZA1963/03

Compound 3

IN-QDK50

R403814

6-(Trifluoromethyl)pyridin-2H-2-

one 

Aerobic soil Pyridinyl 

label

Sandy loam (Hyde 

Farm)

13.8 (50) 0.7 (364)

Sandy clay loam 13.7 (21) 3.9 (119)

Sand 9.4 (50) 5.8 (119)

Sandy loam 

(Frensham)

10.3 (50) 7.9 (119)

Anaerobic soil Waiver requested

Aerobic aquatic Pyridinyl 

label

Old 

Basing

Water 1.0 (83) 0.9 (120)

Sediment 1.1 (120) 1.1 (120)

System 2.0 (120) 2.0 (120)

Virginia 

water

Water 4.5 (120) 4.5 (120)

Sediment 1.5 (120) 1.5 (120)

System 6.0 (120) 6.0 (120)

Anaerobic aquatic Pyridinyl 

label

Water 0.8 (360) 0.8 (360)

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 

studies

Terrestrial MRID 48073841 0.051 ppm (29) 0.0045 

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, 

28)

<0.01 ppm 

(367)

Site 2 0.03 ppm (98) <0.01 ppm 

(365)

N O

F H

F

F
266

Code Name/ 

Synonym Chemical Name Chemical Structure Study Type Maximum %AR (day)

Final 

%AR 

(study 

length)

MRID 48073847 0.03 ppm (94) 0.02 ppm 

(364)

MRID 48073848 0.02 ppm (4, 

15, 28)

<0.01 ppm 

(365)

MRID 48073849 Site 1 0.02 ppm (14, 

28)

<0.01 ppm 

(365)

Site 2 0.02 ppm (13) <0.01 ppm 

(361)

MRID 48073850 0.02 ppm (7, 

14, 27)

<0.01 ppm 

(391)

MRID 48073851 0.05 ppm (7) <0.01 ppm 

(379)

Aquatic MRID 48073838 Not analyzed

ZA1963/04

Compound 4

Methyl (Z)-2-{2-[6-

(trifluoromethyl)pyridin-2-

yloxymethyl]phenyl}-3-

methoxyacrylate

Aerobic soil Not identified but not major

Anaerobic soil Waiver requested

Aerobic aquatic Not identified but not major

Anaerobic aquatic Not identified but not major

Hydrolysis Not identified but not major

Aqueous 

photolysis

Pyridinyl label 14.2 (3.7) 8.3 (17.9)

Phenylacrylate label 11.7 (3.7) 9.1(17.7)

Soil photolysis Pyridinyl label 2.5 (0.8) 1.1 (19.8)

Phenylacrylate label 3.8 (3.8) 2.2 (20.7)

Field studies Not analyzed

ZA1963/07

Compound 7

IN-QFA35

2-{2-[6-(trifluoromethyl)pyridin2-yloxymethyl]phenyl}acetic 

acid

Aerobic soil Bands corresponding to 

reference standards were 

observed on the TLC plates 

but insufficient material was 

available for a conclusive 

identification

Anaerobic soil Waiver requested

Aerobic aquatic Old Basing Pyridinyl 

label

Water 2.3 (30) 0.2 (120)

Sediment 1.4 (120) 1.4 (120)

System 1.6 (120) 1.6 (120)

Phenylacry

late label

Water 0.4 (83) 0.2 (120)

Sediment 2.9 (120) 2.9 (120)

System 3.1 (120) 3.1 (120)

Virginia water Pyridinyl 

label

Water 25.9 (120) 25.9 (120)

Sediment 12.8 (83) 12.4 (120)

N

F

F

F

O

O

H3C

O O

CH3

N

F

F

F

O

HO

O
267

Code Name/ 

Synonym Chemical Name Chemical Structure Study Type Maximum %AR (day)

Final 

%AR 

(study 

length)

System 38.3 (120) 38.3 (120)

Phenylacry

late label

Water 24.2 (120) 24.2 (120)

Sediment 14.2 (83) 12.2 (120)

System 36.4 (120) 36.4 (120)

Anaerobic 

aquatic

Pyridinyl label Water <0.05 (0-360)

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

Compound 12

Methyl 2-hydroxy-{2-[6-

(trifluoromethyl)pyridin-2-

yloxymethyl]phenyl}-acetate

Aerobic soil Not identified but not major

Anaerobic soil Waiver requested

Aerobic aquatic Not identified but not major

Anaerobic aquatic Not identified but not major

Hydrolysis Not identified but not major

Aqueous photolysis Pyridinyl label 15.3 (17.9) 15.3 (17.9)

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

N

F

F

F

O

O

H3C

O

OH
268

Code Name/ 

Synonym Chemical Name Chemical Structure Study Type Maximum %AR (day)

Final 

%AR 

(study 

length)

Carbon dioxide Carbon dioxide

Formula: CO2

Aerobic soil Sandy loam 

(Hyde Farm)

Pyridinyl label 33.9 (364) 33.9 (364)

Phenylacrylate label 59.9 (364) 59.9 (364)

Sandy clay 

loam

Pyridinyl label 32.5 (119) 32.5 (119)

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 

(Frensham)

Pyridinyl label 20.1 (119) 20.1 (119)

Phenylacrylate label 29.9 (119) 29.9 (119)

Anaerobic soil Waiver requested

Aerobic aquatic Old Basing Pyridinyl label 2.9 (120) 2.9 (120)

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

O C O
269

Minor Environmental Degradates of Picoxystrobin

Code Chemical name Chemical structure Study Type

Maximum 

%AR 

(day)

Final 

%AR 

(study 

length)

ZA1963/08

Compound 8

IN-QDY63

R408509

2-[6-(Trifluoromethyl)pyridin-2-

yloxymethyl]-benzoic acid

Aerobic soil Likely present at minor 

concentrations

Anaerobic soil Waiver requested

Aerobic 

aquatic

Old Basing Pyridinyl label Water 2.7 (120) 2.7 (120)

Sediment 0.6 (83) 0.2 (120)

System 2.9 (120) 2.9 (120)

Phenylacrylate 

label

Water 1.1 (83) 0.9 (120)

Sediment 0.8 (83) Not 

detected 

(120)

System 1.9 (83) 0.9 (120)

Virginia 

Water

Pyridinyl label Water 8.4 (120) 8.4 (120)

Sediment 2.7 (120) 2.7 (120)

System 11.1 (120) 11.1 (120)

Phenylacrylate 

label

Water 8.5 (120) 8.5 (120)

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 

label

Water <0.05 (0-360)

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)

N

F

F

F

O

O

OH
270

Code Chemical name Chemical structure Study Type

Maximum 

%AR 

(day)

Final 

%AR 

(study 

length)

MRID 48073844 0.138 ppm (43) na (372)

MRID 

48073846

Site 1 0.09 ppm (7, 

28)

<0.01 ppm 

(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, 

63)

<0.01 ppm 

(365)

MRID 

48073849

Site 1 0.03 ppm (6, 

14)

<0.01 ppm 

(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, 

56)

<0.01 ppm 

(379)

Aquatic MRID 48073838 Not analyzed

ZA1963/13

Compound 13

Methyl 2-oxo-{2-[6-

(trifluoromethyl)pyridin-2-

yloxymethyl]phenyl}-acetate

Aerobic soil Not identified

Anaerobic soil Waiver requested

Aerobic aquatic Not identified

Anaerobic aquatic Not identified

Hydrolysis Not identified

Aqueous photolysis Not identified

Soil photolysis Pyridinyl label 2.0 (0.8) 0.9 (19.8)

Phenylacrylate label 2.1 (0.7-3.8) 1.2 (20.7)

Field studies Not analyzed

ZA1963/15

Compound 15

Phthalic acid Aerobic soil Not identified

Anaerobic soil Waiver requested

Aerobic aquatic Not identified

Anaerobic aquatic Not identified

Hydrolysis Not identified

Aqueous photolysis Not identified

Soil photolysis Phenylacrylate label 5.8 (13.7) 5.2 (20.7)

Field studies Not analyzed

Compound 26 2-Methoxy-6-

(trifluoromethyl)pyridine

Aerobic soil Pyridinyl 

label

Sandy loam 

(Hyde Farm)

6.9 (364) 6.9 (364

N

F

F

F

O

O

H3C

O

O

O

OH

O

OH
271

Code Chemical name Chemical structure Study Type

Maximum 

%AR 

(day)

Final 

%AR 

(study 

length)

Sandy clay loam 8.2 (119) 8.2 (119)

Sand 8.2 (119) 8.2 (119)

Sandy loam 

(Frensham)

5.7 (119) 5.7 (119)

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

N O

F

F

F CH3