Ecological Risk Assessment for the Section 3 New Chemical 

Registration of Ametoctradin (BAS 650 F)

 

CAS: 865318-97-4

U.S. EPA PC Code: 119210

DP Barcode: 392115

Team Members

Anita Ullagaddi, Biologist

Faruque Khan, Senior Fate Scientist

Peer Reviewers

Michael Lowit, Ecologist

Stephen Wente, Biologist

ERB1 Branch Chief 

Nancy Andrews

Date of Approval

September 30, 2011
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TABLE OF CONTENTS

1 Executive Summary ...........................................................................................................................................4

1.1 Proposed Use Patterns...............................................................................................................................4

1.2 Potential Risks to Non-target Organisms...................................................................................................5

1.3 Conclusions: Exposure Characterization...................................................................................................6

1.4 Conclusions: Effects Characterization .......................................................................................................7

1.5 Data Gaps...................................................................................................................................................7

1.6 Significant Uncertainties............................................................................................................................7

2 Problem Formulation ........................................................................................................................................8

2.1 Nature of Regulatory Action.......................................................................................................................8

2.2 Mode of Action ...........................................................................................................................................9

2.3 Overview of Proposed Pesticide Use..........................................................................................................9

2.4 Receptors....................................................................................................................................................9

2.4.1 Aquatic and Terrestrial Effects...................................................................................................................9

2.4.2 Ecosystems Potentially at Risk ...................................................................................................................9

2.4.3 Ecological Effects.....................................................................................................................................10

2.5 Conceptual Model ....................................................................................................................................10

2.5.1 Risk Hypotheses........................................................................................................................................10

2.5.2 Conceptual Diagram ................................................................................................................................10

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

2.6.1 Measures of Effect and Exposure .............................................................................................................14

2.6.2 Data Gaps.................................................................................................................................................15

3 Exposure Analysis............................................................................................................................................16

3.1 Use Characterization................................................................................................................................16

3.2 Exposure Assessment................................................................................................................................16

3.2.1 Environmental Fate and Transport Characterization ..............................................................................16

3.2.2 Aquatic Exposure Estimates for Ametoctradin.........................................................................................22

3.2.3 Terrestrial Wildlife Exposures..................................................................................................................29

3.2.4 Terrestrial and Semi-Aquatic Plant Exposures........................................................................................31

4 Ecological Effects Analysis..............................................................................................................................32

4.1 Aquatic Effects Summary..........................................................................................................................32

4.2 Terrestrial Effects Summary.....................................................................................................................37

4.2.1 Toxic Effects on Birds...............................................................................................................................37

4.2.2 Toxic Effects on Mammals........................................................................................................................38

4.2.3 Toxic Effects on Invertebrates..................................................................................................................39

4.2.4 Toxic Effects on Plants.............................................................................................................................40
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5 Risk Characterization......................................................................................................................................40

5.1 Risk Estimation: Integration of Exposure and Effects Data .....................................................................41

5.1.1 Non-target Aquatic Fish, Invertebrates, and Plants.................................................................................41

5.1.2 Non-target Terrestrial Animals ................................................................................................................45

5.1.3 Terrestrial and Semi-aquatic Plants.........................................................................................................46

5.2 Risk Description .......................................................................................................................................47

5.2.1 Risks of Ametoctradin to Aquatic Organisms...........................................................................................47

5.2.2 Risks of Ametoctradin to Terrestrial Organisms......................................................................................49

5.3 Threatened and Endangered Species Concern.........................................................................................50

5.3.1 Action Area...............................................................................................................................................50

5.3.2 Taxonomic Groups Potentially at Risk: Direct Effects.............................................................................51

5.3.3 Use of Probit Slope Response Relationship to Provide Information on the Endangered Species Levels of 

Concern.........................................................................................................................................................52

5.3.4 Indirect Effects Analysis...........................................................................................................................52

6 Description of Assumptions and Limitations.................................................................................................52

6.1 Assumptions and Limitations Related to Exposure for all Taxa...............................................................52

6.2 Assumptions and Limitations Related to Exposure for Terrestrial Species..............................................53

6.3 Assumptions and Limitations Related to Exposure for Aquatic Species...................................................55

6.4 Assumptions and Limitations Related to Effects Assessment....................................................................55

7 Literature Cited................................................................................................................................................57

Appendix A. Environmental Fate Data ...................................................................................................................60

Appendix B. Aquatic Modeling ................................................................................................................................68

Appendix C. Example T-REX Output.....................................................................................................................79

Appendix D. TerrPlant Output ................................................................................................................................80

Appendix E. RQ Methods and LOC Definitions.....................................................................................................81

Appendix F. Toxicity Data for Terrestrial Invertebrates Other Than the Honey Bee........................................82

Appendix G. LOCATES Output..............................................................................................................................85
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1 Executive Summary

1.1 Proposed Use Patterns

BASF is seeking registration for ametoctradin, also known as BAS 650 F or Initium, which is a 

fungicide that is a strong inhibitor of mitochondrial respiration in complex III (cytochrome bc1) 

of Oomycetes fungi. It is classified as a Group C8 fungicide by the Fungicide Resistance Action 

Committee (FRAC), and the exact binding site is not yet known. Ametoctradin has been 

submitted to the U.S. Environmental Protection Agency (U.S. EPA or the Agency) for 

registration under a global joint review agreement. Participating countries include Canada 

(PMRA), Australia (APVMA), and New Zealand (EPA/ERMA). 

Ametoctradin, formulated into the products BAS 650 00 F, Zampro, and Orvego, is proposed for 

use on Brassica leafy vegetables, bulb vegetables, cucurbit vegetables, fruiting vegetables, 

grapes, hops, leafy vegetables, tuberous and corm vegetables, ornamentals, and golf courses. 

BAS 650 00 F contains ametoctradin only (19.2% a.i.), while Zampro and Orvego contain 

ametoctradin (26.9% a.i.) and dimethomorph (20.2% a.i.). Zampro and Orvego are referred to as 

BAS 651 00 F throughout this assessment. Table 1.1 contains maximum proposed application 

rates, which were assessed in this document. It is important to note that for all crops (excluding 

ornamentals and golf courses), only two sequential applications are allowed; a fungicide with a 

different mode of action should be used in between the second and third applications for 

resistance management purposes. Because the label did not specify whether the use of a different 

fungicide increases the interval between the second and third applications, the Environmental 

Fate and Effects Division (EFED) conservatively assumed that the interval did not increase. 

Table 1.1. Maximum Application Rates from the Proposed Ametoctradin Labels

Product Use Application Method

Application Rate

(Interval between 

Applications)*

Maximum 

Application Rate/ 

Year

BAS 650 00 F

(ametoctradin only; 

19.2%) 

Zampro^

(ametoctradin; 26.9% & 

dimethomorph; 20.2%)

Brassica leafy

vegetables

Ground sprayer

Aerial equipment

Sprinkler/drip irrigation

3 apps @ 0.274 lb a.i./acre

(7 days) 0.822 lb a.i./acre

Bulb vegetables

Cucurbit 

vegetables

Fruiting vegetables

Leafy vegetables

Tuberous and corm 

vegetables

Ground sprayer

Aerial equipment

Sprinkler/drip irrigation

3 apps @ 0.274 lb a.i./acre

(5 days) 0.822 lb a.i./acre

Grapes

Ground sprayer

Aerial equipment

Sprinkler/drip irrigation

4 apps @ 0.274 lb a.i./acre

(7 days) 1.096 lb a.i./acre

Hops

Ground sprayer

Aerial equipment

Sprinkler/drip irrigation

3 apps @ 0.274 lb a.i./acre

(10 days) 0.822 lb a.i./acre
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Table 1.1. Maximum Application Rates from the Proposed Ametoctradin Labels

Product Use Application Method

Application Rate

(Interval between 

Applications)*

Maximum 

Application Rate/ 

Year

Orvego^

(ametoctradin; 26.9% & 

dimethomorph; 20.2%)

Field- and 

container-grown 

woody and 

herbaceous 

ornamentals

Golf courses

Residential and 

commercial 

landscapes

Greenhouses

Foliar spray

Soil surface spray or 

drench

Chemigation

4 apps @ 0.274 lb a.i./acre**

(10 days) 1.096 lb a.i./acre**

*Only 2 sequential applications allowed. A fungicide with a different mode of action must be used between the second and third 

applications. Due to the absence of label statements, EFED conservatively concludes that the application interval between the 

second and third application does not increase. 

**The label states that the single application rate is 0.468 lb a.i.; EFED assumed this was total a.i. for both ametoctradin and 

dimethomorph based on information on the first page of the label.

^Zampro and Orvego are referred to as BAS 651 00 F throught this assessment.

1.2 Potential Risks to Non-target Organisms

A screening-level risk assessment suggests that ametoctradin presents potential risks to listed 

non-vascular aquatic plants and to organisms that depend on these plants for habitat and forage

as a result of some of the proposed uses (bulb vegetables, cucurbit vegetables, fruiting 

vegetables, tuberous and corm vegetables, and grapes). However, it should be noted that there 

are currently no non-vascular aquatic plants identified as endangered or threatened, but species

may be identified in the future.

Listed Species

Based on available screening level information, for some of the proposed uses of ametoctradin

(bulb vegetables, cucurbit vegetables, fruiting vegetables, tuberous and corm vegetables, and 

grapes), there is a potential for direct effects to listed non-vascular aquatic plants. In conducting 

a screen for indirect effects, direct effect levels of concern (LOCs; see Appendix E) for each 

taxonomic group are used to make inferences concerning the potential for indirect effects upon 

listed species that rely upon non-endangered organisms in these taxonomic groups as resources 

critical to their life cycle. However, because non-vascular aquatic plants may be directly affected

only at a level of concern for listed species, indirect effects to other listed taxa should be 

identified only if there is a one to one obligate relationship between the listed species in another 

taxa and a species of non-vascular plant on which it directly relies. Because no listed nonvascular aquatic plants have been identified and it is impossible to then predict the species that 

may be indirectly affected, the indirect effects identified in this assessment are very conservative; 

it is highly unlikely that all species in all taxa identified for indirect effects will actually be 

affected. A summary of the risk conclusions and direct and indirect effects determinations is 

presented in Table 1.2.
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Table 1.2. Potential Listed Species Risks Associated with Direct or Indirect Effects 

Due to the Proposed Applications of Ametoctradin

Listed Taxonomy Direct Effects Indirect Effects

Terrestrial and semi-aquatic plants –

monocots No No

Terrestrial and semi-aquatic plants – dicots No No

Terrestrial invertebrates No No

Birds (surrogate for terrestrial-phase 

amphibians and reptiles) No No

Mammals No No

Aquatic vascular plants No Yes*

Aquatic non-vascular plants Yes+ Yes*

Freshwater fish (surrogate for aquaticphase amphibians) No Yes*

Freshwater Invertebrates No Yes*

Freshwater Benthic Invertebrates Acute – No^

Chronic – No Yes*

Estuarine/Marine Benthic Invertebrates Acute – No

Chronic – No^ Yes*

Estuarine/Marine Fish Acute – No

Chronic – No^ Yes*

Estuarine/Marine Crustaceans Acute – No

Chronic – No^ Yes*

Estuarine/Marine Mollusks No Yes*

+No aquatic non-vascular plants have been designated as endangered or threatened; however, the potential 

for risk to these organisms exists.

*For indirect effects, all aquatic taxa have been identified due to the potential direct effects on listed nonvascular aquatic plants. However, any species identified for potential indirect effects would require an 

obligate relationship with the directly affected listed non-vascular aquatic plant. Because there are no listed 

non-vascular aquatic plants, the taxa identified for indirect effects are very conservative assumptions.

^While data were not submitted, a weight of evidence approach was used to discount potential risks to these 

taxa. 

Incidents

No incidents have been reported, which is to be expected as ametoctradin is a new chemical.

1.3 Conclusions: Exposure Characterization

Ametoctradin is a non-volatile (vapor pressure of 4.5 x 10-12 mm Hg at 25°C) compound and 

sparingly soluble (0.15 mg/L at 20°C) in water. Its major routes of degradation are aerobic 

biodegradation in terrestrial environments and aerobic and anaerobic biodegradation in aquatic 

environments. The parent compound is expected to degrade with a half-life of less than 1 to 4

weeks in aerobic environments and anaerobic water bodies and a half-life of several months in 

anaerobic soils. The transformation of ametoctradin is governed by microbial decomposition in 

soil and water, proceeding primarily via oxidative cleavage of the n-octyl side chain, forming 

major transformation products with successively shorter octyl side chains: M650F01, M650F02, 

M650F03, and M650F04; and CO2. Ametoctradin tends to adsorb strongly to soil and sediment 

(KFOC = 1580-6620 L/Kg) and is expected to be slightly mobile to hardly mobile according to 

FAO mobility classifications (FAO, 2000). Exposure of ametoctradin in the environment is 
7

expected to occur predominantly via spray drift and runoff of dissolved degradates and parent 

residues sorbed to suspended sediment.

1.4 Conclusions: Effects Characterization

The acute and chronic toxicity of ametoctradin was determined for a variety of aquatic algal, 

invertebrate and fish species. Acute and/or chronic toxicity studies were also conducted on 

selected species with the end-use products BAS 650 00 F (ametoctradin only; 19.2%) and BAS 

651 00 F (ametoctradin; ~27% & dimethomorph; ~20%), as well as the transformation products 

M650F01, M650F02, M650F03, and M650F04. With the exception of the aquatic plant and 

chronic freshwater fish and invertebrate studies where significant effects were observed, the 

studies did not produce definitive endpoints (i.e., EC50/LC50s were greater than the highest 

concentration tested). 

Seventeen studies were submitted that evaluated the effects of ametoctradin to terrestrial nontarget organisms. In general, ametoctradin was practically non-toxic to birds, mammals, 

invertebrates, and plants, and chronic effects were not observed.

1.5 Data Gaps

No environmental fate data gaps were identified. However, a key requirement of taxonomic soil 

classification based on Soil Taxonomy or World Reference Base for Soil Resources was not 

provided for the soils used in various environmental fate studies and is considered as a 

deficiency.

Chronic estuarine/marine invertebrate and fish studies were identified as data gaps prior to 

beginning this ecological risk assessment. However, BASF submitted a waiver request. Because 

differential acute toxicity between media types was not evident in the acute mysid shrimp and 

sheepshead minnow studies and the observed effects in the chronic freshwater studies did not 

cause RQs to exceed LOCs, EFED concurs that the studies may be waived for the currently 

proposed uses (DP 383243; September 30, 2011). Chronic risks to estuarine/marine fish and 

invertebrates are unlikely, and the submission of additional data is unlikely to change the risk 

conclusion. 

A 10-day estuarine/marine sediment toxicity study was submitted, along with a chronic 

freshwater sediment toxicity study. Both studies tested a formulated product rather than the 

technical grade active ingredient, as required by 40 CFR Part 158 data requirements. However, 

additional studies utilizing the TGAI, as well as a 10-day freshwater study and a chronic 

estuarine/marine study, are unlikely to add value to the ecological risk assessment or change risk 

conclusions (see Section 5.2.1). 

1.6 Significant Uncertainties

Although no acute oral or contact toxicity was observed in the honey bee studies, there is 

uncertainty as to how fungicides interact with insecticides and whether fungicides may disrupt 

the process of fermentation of pollen stores, which may have significant effects on honey bee 

nutrition and health (Alarcon et al., 2009). While EFED does not have a quantitative method for 
8

assessing potential risk of this nature, additional studies evaluating the effects of ametoctradin on 

honey bee health may be of value. Considering this and the toxicity data for the predatory wasp 

(see Section 5.2.2), an appropriate exposure reduction strategy may be to restrict applications of 

ametoctradin during bloom. 

Aquatic organisms were not tested up to 100 mg/L (see OCSPP 850.1000 guideline for details) 

due to the low solubility of ametoctradin (0.150 mg/L). Therefore, aquatic organisms were tested 

at concentrations up to the functional solubility of the chemical in laboratory test media. 

Attempts were made to create saturated solutions through the use of glass wool and saturator 

columns. For aquatic plants, suspensions were centrifuged prior to test initiation. Test solutions 

were visually confirmed to be clear and free of precipitate during the studies, and concentrations 

were generally maintained throughout the studies, as evidenced by high recovery rates. However, 

the uncertainty that the functional solubility of the chemical may increase in certain 

environmental conditions (e.g., tank mixture) remains and, if this is the case, could potentially 

result in risk to aquatic organisms not predicted in this assessment. The likelihood of the 

assessment underestimating risks to aquatic organisms is low because RQs were not close to 

LOCs and the high Kfoc for ametoctradin suggests that it is not likely to remain dissolved in 

water for a long period of time.

2 Problem Formulation

2.1 Nature of Regulatory Action

The purpose of this assessment is to evaluate the environmental fate and ecological risks for the 

registration of the new chemical ametoctradin. U.S. EPA is required under the Federal 

Insecticide Fungicide and Rodenticide Act (FIFRA) to ensure that ametoctradin does not have 

the potential to cause unreasonable adverse effects to the environment based on its proposed uses

(see Table 1.1). Potential effects to listed species (i.e., species on the Federal list of endangered 

and threatened wildlife and plants) are also considered under the Endangered Species Act in 

order to ensure that the registration of ametoctradin is not likely to jeopardize the continued 

existence of such listed species or adversely modify their habitat. To these ends, this assessment 

follows U.S. EPA guidance on conducting ecological risk assessments (U.S. EPA, 1998) and the 

Office of Pesticide Program’s policies for assessing risk to non-target and listed organisms (U.S. 

EPA, 2004).

Among the end products of the U.S. EPA pesticide registration process is a determination of 

whether a product is eligible for registration and, if so, an enforceable description of how the 

product may be used. A label represents the legal document, which stipulates how and where a 

given pesticide may be used. End-use labels describe the formulation type, acceptable methods 

of application, where the product may be applied, and any restrictions on how applications may 

be conducted. Thus, the use, or potential use, described by the pesticide’s labels is considered 

“the action” being assessed. 
9

2.2 Mode of Action

Ametoctradin belongs to the C8 class of fungicides (FRAC code 451

2.3 Overview of Proposed Pesticide Use

), but the binding site is 

unknown. Ametoctradin is a strong inhibitor of mitochondrial respiration in complex III 

(cytochrome bc1) of Oomycetes fungi.

Ametoctradin has been proposed for use on vegetables, grapes, hops, ornamentals, and golf 

courses (see Table 1.1) to control downy mildew, Phytophthora blight or crown rot, and late 

blight. The proposed use areas are found throughout the United States and cannot be limited to a 

geographic region. Because ametoctradin is a new chemical, usage data do not yet exist. 

2.4 Receptors

2.4.1 Aquatic and Terrestrial Effects

The receptor is the biological entity that is exposed to the stressor (U.S. EPA, 1998). Consistent 

with the process described in the Overview Document (U.S. EPA, 2004), this risk assessment 

uses a surrogate species approach in its evaluation of ametoctradin. Toxicological data generated 

from 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 taxonomic groupings. 

Acute and chronic toxicity data from studies submitted by pesticide registrants along with any

available open literature are used to evaluate the potential direct effects of ametoctradin to the 

aquatic and terrestrial receptors identified in this section. This includes toxicity data on the 

technical grade active ingredient, degradates, and when available, formulated products (e.g.,

“Six-Pack” studies). The open literature studies are identified through U.S. EPA’s publicly 

available ECOTOX database (http://cfpub.epa.gov/ecotox/), which employs a literature search 

engine for locating chemical toxicity data for aquatic life, terrestrial plants, and wildlife. The 

evaluation of both sources of data can also provide insight into the direct and indirect effects of 

ametoctradin on biotic communities from loss of species that are sensitive to the chemical and 

from changes in structure and functional characteristics of the affected communities. 

2.4.2 Ecosystems Potentially at Risk

The ecosystems at risk are often extensive in scope; as a result, it may not be possible to identify 

specific ecosystems during the development of a baseline risk assessment. However, in general 

terms, terrestrial ecosystems potentially at risk 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 include water bodies adjacent to or downstream from the 

treated field and might include impounded bodies such as ponds, lakes and reservoirs, or flowing 

 1 http://www.frac.info/frac/publication/anhang/FRAC%20Code%20List%202011-final.pdf
10

waterways such as streams or rivers. For uses in coastal areas, aquatic habitat also includes 

marine ecosystems, including estuaries. 

2.4.3 Ecological Effects

Each assessment endpoint requires one or more “measures of ecological effect,” which are 

defined as changes in the attributes of an assessment endpoint itself or changes in a surrogate 

entity or attribute in response to exposure to a pesticide. Ecological measurement endpoints for 

this risk assessment would be based on toxicity information for ametoctradin in the publicly 

available ECOTOX database (if available) and a suite of registrant-submitted toxicity studies 

performed on a limited number of organisms in the following broad groupings:

1. Birds (mallard duck or bobwhite quail and a passerine species), also used as a surrogate 

for terrestrial-phase amphibians and reptiles

2. Mammals (laboratory rat)

3. Freshwater fish (rainbow trout and bluegill sunfish), also used as a surrogate for aquaticphase amphibians

4. Freshwater invertebrates (daphnid)

5. Estuarine/marine fish (sheepshead minnow)

6. Estuarine/marine invertebrates (Eastern oyster, mysid shrimp)

7. Terrestrial plants (monocots and dicots)

8. Aquatic plants (vascular and non-vascular plants)

9. Terrestrial invertebrates (honey bee)

Within each of these very broad taxonomic groups, an acute and chronic endpoint is selected 

from the available test data, as the data allow. 

2.5 Conceptual Model 

A conceptual model provides a written description and visual representation of the predicted 

relationships between ametoctradin, potential routes of exposure, and the predicted effects for the 

assessment endpoint. A conceptual model consists of two major components: risk hypotheses 

and a conceptual diagram (U.S. EPA, 1998).

2.5.1 Risk Hypotheses

• Terrestrial and aquatic organisms are subject to adverse direct effects such as reduced 

survival, growth, and fecundity or indirect effects such as habitat, food web dynamics, 

perturbing forage or prey availability, and altering the extent and nature of nesting when 

exposed to ametoctradin residues as a result of labeled use of the pesticide.

• Terrestrial, semi-aquatic, and aquatic plants are subject to adverse effects such as reductions 

in vegetative vigor and seedling emergence (terrestrial) or biomass and growth rate (aquatic) 

when exposed to ametoctradin residues as a result of labeled use of the pesticide.

2.5.2 Conceptual Diagram

In order for a chemical to pose an ecological risk, it must reach ecological receptors in 

biologically significant concentrations. An exposure pathway is the means by which a 
11

contaminant moves in the environment from a source to an ecological receptor. For an ecological 

exposure pathway to be complete, it must have a source, a release mechanism, an environmental 

transport medium, a point of exposure for ecological receptors, and a feasible route of exposure. 

In addition, the potential mechanisms of transformation (i.e., which degradates may form in the 

environment, in which media, and how much) must be known, especially for a chemical whose 

metabolites/degradates are of greater toxicological concern. The assessment of ecological 

exposure pathways, therefore, includes an examination of the source and potential migration 

pathways for constituents, and the determination of potential exposure routes (e.g., ingestion, 

inhalation, and dermal absorption).

Figure 2.1. Conceptual Model for Exposure and Effects of Ametoctradin to Aquatic 

Organisms. Dotted Lines Indicate Exposure Pathways that Have a Low Likelihood of 

Contributing to Ecological Risk.

** Route of exposure includes only ingestion of fish and aquatic

Stressor

Source

Receptors

Attribute

Change

Ametoctradin and its degradates applied to proposed use sites

Spray drift

Aquatic animals

Invertebrates 

Vertebrates

**Piscivorous mammals 

 and birds 

Individual 

organisms

Reduced survival

Reduced growth

Reduced reproduction

Food chain

Reduction in algae and 

 vascular plants

Reduction in prey

Modification of PCEs 

 related to prey availability

Habitat integrity

Reduction in primary 

productivity

Reduced cover

Community change

Modification of PCEs related to 

 habitat

Surface water/

Sediment

Runoff

Aquatic Animals

Invertebrates

Vertebrates

Exposure

Media

Uptake/gills 

or integument

Ingestion Ingestion

Atmospheric 

transport

Wet/dry deposition

Soil Leaching to

Groundwater

Uptake/gills 

or integument

Aquatic Plants

Non-vascular

Vascular

Uptake/cell, 

roots, leaves Riparian plants

terrestrial 

exposure 

pathways see 

Figure 2.2
12

Figure 2.2. Conceptual Model for Exposure and Effects of Ametoctradin to Terrestrial 

Organisms. Dotted Lines Indicate Exposure Pathways that Have a Low Likelihood of 

Contributing to Ecological Risk.

Stressor

Source

Attribute

Change

Ametoctradin and its degradates applied to proposed use sites

Direct

application Spray drift

Terrestrial 

vertebrates*

Terrestrial 

Inverts*

Individual 

organisms

Reduced survival

Reduced growth

Food chain

Reduction in prey and food

Modification of PCEs 

 related to prey availability

Habitat integrity

Reduction in primary productivity

Reduced cover

Community change

Modification of PCEs related

 to habitat

Terrestrial plants

grasses/forbs, fruit, seeds 

(trees, shrubs)

Runoff

Terrestrial 

vertebrates* 

Exposure Media 

& Receptors Soil

Ingestion

Ingestion

Dermal uptake/Ingestion

Atmospheric 

transport

Root uptake/contact

Wet/dry deposition

Ingestion

Leaching to

Groundwater Irrigation 

water

* See Figure 6.3 for drinking water and inhalation exposure pathways for terrestrial vertebrates and 

ingestion of residues in dew by terrestrial invertebrates. 
13

Figure 2.3. Conceptual Model for Drinking Water and Inhalation Exposure Pathways for 

Terrestrial Vertebrates and Ingestion of Residues in Dew by Terrestrial Invertebrates. 

Dotted Lines Indicate Exposure Pathways that Have a Low Likelihood of Contributing to 

Ecological Risk. 

Based on the labels submitted by the registrant, the source and mechanisms of release for 

ametoctradin are aerial and/or ground application in the form of suspension concentrates. The 

conceptual model and subsequent analysis of exposure and effects are based on the parent

ametoctradin. Potential emission of volatile compounds is not considered to be a viable release 

mechanism for ametoctradin, because Henry’s Law constant (3.10 x 10-9 atm•m3

•mol-1) suggests 

that volatilization is not expected to be a significant route of dissipation for this chemical 

(indicated by dashed lines in the diagram). Concentrations of ametoctradin, sorbed to soil, in 

surface waters may be relatively high when significant runoff events occur after application 

and/or spray drift to water bodies in close proximity to the treatment area occurs. Ametoctradin

is not likely to leach to ground water; however, the degradates have the potential to reach ground 

water. The conceptual models shown in Figures 2.1, 2.2, and 2.3 generically depict the potential 

source of ametoctradin, release mechanisms, abiotic receiving media, and biological receptor 

types.

Stressor

Source

Attribute

Change

Ametoctradin and its degradates applied to proposed use sites

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
14

2.6 Analysis Plan

This assessment characterizes the environmental fate and effects of ametoctradin and determines 

whether there is potential for risks to non-target organisms based on the proposed use patterns. 

Available environmental fate, ecotoxicity, and physicochemical property data were taken from 

studies submitted to the Agency. The environmental fate and effects studies underwent reviews 

to determine their acceptability relative to published U.S. EPA guidelines. 

The maximum proposed label application rates for the use of ametoctradin on crops, 

ornamentals, and golf courses were selected for modeling environmental concentrations for this 

base-level deterministic (risk quotient-based) assessment. The most sensitive toxicity endpoints 

from surrogate test species are used to estimate treatment-related effects on survival, growth, and 

reproduction. Estimated environmental concentrations (EECs) used in terrestrial and aquatic 

ecological risk assessments are based on the parent ametoctradin compound. For terrestrial 

organisms, the Residues of Concern Knowledgebase Subcommittee (ROCKS) of the Health 

Effects Division (US EPA, 2011) determined that none of the degradates were of concern for 

mammals; therefore, EFED did not assess potential risk for mammals or birds due to exposure to 

the degradates. For aquatic organisms, submitted degradate data showed similar or less toxicity; 

therefore, EFED did not assess potential risks for aquatic organisms due to exposure to the 

degradates. For the aquatic assessment, EECs are initially produced by GENEEC. If LOC 

exceedances occur when comparing EECs to the toxicity values, PRZM/EXAMS would then be 

used to refine exposure estimates. For the terrestrial assessment, EECs are produced by T-REX 

and TerrPlant. The Screening Imbibition Program (SIP v.1.0) provides an upper-bound estimate 

of exposure of birds and mammals to pesticides through drinking water alone. Due to the low 

solubility of ametoctradin, it was not necessary to use SIP. The Screening Tool for Inhalation 

Risk (STIR v.1.0) assesses the potential for risk to birds and mammals through inhalation 

exposure. Due to the low volatility of ametoctradin, it was not necessary to use STIR.

The following sections characterize the use, environmental fate, and ecological effects of 

ametoctradin and use the risk quotient approach (ratio of EEC to toxicity value) to estimate the 

potential for adverse effects on non-target terrestrial and aquatic organisms. This risk quotientbased 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 base-level assessment.

In the event that endpoints from submitted ecotoxicity studies are non-definitive, the Guidance 

for Using Non-Definitive Endpoints in Evaluating Risks to Listed and Non-listed Animal 

Species memo will be consulted (U.S. EPA, 2011). 

2.6.1 Measures of Effect and Exposure

Table 2.2 lists the measures of environmental exposure and ecological effects used to assess the 

potential risks of ametoctradin to non-target organisms (U.S. EPA, 2004).
15

Table 2.2. Measures of Environmental Exposure and Ecological Effects Used to Assess the 

Potential Risks of Ametoctradin to Non-target Organisms

Assessment Endpoint Measures of Effect Measures of Exposure

Abundance (i.e., survival, 

reproduction, and growth) of 

individuals and populations of birds 

Bobwhite quail or mallard duck and 

passerine species acute oral LD50

Bobwhite quail and mallard duck sub-acute 

dietary LC50

Bobwhite quail and mallard duck chronic 

reproduction NOAEC and LOAEC 

Maximum residues on food 

items (foliar)

Abundance (i.e., survival, 

reproduction, and growth) of 

individuals and populations of 

mammals 

Laboratory rat acute oral LD50

Laboratory rat 2-generation NOAEC and 

LOAEC

Abundance (i.e., survival, 

reproduction, and growth) of 

individuals and communities of 

freshwater fish

Rainbow trout and bluegill sunfish LC50

Peak EEC

Rainbow trout and/or bluegill sunfish 

NOAEC and LOAEC

60-day average EEC

Abundance (i.e., survival, 

reproduction, and growth) of 

individuals and communities of 

freshwater invertebrates

Daphnid EC50 Peak EEC

Daphnid life cycle NOAEC and LOAEC

21-day average EEC

Abundance (i.e., survival, 

reproduction, and growth) of 

individuals and communities of 

estuarine/marine fish and 

invertebrates 

Sheepshead minnow acute LC50

Eastern oyster EC50

Mysid shrimp LC50

Peak EEC

Sheepshead minnow NOAEC and LOAEC

Mysid shrimp NOAEC and LOAEC

60-day average EEC

21-day average EEC

Survival of beneficial insect 

populations

Honeybee acute contact LD50 Not Applicable*

Maintenance and growth of 

individuals and populations of 

terrestrial plants from standing crop 

or biomass

Monocot EC25 and NOAEC values for 

seedling emergence and vegetative vigor 

(survival and growth rate) 

Dicot EC25 and NOAEC values for seedling 

emergence and vegetative vigor (survival and 

growth rate) 

Estimates of runoff and spray 

drift to non-target areas

Maintenance and growth of 

individuals and populations of aquatic 

plants from standing crop or biomass

Vascular plant (i.e., Lemna) EC50 and 

NOAEC values for growth rate and biomass 

measurements

Non-vascular plant (i.e., green algae) EC50

and NOAEC values for growth rate and 

biomass measurements 

Peak EEC

*EFED does not currently have a method for quantitatively assessing exposure and risk to non-target terrestrial 

invertebrates. 

 

2.6.2 Data Gaps

No environmental fate data gaps were identified. However, a key requirement of taxonomic soil 

classification based on Soil Taxonomy or World Reference Base for Soil Resources was not 
16

provided for the soils used in various environmental fate studies and is considered as a 

deficiency.

Chronic estuarine/marine invertebrate and fish studies were identified as data gaps prior to 

beginning this ecological risk assessment. However, BASF submitted a waiver request. Because 

differential acute toxicity between media types was not evident in the acute mysid shrimp and 

sheepshead minnow studies and the observed effects in the chronic freshwater studies did not 

cause RQs to exceed LOCs, EFED concurs that the studies may be waived for the currently 

proposed uses (DP 383243; September 30, 2011). Chronic risks to estuarine/marine fish and 

invertebrates are unlikely, and the submission of additional data is unlikely to change the risk 

conclusion. 

A 10-day estuarine/marine sediment toxicity study was submitted, along with a chronic 

freshwater sediment toxicity study. Both studies tested a formulated product rather than the 

technical grade active ingredient, as required by 40 CFR Part 158 data requirements. However, 

additional studies utilizing the TGAI, as well as a 10-day freshwater study and a chronic 

estuarine/marine study, are unlikely to add value to the ecological risk assessment or change risk 

conclusions (see Section 5.2.1). 

3 Exposure Analysis

3.1 Use Characterization

Ametoctradin, formulated into the products BAS 650 00 F, Zampro, and Orvego, is proposed for 

use on vegetables, grapes, hops, ornamentals, and golf courses. BAS 650 00 F contains 

ametoctradin only (19.2% a.i.), while Zampro and Orvego contain ametoctradin (26.9% a.i.) and 

dimethomorph (20.2% a.i.)2

. Table 1.1 contains maximum proposed application rates, which 

were assessed in this document. It is important to note that for all crops (excluding ornamentals 

and golf courses), only two sequential applications are allowed; a fungicide with a different 

mode of action should be used in between the second and third applications for resistance 

management purposes. Because the label did not specify whether the use of a different fungicide 

increases the interval between the second and third applications, EFED conservatively assumed 

that the interval did not increase. 

3.2 Exposure Assessment

3.2.1 Environmental Fate and Transport Characterization

Submitted environmental fate and transport data was jointly reviewed by all participating 

countries. DERs were compiled in the form of a monograph (DP393440).

Ametoctradin is a non-volatile (vapor pressure of 4.5 x 10-12 mm Hg at 25°C) compound and 

sparingly soluble (0.15 mg/L at 20°C) in water. Its major routes of degradation are aerobic 

biodegradation in terrestrial environments and aerobic and anaerobic biodegradation in aquatic 

environments. The parent compound is expected to degrade with a half-life of less than 1 to 4

 2

Zampro and Orvego are referred to as BAS 651 00F in the ecotoxicity section.
17

weeks in aerobic environments and anaerobic water bodies and a half-life of several months in 

anaerobic soils. The transformation of ametoctradin is governed by microbial decomposition in 

soil and water, proceeding primarily via oxidative cleavage of the n-octyl side chain, forming 

major transformation products with successively shorter octyl side chains: M650F01, M650F02, 

M650F03 and M650F04; and CO2. Table A-1 in Appendix A provides structures and physicochemical properties of major and minor degradates. With sufficient microbial exposure, the 

pyrimidine-carboxylic acid ring structure may be broken, leading to mineralization to CO2 and 

formation of non-extractable residues. Non-extractable residues made up a significant amount of 

recovered radioactive material, with maximum levels ranging from 23.8 to 51.4% in various fate 

studies. Ametoctradin tends to adsorb strongly to soil and sediment (KFOC = 1580-6620 L/kg) 

and is expected to be slightly mobile to hardly mobile according to FAO mobility classifications 

(FAO, 2000). Therefore, transport of ametoctradin in the environment is expected to occur 

predominantly via spray drift and runoff of dissolved degradates and parent residues sorbed to 

suspended sediment. Terrestrial field dissipation studies confirmed that ametoctradin’s mobility 

was limited to surface horizons at all sites. 

Degradation/Dissipation in Aquatic and Terrestrial Environments

Table 3.1 summarizes the registrant-submitted environmental fate and transport properties of 

ametoctradin. The hydrolysis of ametoctradin was stable in buffered aqueous solutions at pH 4, 

5, 7, and 9 at 50°C. Under photolytic conditions at pH 7, degradation slowly occurred (DT50 = 

76.8 days), but no significant metabolites were found. However, low amounts of oxidation 

products (hydroxylation and keto-formation at the octyl side-chain) were detected. The photodegradation of a major degradate, M650F03, was also determined in sterile buffered water and 

natural water. The estimated environmental DT50 ranges between 11.6 and 35.6 days. 

Table 3.1. Physical Chemical and Environmental Fate and Chemistry Properties of 

Ametoctradin

Parameter Value Reference/Comments

Selected Physical/Chemical Parameters

PC code 119210

MRID 4770009

Cas No. 865318-97-4

Chemical name [1,2,4]triazolo-[1,5-a]pyrimidin-7-amine, 5-ethyl-6-

octyl]

Structure

Molecular formula C15H25N5

Molecular weight 275.4 g/mol

Relative Density 1.12 g/cm3 MRID 4770009

Water solubility 

(20°C)

 Deionized water

 pH 4 (Buffer)

0.14 mg/L 

0.23 mg/L

MRID 47700012
18

Table 3.1. Physical Chemical and Environmental Fate and Chemistry Properties of 

Ametoctradin

Parameter Value Reference/Comments

 pH 7 (Buffer)

 pH 9 (Buffer)

0.15 mg/L

0.20 mg/L

Vapor Pressure 1.58 x 10-12 mm Hg (20°C) 

4.50 x 10-12 mm Hg (25°C) MRID 4770009

Henry’s law 

constant 3.10 x 10-9 atm•m3

•mol-1 (25°C) MRID 47700010

logKOW

 pH 4 (Buffer)

 pH 7 (Buffer)

 pH 9 (Buffer)

4.24

4.40 

4.18

MRID 47700014

Persistence

Hydrolysis Stable (pH = 4,5,7,9 at 50°C) MRID 47700015

Photolysis 

Matrix Kinetic 

Modela

DT50

(days)

DT90

(days)

Water

@ pH 7.0 SFOb 76.8 255.2 MRID 47700016

Soil

Bruch West SFO Stable MRID 47700120

Aerobic Soil 

Metabolism

Idaho Soil SFO

DFOP

IORE

12.3

9.64

11.4

40.9

192

139

MRID 47700118

Illinois Soil SFO

DFOP

IORE

6.89

6.84

6.94

22.9

23.6

22.6

New Jersey Soil SFO

DFOP

IORE

7.07

6.89

7.1

23.5

25.7

23.1

Wisconsin Soil SFO

DFOP

IORE

26.6

16.7

18.5

88.5

267

230

Bruch West Soil SFO

DFOP

IORE

1.44

1.33

1.28

4.79

7.34

8.06

MRID 47700117

Lufa 5M Soil SFO

DFOP

IORE

1.63

1.48

1.45

5.41

8.44

8.12

MRID 47700121

Lufa 2.2 Soil SFO

DFOP

IORE

1.92

1.81

1.77

6.38

7.59

8.35
19

Table 3.1. Physical Chemical and Environmental Fate and Chemistry Properties of 

Ametoctradin

Parameter Value Reference/Comments

Li 10 Soil SFO

DFOP

IORE

3.36

3.21

3.27

11.2

12.8

12.2

Anaerobic soil 

metabolism

Bruch West

Soil

SFO

IORE

182

683

606

118000

MRID 47700119

47700145

Aerobic aquatic 

metabolism

BerghauserAltrhein

 Water

 Sediment

 Total system 

SFO

DFOP

SFO

0.69

2.07

1.72

2.29

2.18

5.71

Ranschgraben MRID 47700145

 Water

 Sediment

 Total system 

SFO

DFOP

SFO

0.89

2.12

1.51

2.94

7.81

5.01

Anaerobic aquatic 

metabolism

White Lake

 Water

 Sediment

 Total system 

IORE

IORE

SFO

DFOP

IORE

1.6

13.8

8.86

7.4

6.83

10.3

22.7

29.4

60.1

58.1

MRID 47700221

Mobility

Batch Equilibrium

Soil Kf

[L/kg] 1/N Kfoc[L/kg]

Schifferstadt

(loamy sand) 59.6 0.842 6620

MRID 47700133

LUFA 2.2

(loamy sand) 61.2 0.799 3560

Obihiro

(silty loam) 80.0 0.819 4850

New Jersey 

(loam) 44.7 0.751 4060

1680

(loamy sand) 38.0 0.773 4320

LUFA 3A 

(loam) 72.8 0.810 2250

Studernheim 

(sandy loam) 23.9 0.718 1580

California 

(sandy loam) 14.2 0.677 4060

Laboratory 

volatility NA Volatility not likely based on low vapor pressure

Field Dissipation

Terrestrial field 

dissipation

Location Kinetic 

Model DT50(d) DT90(d)

Ontario SFO 4.2 14.0

Illinois SFO 1.1 3.8 MRID 47700127 

Florida SFO 5.0 16.5

California DFOS 1.6 19.5 MRID 47700106 Washington FOMC 0.4 4.2

Bioaccumulation
20

Table 3.1. Physical Chemical and Environmental Fate and Chemistry Properties of 

Ametoctradin

Parameter Value Reference/Comments

Accumulation in 

fish, BCF

Edible tissues: 3.9-4.5X

Inedible tissues: 186-190X

Whole Fish: 148-149X 

MRID 47700165

a SFO = Single first-order, DFOP = Double first-order in parallel, DFOS = Double first-order in Series, 

FOMC = First Order multi compartment, IORE = Intermediate-order rate equation b Bolded kinetic models are the best described dissipation/degradation patterns based on the model with the lowest 

model error (%) and/or the least bias in residuals of regression data points.

In aerobic aquatic sediment systems, ametoctradin rapidly dissipated under dark conditions, and 

M650F01, M650F02, M650F03, and M650F04 were the major metabolites. Dissipation times 

(DT50 values) in the total system were 1.5 – 1.7 days (ametoctradin), 3.1 – 4.9 days (M650F01), 

17.1 – 33.5 days (M650F02), and 377 – 479 days (M650F03). In water, DT50 values were 0.7 –

0.9 days (ametoctradin), 3.2 – 3.4 days (M650F01), 14 – 17.2 days (M650F02), and 226 – 328 

days (M650F03). In the sediment, DT50 values for ametoctradin were 1.9 – 2.2 days. In an 

anaerobic aquatic sediment system, ametoctradin also readily degraded with DT50 of total system 

of 7.4 days, and M650F01 and M650F03 were the major metabolites. Dissipation/degradation of 

M650F01, M650F02, M650F03, and M650F04 are provided in Table A-2 in Appendix A. 

Figure A-1 in Appendix A shows the proposed route of degradation of ametoctradin in 

water/sediment systems.

Under aerobic conditions, ametoctradin degraded rapidly in four different US soils (1 sandy

loam, 2 loam, and 1 loamy sand), with DT50 values ranging from 6.84 to 26.6 days and 

corresponding DT90 values ranging from 22.6 to 267 days. In four other European soils (2 sandy 

loam and 2 loamy sand), the DT50 values of ametoctradin ranged from 1.33 to 3.36 days and 

corresponding DT90 values ranging from 4.79 to 12.8 days. Ametoctradin underwent an initial 

rapid period of biotransformation over the first 0-6 days, followed by a slower degradation 

period. Degradation rates were best described using double first-order in parallel (DFOP) or 

single first-order (SFO) kinetics models. Figure A-2 in Appendix A depicts the proposed 

metabolic transformation pathway of ametoctradin in soil.

Several metabolites were formed at levels greater than 10% via microbial processes. The 

oxidation of the aliphatic side chain produced M650F01, M650F02, M650F03, and M650F04. 

These metabolites were observed at levels greater than 10% TAR in all soils, but declined over 

time. In soil treated with [14C]- ametoctradin, 14CO2 was found at levels up to 65.7% TAR, 

demonstrating further degradation of the low molecular weight components. Non-extractable 

residues reached maximum levels of 51.4% TAR by the end of the 365-day study. Under 

anaerobic conditions, ametoctradin dissipated in soil with a DT50 value of 683 days. This 

dissipation during the anaerobic phase is mainly due to the formation of bound residues since no 

mineralization was observed and the formation of metabolites was negligible. 

The degradation rates of the ametoctradin transformation products, M650F03 and M650F04,

were also determined in four aerobic soils (three European and one U.S. soil) ranging from sand 

to loam conditions (Table A-3, Appendix A). M650F03 was slightly persistent to moderately 

persistent under the conditions of the study, with DT50s ranging between 29 and 75 days and 
21

DT90 between 96 and 249 days. The only major transformation product, M650F04, continued to 

accumulate to the end of the study period (120 DAT), which is consistent with the parent studies.

Ametoctradin degrades in soil with and without the presence of light. The rate of transformation 

was slower under irradiation than in the dark control, indicating that irradiation does not enhance 

transformation of ametoctradin in soil. A phototransformation half-life could not be determined. 

Phototransformation of ametoctradin is not considered a route of dissipation in the environment. 

Two terrestrial field studies with a total of five sites were designed to evaluate the fate behavior 

of ametoctradin and its degradates in soils supporting uses in row vegetables, orchards/vineyards, 

and root vegetables in North America. Three field trials in ONT (Canada), IL, and FL were 

initiated to support the row vegetable use. Two field trials were initiated in areas representative 

of major orchard/vineyard and root vegetable (WA and CA) regions of NAFTA. The major route 

of dissipation of ametoctradin in the bare soil was biotransformation. DT50 values ranged from 

0.4 – 5.0 days and corresponding DT90s ranged from 3.2 – 16.5 days. Three major 

transformation products, M650F01, M650F02, and M650F03, were similarly non-persistent, 

with DT50s ranging from 1.3 – 13.3 days, with corresponding DT90s of 4.5 – 144 days. M650F03,

however, was moderately persistent in California sandy loam with a DT50 and DT90 of 101 and 

336 days, respectively. Dissipation of the fourth major transformation product, M650F04, was 

more variable between trial sites. M650F04 was persistent in Ontario (estimated DT50 > 365 

days), moderately persistent in Illinois and California (DT50 = 177 and 113 days, respectively), 

and slightly persistent in Washington soils (DT50 = 36.1 days). M650F04 was not found in 

significant quantities in the Florida study site. 

Among all sites, the maximum levels of the transformation products relative to the initial 

measured amount of the parent following the final application were: 14-29% for M650F01, 4-

23% for M650F02, 38-171% for M650F03 (except FL), and 37-77% for M650F04 (except FL). 

At the site in Florida, M650F03 and M650F04 were observed at lower amounts than other sites 

(4-12% of the applied ametoctradin parent material); however, transformation pathways were 

consistent with the other sites. Ametoctradin and the transformation products were not detected 

below the 15.2-30.5 cm segment at any site (LOQ = 0.01 mg/kg). Soil moisture conditions were 

favorable for leaching during and/or shortly after the application period at most sites, indicating 

that ametoctradin and its major transformation products have low inherent susceptibility for 

leaching. Ametoctradin is not volatile, and therefore this route of dissipation was not evaluated 

in the field.

Ametoctradin did not carryover to the following growing season at any of the trial sites. Of the 

four transformation products monitored in the field, only M650F04 was present at the beginning 

of the following growing season in both Ontario and Illinois test plots (279-280 days after first 

application) at 23 - 43% of the amount of applied parent material. 

Mobility

Batch adsorption studies were performed for ametoctradin and four major soil metabolites: 

M650F01, M650F02, M650F03, and M650F04. Desorption was characterized for M650F03 and 

M650F04 only. The sorption of ametoctradin onto sterilized soil was investigated in a laboratory 

sorption study with five European, and two North American soils. The measured KFOC values 
22

ranged from 1580 L/kg to 6620 L/kg, while the corresponding Freundlich exponents (1/n values) 

ranged from 0.677 to 0.842. Ametoctradin adsorption was not linear with concentration, but 

tended to have slightly higher adsorption at lower concentrations. Ametoctradin is expected to be 

slightly mobile to hardly mobile according to FAO mobility classifications (FAO, 2000). Table 

3.1 provides the results of the sorption study. The estimated KFoc of degradates range from 8 to 

193 L/Kg and would be categorized as highly mobile to moderately mobile (Table A-4, 

Appendix A). Desorption constants were not evaluated for parent and degradates except for 

M650F03 and M650F04. The desorption values of M650F03 and M650F04 suggest that these 

metabolites are readily desorbed from soils, indicating that adsorption of these compounds is 

reversible.

Ametoctradin is a non-volatile compound and sparingly soluble in water. Therefore, transport of 

ametoctradin in the environment is expected to occur predominantly via spray drift and runoff of 

dissolved degradates and parent residues sorbed to suspended sediment. Terrestrial field 

dissipation studies confirmed that ametoctradin’s mobility was limited to surface horizons at all 

sites. However, depending on soil, site and meteorological conditions ametoctradin may be 

transported off-site to water sources mainly via runoff and spray drift and to lesser extent by 

leaching. 

Bioaccumulation

The reported values of bioconcentration factors at steady state (BCFSS) were 4.5X, 190X, and 

149X for edible, inedible, and whole fish tissues, respectively, of the low dose (0.1 μg/L) group. 

The corresponding BCFSS values for the high dose (1.0 μg/L) group were 3.9X, 186X, and 148X.

Time to reach 90% depuration was less than 3 days. The log Kow of 4.4 indicates that it has 

potential to bioaccumulate; however, the registrant reported a BCF value of ≤ 149X, and rapid 

depuration values suggest that ametoctradin is not a bioaccumulative compound.

The KOW (octanol-water coefficient based) Aquatic BioAccumulation Model (KABAM v.1.0) 

can be used to estimate potential bioaccumulation of ametoctradin residues in a freshwater 

aquatic food web and subsequent risks these residues pose to terrestrial organisms via 

consumption of contaminated aquatic prey (i.e., aquatic invertebrates and fish). However, it was 

not necessary to use KABAM for this assessment to estimate/explore the potential for 

bioaccumulation because of the lack of observed toxicity for various aquatic and terrestrial taxa.

3.2.2 Aquatic Exposure Estimates for Ametoctradin 

A Tier I screening-level surface water exposure for aquatic risk assessment was conducted for 

the Section 3 proposed new chemical registration. Modeled application rates represent the 

maximum use pattern of the proposed label for use on vegetable, grapes, hops, and ornamentals. 

The aquatic exposure estimates presented in this assessment were based on the use of models, as 

no surface and groundwater monitoring data are available for ametoctradin within the continental 

United States. To simulate surface water exposure for the ecological risk assessment, the Tier I

GENEEC (GENeric Estimated Environmental Concentration, version 2.0, May 1, 2001) model

was used. 
23

GENEEC2 Model Inputs for Ametoctradin

GENEEC2 is a single-event model, based on a single, large rainfall/runoff event occurring on a 10-

hectare field that removes a large quantity of pesticide at one time from the field to a pond that has a 

20,000-liter water volume and is 2-meter deep. As such, it provides upper bound values on the 

concentrations that might be found in surface water due to the use of a pesticide. The model also 

incorporates spray drift, the amount of which is dependent primarily upon the droplet size of the 

spray, release height, and meteorological condition during pesticide application. GENEEC2 provides 

a rapid screen to separate the low risk pesticides from those that need more refined assessments. OPP 

assumes that if this model indicates no concerns when compared with the appropriate toxicity data, 

then further analysis is not necessary as there would be no effect on the species. Inputs for 

GENEEC2 are listed in Table 3.2. These parameters were selected in accordance with EFED’s 

input parameter guidance (U.S. EPA, 2010b). Single first order (SFO) half-lives listed in Table 

3.1 were used for exposure modeling. Additional information on this model can be found at: 

http://www.epa.gov/oppefed1/models/water /index.htm.

Table 3.2. GENEEC (version 2.0) input parameter values for Ametoctradin (BAS 650 F) 

Parameter Value Source Comments

Application Rate 0.274 lb a.i./acre BAS 650 00F

Zampro

Orvego

Maximum application rate was 

based on information provided in 

the submitted labels for vegetables, 

grape, hops, and ornamentals and 

flower bulbs

Number of Applications 3 to 4 BAS 650 00F

Zampro

Orvego

#s of application were based on 

information provided in the 

submitted labels for vegetables, 

grape, hops, and ornamentals and 

flower bulbs

Interval between 

Applications

5 days (vegetable)

7 days (grape)

10 days (hops)

10 days (ornamentals and 

flower bulbs)

BAS 650 00F

Zampro

Orvego

Application intervals were based 

on information provided in the 

submitted labels for vegetables, 

grape, hops, and ornamentals and 

flower bulbs

Soil Partitioning 

Coefficient (Kfoc)

3912.5 mL/goc MRID 47700133 Mean value 

Aerobic Soil 

Metabolism t1/2

11.9 days MRID 47700117

MRID 47700118

MRID 47700121

90th percentile upper confidence 

bound on the mean.

Wetted in? No --- ---

Depth of Incorporation 0 in --- Foliar application
24

Table 3.2. GENEEC (version 2.0) input parameter values for Ametoctradin (BAS 650 F) 

Parameter Value Source Comments

Method of Application Ground

Aerial

BAS 650 00F

Zampro

Orvego

---

Spray Drift Fraction Ground

Aerial

6.4

13.0

Model defaults

Solubility in Water 0.15 mg/L MRID 47700012 pH = 7

Aerobic Aquatic 

Metabolism t1/2

1.94 days MRID 47700145 Total System

90th percentile upper confidence 

bound on the mean

Hydrolysis t1/2

0 days MRID 47700015 Stable to hydrolysis

Aquatic Photolysis t1/2

76.8 days MRID 47700016 ---

The aquatic EECs for the various scenarios and application methods are listed in Table 3.3. 

EECs were highest for aerial applications to grapes with peak, 21-day and 60-day values of 5.24

μg/L, 1.36 μg/L, and 0.48 μg/L, respectively. The modeling results of EECs for various 

scenarios are listed in Appendix B.

Table 3.3. GENEEC Estimated Environmental Concentrations (EECs) Resulting from 

Applications of Ametoctradin for Proposed Uses

Model Use Method

Application Rate

(interval between 

applications)

Peak 

EEC

(μg/L)

21-Day 

EEC

(μg/L)

60-Day 

EEC

(μg/L)

Surface Water 

(GENEEC2)

Vegetables* Aerial 3 apps @ 0.274 lb a.i./acre

(5-day interval) 5.18 1.36 0.48

Grapes

Aerial

4 apps @ 0.274 lb a.i./acre

(7-day interval)

5.24 1.36 0.48

Ground 5.00 1.28 0.46

Hops Aerial 3 apps @ 0.274 lb a.i./acre

(10-day interval) 4.16 1.09 0.39

Ornamentals

&

Golf Courses

Ground 4 apps @ 0.274 lb a.i./acre

(10-day interval) 4.26 1.09 0.39

*Although the Brassica leafy vegetables group requires a 7-day interval, it was conservatively included in the 5-

day interval group for all other vegetables because GENEEC does not distinguish between types of vegetables.

Maximum EECs in bold.
25

PRZM/EXAMS Model Inputs for Ametoctradin

Since Tier I aquatic EECs exceed the toxicity value for listed non-vascular aquatic plants, the 

Tier II model Pesticide Root Zone Model (PRZM v3.12.2) linked with EXposure Analysis 

Modeling System (EXAMS v2.98.4.6) via the model shell PRZM/EXAMS (PE v5.0, Nov. 15, 

2006) was run to estimate baseline-level exposures for representative crop scenarios. 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 run for multiple (usually 30) years, and the 

Agency estimates peak and running mean values that are expected once every ten years based on 

the daily values generated during the simulation. The coupled PE models and users manuals are 

available from the U.S. Environmental Protection Agency Water Models web-page (U.S. EPA, 

2011).

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. A summary of inputs used to estimate 

ametoctradin concentrations in the aquatic systems for ecological risk assessment are listed in 

Table 3.4.

Table 3.4. PRZM/EXAM input parameter values for Ametoctradin (BAS 650 F) 

Parameter Value Source Comments

Application Rate (lb 

a.i./A)

0.274 lb a.i/A BAS 650 00F

Zampro

Orvego

Maximum application rate was 

based on information provided in 

the submitted labels for vegetables, 

grape, hops, and ornamentals and 

flower bulbs

Number of Applications 3-4 BAS 650 00F

Zampro

Orvego

#s of application were based on 

information provided in the 

submitted labels for vegetables, 

grape, hops, and ornamentals and 

flower bulbs
26

Table 3.4. PRZM/EXAM input parameter values for Ametoctradin (BAS 650 F) 

Parameter Value Source Comments

Interval between 

applications (days) 5 to 10

BAS 650 00F

Zampro

Orvego

Application intervals were based 

on information provided in the 

submitted labels for vegetables, 

grape, hops, and ornamentals and 

flower bulbs

Crops

PRZM/EXAMS 

Scenarios and 

application Dates

Brassica Leafy Vegetable

 FL Cabbage: Jan 8

Based on 

PRZM/EXAMS 

Scenarios

Approximate 30 to 45 days before 

harvest date 

Bulb Vegetables

 GA Onion: Jan 8

Cucurbit Vegetable

 FL Cucumber: Jan 8

Fruiting Vegetables

 FL Pepper: Nov 01

 FL Tomato: Mar 15

 PA Tomato: Sept 15

Leafy Vegetables

 CA Lettuce: Mar 12

Tuberous and Corm 

Vegetables

 FL carrot: Dec 01

 ID Potatoes: Aug 15

 ME Potatoes: Nov 05

Grape

 NY Grape: Sept 10

 CA grape: Aug 27

Hops

 OR Hops: Aug 01

Ornamentals

 MI Nursery: Nov 15

 FL Nursery Nov 30

Golf Courses

 FL Turf: Nov 05

 PA Turf: Oct 21
27

Table 3.4. PRZM/EXAM input parameter values for Ametoctradin (BAS 650 F) 

Parameter Value Source Comments

Residential

 CA Residential: May 11

Soil Partitioning 

Coefficient (Kfoc; 

ml/goc)

3912.5 MRID 47700133 Mean value 

Aerobic Soil 

Metabolism t1/2 (d)

11.9 MRID 47700117

MRID 47700118

MRID 47700121

90th percentile upper confidence 

bound on the mean.

Wetted in No --- ---

Depth of Incorporation 

(inches)

0 --- Foliar application

Method of Application Ground Spray

Aerial Spray

BAS 650 00F

Zampro

Orvego

---

Spray Drift Fraction Ground

Aerial

1.0%

5.0%

Model defaults

Application Efficiency Ground Spray

Aerial Spray

0.99

0.95

Model defaults

Molecular Mass (g/mol) 275.4 MRID 4770009 Product Chemistry

Solubility in Water 

(mg/L)

0.15 MRID 47700012 pH = 7

Vapor Pressure ( mm 

Hg)

4.50 x 10-12 (25°C) MRID 4770009 Product Chemistry

Henry’s law constant

(atm•m3

•mol-1)

3.10 x 10-9 (25°C) 

MRID 47700010 Product Chemistry

Aerobic Aquatic 

Metabolism t1/2 (days)

1.94 MRID 47700145 Total System

90th percentile upper confidence 

bound on the mean

Hydrolysis t1/2

0 MRID 47700015 Stable to hydrolysis

Aquatic Photolysis t1/2

(days)

76.8 MRID 47700016 ---
28

The refined water column EECs, as predicted by PRZM/EXAMS, are located in Table 3.5, and 

outputs are included in Appendix B. Pore water and sediment EECs for the FL Tomato and NY 

Grape scenarios are located in Table 3.6.

Table 3.5. PRZM/EXAMS Estimated Environmental Concentrations (EECs) in Water 

Column Resulting from Applications of Ametoctradin for the Proposed Uses

PRZM/EXAMS 

Scenario Method

Application Rate 

(Interval between 

Applications) 

Peak 

EEC

(μg/L)

21-Day 

EEC

(μg/L)

60-Day 

EEC

(μg/L)

FL Cabbage

Aerial 3 apps @ 0.274 lb/A

(7 days)

1.23 0.54 0.28

Ground 0.80 0.23 0.13

GA Onion

Aerial

3 apps @ 0.274 lb/A

(5 days)

1.76 0.82 0.39

Ground 0.95 0.37 0.18

FL Cucumber

Aerial 2.43 0.70 0.28

Ground 1.87 0.38 0.16

FL Pepper

Aerial 3.17 0.86 0.32

Ground 2.81 0.64 0.25

FL Tomato

Aerial 3.17 0.62 0.30

Ground 3.28 0.49 0.23

PA Tomato

Aerial 2.61 0.75 0.37

Ground 2.40 0.51 0.25

CA Lettuce

Aerial 1.06 0.53 0.24

Ground 0.36 0.13 0.07

FL Carrot

Aerial 1.40 0.46 0.18

Ground 0.82 0.20 0.08

ID Potato

Aerial 1.06 0.43 0.20

Ground 0.38 0.17 0.09

ME Potato

Aerial 2.10 1.23 0.69

Ground 1.40 0.75 0.44

CA Grape Aerial

4 apps @ 0.274 lb/A

(7 days)

0.82 0.27 0.12

Ground 0.16 0.05 0.03

NY Grape Aerial 3.11 1.20 0.68

Ground 3.02 1.02 0.54

OR Hops Aerial 3 apps @ 0.274 lb/A

(10 days)

0.83 0.30 0.19

Ground 0.52 0.13 0.07

MI Nursery Ground 4 apps @ 0.274 lb/A

(10 days)

0.40 0.13 0.07

FL Nursery Ground 0.69 0.13 0.07

FL Turf Ground

4 apps @ 0.274 lb/A

(10 days)

0.46 0.31 0.13

PA Turf Ground 0.35 0.15 0.11

CA Residential Ground 0.22 0.11 0.07

Maximum EECs in bold.
29

Table 3.6. PRZM/EXAMS Estimated Environmental Concentrations (EECs) in Pore 

Water and Sediment Resulting from Applications of Ametoctradin for FL Tomato and 

NY Grape Scenarios

PRZM/EXAMS 

Scenario Method Matrix

Peak 

EEC

(μg/L)

21-Day 

EEC

(μg/L)

60-Day 

EEC

(μg/L)

FL Tomato

Aerial

Pore Water

0.19 0.16 0.11

Ground 0.16 0.14 0.10

NY Grape Aerial 0.77 0.72 0.59

Ground 0.71 0.66 0.55

PRZM/EXAMS 

Scenario Method Matrix Peak EEC(μg/kg)

21-Day EEC

(μg/kg)

60-Day EEC

(μg/kg)

FL Tomato

Aerial 

Sediment*

29.74 25.04 17.22

Ground 25.04 21.91 15.65

NY Grape Aerial 120.51 112.68 92.34

Ground 111.12 103.29 86.08

Maximum EECs in bold.

*Assumes 4% organic carbon in sediment (Arnot et al., 2004).

3.2.3 Terrestrial Wildlife Exposures

Terrestrial wildlife exposure estimates are typically calculated for birds and mammals 

emphasizing a dietary exposure route for uptake of pesticide residues on vegetative matter and 

insects. Birds are used as surrogates for terrestrial-phase amphibians as well as reptiles. For 

exposure to terrestrial organisms, pesticide residues on food items are estimated based on the 

assumption that organisms are exposed to a single pesticide residue in a given exposure scenario. 

The residue estimates from spray applications are based on a nomogram by Hoerger and Kenaga 

(1972) as modified by Fletcher et al. (1994) that correlated residue levels, based on application 

rate, on various terrestrial items immediately following application in the field. The “maximum” 

residue concentration, an upper bound defined by Fletcher et al. (1994), for each food group was 

derived from literature and tolerance data. 

Dissipation of ametoctradin residues on food items following single and multiple applications is 

predicted using a first-order residue degradation half-life with EFED's T-REX v1.4.1 model. TREX assumes a default foliar dissipation half-life estimate of 35 days (Willis and McDowell, 

1987). This half-life is used in lieu of ametoctradin foliar dissipation data, which were not 

submitted by the registrant. The maximum predicted residues on avian and mammalian food 

items (dietary EECs) as a result of applications to non-crop areas are provided in Table 3.7 and 

3.8. 

The residues or EECs on food items may be compared directly with sub-acute dietary toxicity 

data or converted to an ingested whole-body dose (single oral dose). Single oral dose estimates 

represent, for many pesticides, an exposure scenario where absorption of the pesticide is 

maximized over a single ingestion event. Sub-acute dietary estimates provide for possible effects 

of the dietary matrix and more extended time of gut exposure to pesticide absorption across the 

gut. However, dietary exposure endpoints are limited in their utility because the current food 

ingestion estimates are uncertain and may not be directly comparable from laboratory conditions 

to field conditions. The EEC is converted to an oral dose by multiplying the EEC by the 
30

percentage of body weight consumed as estimated through allometric relationships. These 

consumption-weighted EECs (i.e., EEC equivalent dose) are determined for each food source 

and body size for birds (20, 100, and 1000 g) and mammals (15, 35, and 1000 g). EEC 

equivalent doses for birds and mammals are given in Tables 3.7 and 3.8, respectively. Example 

output from T-REX is included in Appendix C.

Table 3.7. Avian Exposure Concentration Estimates for Ametoctradin

Feeding Category

Dietary-based 

EECs (mg/kgfood item)

Dose-based EECs (mg/kg-bw)

Small

(20 g)

Medium

(100 g)

Large

(1000 g)

Vegetables* 

3 apps @ 0.274 lb a.i./acre

(5-day interval)

Short grass 179.27 204.17 116.42 52.12

Tall grass 82.16 93.58 53.36 23.89

Broadleaf plants/small insects 100.84 114.84 65.49 29.32

Fruits/pods/seeds/large insects 11.20 12.76 7.28 3.26

Granivores - 2.84 1.62 0.72

Grapes

4 apps @ 0.274 lb a.i./acre

(7-day interval)

Short grass 216.23 246.26 140.43 62.87

Tall grass 99.11 112.87 64.36 28.82

Broadleaf plants/small insects 121.63 138.52 78.99 35.37

Fruits/pods/seeds/large insects 13.51 15.39 8.78 3.93

Granivores - 3.42 1.95 0.87

Hops

3 apps @ 0.274 lb a.i./acre

(10-day interval)

Short grass 163.96 186.73 106.48 47.67

Tall grass 75.15 85.59 48.80 21.85

Broadleaf plants/small insects 92.23 105.04 59.90 26.82

Fruits/pods/seeds/large insects 10.25 11.67 6.66 2.98

Granivores - 2.59 1.48 0.66

Ornamentals & Golf Courses

4 apps @ 0.274 lb a.i./acre

(10-day interval)

Short grass 200.26 228.08 130.06 58.23

Tall grass 91.79 104.54 59.61 26.69

Broadleaf plants/small insects 112.65 128.29 73.16 32.75

Fruits/pods/seeds/large insects 12.52 14.25 8.13 3.64

Granivores - 3.17 1.81 0.81

*Although the Brassica leafy vegetables group requires a 7-day interval, it was conservatively included in the 

5-day interval group for all other vegetables.
31

Table 3.8. Mammalian Exposure Concentration Estimates for Ametoctradin

Feeding Category

Dietary-based 

EECs (mg/kgfood item)

Dose-based EECs (mg/kg-bw)

Small

(15 g)

Medium

(35 g)

Large

(1000 g)

Vegetables* 

3 apps @ 0.274 lb a.i./acre

(5-day interval)

Short grass 179.27 170.92 118.13 27.39

Tall grass 82.16 78.34 54.14 12.55

Broadleaf plants/small insects 100.84 96.14 66.45 15.41

Fruits/pods/seeds/large insects 11.20 10.68 7.38 1.71

Granivores - 2.37 1.64 0.38

Grapes

4 apps @ 0.274 lb a.i./acre

(7-day interval)

Short grass 216.23 206.16 142.48 33.04

Tall grass 99.11 94.49 65.30 15.14

Broadleaf plants/small insects 121.63 115.96 80.15 18.58

Fruits/pods/seeds/large insects 13.51 12.88 8.91 2.06

Granivores - 2.86 1.98 0.46

Hops

3 apps @ 0.274 lb a.i./acre

(10-day interval)

Short grass 163.96 156.32 108.04 25.05

Tall grass 75.15 71.65 49.52 11.48

Broadleaf plants/small insects 92.23 87.93 60.77 14.09

Fruits/pods/seeds/large insects 10.25 9.77 6.75 1.57

Granivores - 2.17 1.50 0.35

Ornamentals & Golf Courses

4 apps @ 0.274 lb a.i./acre

(10-day interval)

Short grass 200.26 190.93 131.96 30.60

Tall grass 91.79 87.51 60.48 14.02

Broadleaf plants/small insects 112.65 107.40 74.23 17.21

Fruits/pods/seeds/large insects 12.52 11.93 8.25 1.91

Granivores - 2.65 1.83 0.42

*Although the Brassica leafy vegetables group requires a 7-day interval, it was conservatively included in the 

5-day interval group for all other vegetables.

3.2.4 Terrestrial and Semi-Aquatic Plant Exposures

Terrestrial and semi-aquatic plants may be exposed to pesticides from runoff, spray drift, or 

volatilization. Semi-aquatic plants are those that inhabit low-lying wet areas that may be dry at 

certain times of the year. The runoff scenario in TerrPlant v1.2.2 is: (1) based on a pesticide's 

water solubility and the amount of pesticide present on the soil surface and its top one 

centimeter, (2) characterized as "sheet runoff" (one treated acre to an adjacent acre) for dry areas, 

(3) characterized as "channel runoff" (10 acres to a distant low-lying acre) for semi-aquatic or 

wetland areas, and (4) based on runoff values of 1, 2, and 5% for water solubility values of <10, 

10-100, and >100 ppm, respectively. Spray drift is assumed as (1) 1% for ground application, (2) 

5% for aerial, airblast, forced air, and spray chemigation applications, and (3) 0% for granular 

applications. Currently, EFED derives plant exposure concentrations from a single maximum 
32

application rate only. Exposure through volatilization is not accounted for in this baseline

assessment; however, based on the low vapor pressure, it is not expected to be a significant route 

of exposure. EECs are presented in Table 3.9. Example of TerrPlant output is provided in 

Appendix D.

Table 3.9. EECs for Terrestrial and Semi-aquatic Plants for Aerial and/or Ground 

Application to Turf and Non-crop Areas

Description

All Uses

1 app @ 0.274 lb a.i./acre

Ground

(spray)

Aerial

(spray)

Runoff to dry areas 0.00274 0.00274

Runoff to semi-aquatic areas 0.0274 0.0274

Spray drift 0.00274 0.0137

Total for dry areas 0.00548 0.01644

Total for semi-aquatic areas 0.03014 0.0411

4 Ecological Effects Analysis

A search of the public ECOTOX database (http://cfpub.epa.gov/ecotox) on August 25, 2011 did 

not yield any aquatic or terrestrial open literature studies for ametoctradin. This result is to be 

expected as ametoctradin is a new chemical. Therefore, only studies submitted by the registrant 

were evaluated to determine the effects of ametoctradin on non-target organisms. The Ecological 

Incident Information System (EIIS) was also searched on August 25, 2011 to provide a refined 

characterization of the ecological effects. As expected, no incidents were found for ametoctradin.

Submitted ecological toxicity data were jointly reviewed by all participating countries. DERs 

were compiled in the form of a monograph (DP393441).

4.1 Aquatic Effects Summary

The acute and chronic toxicity of ametoctradin was determined for a variety of algal, invertebrate 

and fish species. Acute and/or chronic toxicity studies were also conducted on selected species 

with the end-use products BAS 650 00 F (ametoctradin only; 19.2%) and BAS 651 00 F

(ametoctradin; ~27% & dimethomorph; ~20%), as well as the transformation products M650F01, 

M650F02, M650F03, and M650F04. BAS 651 00 F is the BASF reference name for the premix 

of ametoctradin and dimethomorph; the data set for BAS 651 00 F supports both the Orvego and 

Zampro products. A summary of all submitted aquatic toxicity studies is included in Table 4.1. 

Acute toxicity 

The test concentrations for the acute toxicity tests with ametoctradin (technical grade active 

ingredient) were all limited by the low solubility of the test substance. Studies were conducted by 

super-saturating test solutions (generally, a glass wool method was used) prior to exposure rather 

than using co-solvents; therefore, the highest concentration tested represents the upper limit of 

the functional solubility of the test material. Test solutions were observed to be clear with no 

precipitate formed; for the aquatic plant studies, suspensions were centrifuged prior to initiation. 

Acute effect concentrations (EC50 values) were generally above the highest achievable test 

TGAI
33

concentrations, with the exception of the freshwater diatom N. pelliculosa and the aquatic plant 

L. gibba. The most sensitive species to acute ametoctradin exposure was N. pelliculosa with an 

EC50 (50% effect on yield measurements) of 7.8 μg a.i./L. Therefore, with the exception of two 

aquatic plant species, ametoctradin was not acutely toxic to aquatic organisms up to its 

functional limit of solubility.

Acute toxicity studies with BAS 650 00 F (ametoctradin only) and BAS 651 00 F (ametoctradin 

and dimethomorph) were conducted with green algae, Daphnia, rainbow trout and the marine 

amphipod L. plumulosus. Results are summarized as mg EP/L and mg a.i./L (as ametoctradin). 

BAS 650 00 F was not acutely toxic to any species tested, with EC50 values greater than the 

highest concentration tested. The increased solubility of ametoctradin in the formulated product 

BAS 650 00 F (200 g ametoctradin/L) allowed for exposure to higher concentrations of the 

active ingredient, but did not result in acute toxicity to aquatic organisms. However, BAS 651 00 

F (300 g ametoctradin/L + 225 g dimethomorph/L) was acutely toxic to green algae and rainbow 

trout within the range of concentrations tested. Rainbow trout was the more sensitive of the two 

species tested, with an LC50 of 23.2 mg EP/L, or 6.32 mg a.i./L expressed relative to 

ametoctradin content. The increased sensitivity of aquatic species to BAS 651 00 F over BAS 

650 00 F may be due to the presence of dimethomorph in the BAS 651 00 F formulation. 

End-use Products

The acute toxicity of M650F03 and M650F04 was determined for green algae, Daphnia, and 

rainbow trout. In addition, acute toxicity studies with M650F01 and M650F02 were conducted 

with Daphnia. All studies were conducted at nominal application rates up to 100 mg/L. The 

transformation products were not acutely toxic within the range of concentrations tested, as 

EC50/LC50 values exceeded the highest test concentrations.

Transformation Products

Chronic toxicity 

The chronic toxicity of ametoctradin (technical grade active ingredient) was determined in a 21-

day semi-static test with Daphnia and a 33-day early life-stage test with fathead minnow. 

Chronic exposure resulted in adverse effects on reproduction in Daphnia (NOAEC = 44 μg 

a.i./L) and reduced survival in larval fathead minnows (NOAEC = 48 μg a.i./L).

TGAI

In a 28-day static spiked sediment study with BAS 650 00 F, a significant reduction in 

emergence rate was seen for the freshwater midge C. riparius. The NOAEC based on mean 

measured concentrations of ametoctradin was 221.6 mg a.i./kg dw sediment or 0.242 mg a.i./L in 

pore water. 

End-use Products

Chronic exposure of M650F03 to Daphnia resulted in significant reductions in parental growth 

and survival and reduced fecundity. The NOAEC was 41.8 mg/L.

Transformation Products
34

Table 4.1. Toxic Effects in Aquatic Organisms Exposed to Ametoctradin

Study Type & 

Purity or Product Species Toxicity Value Toxicity Classification+

Study 

Classification MRID #

Toxicity of the Technical Grade Active Ingredient

850.1075

Acute Freshwater

Fish

99.1%

Rainbow trout

(Oncorhynchus 

mykiss)

LC50: >64.6 μg a.i./L

NOAEC: 36.6 μg a.i./L

(mortality and tottering)

Unknown Acceptable 477001-55

850.1075

Acute Freshwater

Fish

99.3%

Common carp

(Cyprinus 

carpio)

LC50: >110 μg a.i./L

NOAEC: 110 μg a.i./L

(no effects)

Unknown Acceptable 477002-16

850.1075

Acute Freshwater

Fish

99.1%

Bluegill sunfish

(Lepomis 

macrochirus)

LC50: >129 μg a.i./L

NOAEC: 129 μg a.i./L

(no effects)

Unknown Acceptable 477001-57

850.1075

Acute Freshwater 

Fish

99.3%

Fathead minnow

(Pimephales 

promelas)

LC50: >123 μg a.i./L

NOAEC: 123 μg a.i./L

(no effects)

Unknown Acceptable 477001-58

850.1010

Acute Freshwater 

Invertebrate

99.3%

Water flea

(Daphnia 

magna)

EC50: >155 μg a.i./L

NOAEC: 155 μg a.i./L

(no effects)

Unknown Acceptable 477001-66

850.5400

Non-vascular Plant

99.3%

Green algae

(Pseudokirchneriella 

subcapitata)

EC50: >118 μg a.i./L

NOAEC: 36 μg a.i./L

(growth rate and cell density)

Unknown Acceptable 477001-73

850.5400

Non-vascular Plant

99.3%

Blue-green algae

(Anabaena flosaquae)

EC50: >67.9 μg a.i./L

NOAEC: 5.3 μg a.i./L

(growth rate, yield, and cell 

density)

Unknown Acceptable 477001-77

850.5400

Non-vascular Plant

99.3%

Freshwater 

diatom

(Navicula 

pelliculosa)

EC50: 7.8 μg a.i./L*

(yield and cell density)

NOAEC: 1.4 μg a.i./L*

(growth rate, yield, and cell 

density)

Very highly 

toxic Acceptable 477001-78

850.5400

Non-vascular Plant

99.3%

Marine diatom

(Skeletonema 

costatum)

EC50: >108.3 μg a.i./L

NOAEC: 4.8 μg a.i./L

(growth rate, yield, and cell 

density)

Unknown Acceptable 477001-79

850.4400

Vascular Plant

99.3%

Duckweed

(Lemna gibba)

EC50: 132 μg a.i./L*

(yield)

NOAEC: 13 μg a.i./L*

(dry weight)

Highly toxic Acceptable 477001-80

850.1025

Estuarine/Marine 

Mollusk

99.3%

Eastern oyster

(Crassostrea 

virginica)

EC50: >97 μg a.i./L

NOAEC: 37 μg a.i./L

(reduction in shell deposition)

Unknown Acceptable 477001-61

850.1035

Acute

Estuarine/Marine 

Invertebrate

99.3%

Mysid shrimp

(Americamysis 

bahia)

EC50: >94 μg a.i./L

NOAEC: 94 μg a.i./L

(no effects)

Unknown Acceptable 477001-62
35

Table 4.1. Toxic Effects in Aquatic Organisms Exposed to Ametoctradin

Study Type & 

Purity or Product Species Toxicity Value Toxicity Classification+

Study 

Classification MRID #

850.1075

Acute

Estuarine/Marine 

Fish

99.3%

Sheepshead 

minnow

(Cyprinodon 

variegates)

LC50: >110 μg a.i./L

NOAEC: 110 μg a.i./L

(no effects)

Unknown Acceptable 477001-63

850.1400

Chronic ELS 

Freshwater Fish

99.1%

Fathead minnow

(Pimephales 

promelas)

NOAEC: 48 μg a.i./L *

LOAEC: 124 μg a.i./L

(survival)

Not applicable Acceptable 477001-64

850.1300

Chronic Freshwater 

Invertebrate

99.3%

Water flea

(Daphnia 

magna)

NOAEC: 44 μg a.i./L*

LOAEC: 88 μg a.i./L

(reproduction and length)

EC50: 148 μg a.i./L

(reproduction)

Not applicable Acceptable 477001-71

Toxicity of Metabolites

850.1075

Acute Freshwater 

Fish

M650F03; 82.6%

Rainbow trout

(Oncorhynchus 

mykiss)

LC50: >82.6 mg M650F03/L

NOAEC: 82.6 mg M650F03/L

(no effects)

Unknown

(Slightly toxic to 

Practically nontoxic)

Acceptable 477001-59

850.1075

Acute Freshwater 

Fish

M650F04; 95.8%

Rainbow trout

(Oncorhynchus 

mykiss)

LC50: >95.8 mg M650F04/L

NOAEC: 95.8 mg M650F04/L

(no effects)

Unknown

(Slightly toxic to 

Practically nontoxic)

Acceptable 477001-60

850.1010

Acute Freshwater 

Invertebrate

M650F01; 81.7%

Water flea

(Daphnia 

magna)

EC50: >100 mg M650F01/L

NOAEC: 100 mg M650F01/L

(no effects)

Practically nontoxic Acceptable 477001-67

850.1010

Acute Freshwater 

Invertebrate

M650F02; 75.8%

Water flea

(Daphnia 

magna)

EC50: >75.8 mg M650F02/L

NOAEC: 75.8 mg M650F02/L

(no effects)

Unknown

(Slightly toxic to 

Practically nontoxic)

Acceptable 477002-23

850.1010

Acute Freshwater 

Invertebrate

M650F03; 82.6%

Water flea

(Daphnia 

magna)

EC50: >82.6 mg M650F03/L

NOAEC: 46.3 mg M650F03/L

(immobility)

Unknown

(Slightly toxic to 

Practically nontoxic)

Acceptable 477001-68

850.1010

Acute Freshwater 

Invertebrate

M650F04; 95.8%

Water flea

(Daphnia 

magna)

EC50: >95.8 mg M650F04/L

NOAEC: 95.8 mg M650F04/L

(no effects)

Unknown

(Slightly toxic to 

Practically nontoxic)

Acceptable 477001-69

850.5400

Non-vascular Plant

M650F03; 82.6%

Green algae

(Pseudokirchneriella 

subcapitata)

EC50: >82.6 mg M650F03/L

NOAEC: 82.6 mg M650F03/L

(no effects)

Unknown

(Slightly toxic to 

Practically nontoxic)

Acceptable 477001-75

850.5400

Non-vascular Plant

M650F04; 95.8%

Green algae

(Pseudokirchneriella 

subcapitata)

EC50: >95.8 mg M650F04/L

NOAEC: <9.58 mg 

M650F04/L

(growth rate, yield, and cell 

density)

Unknown

(Slightly toxic to 

Practically nontoxic)

Supplemental 477001-76
36

Table 4.1. Toxic Effects in Aquatic Organisms Exposed to Ametoctradin

Study Type & 

Purity or Product Species Toxicity Value Toxicity Classification+

Study 

Classification MRID #

850.1300

Chronic Freshwater 

Invertebrate

M650F03; 83.5%

Water flea

(Daphnia 

magna)

NOAEC: 41.75 mg 

M650F03/L

LOAEC: 83.5 mg M650F03/L

(parental growth and survival, 

reduced fecundity)

EC50: 77.8 mg M650F03/L

(survival)

Not applicable Acceptable 477001-72

Toxicity of End-use Products^

850.1075

Acute Freshwater 

Fish

BAS 650 00 F

Rainbow trout

(Oncorhynchus 

mykiss)

LC50: >103 mg EP/L

(>19 mg a.i./L)

NOAEC: 103 mg EP/L

(19 mg a.i./L)

(no effects)

Not applicable Acceptable 477001-56

850.1075

Acute Freshwater 

Fish

BAS 651 00 F

Rainbow trout

(Oncorhynchus 

mykiss)

LC50: 23.2 mg EP/L

(6.32 mg a.i./L)

NOAEC: 22 mg EP/L

(5.98 mg a.i./L)

Not applicable Acceptable 477003-16

850.1010

Acute Freshwater 

Invertebrate

BAS 650 00 F

Water flea

(Daphnia 

magna)

EC50: >105.2 mg EP/L

(>19.4 mg a.i./L)

NOAEC: 105.2 mg EP/L

(19.4 mg a.i./L)

(no effects)

Not applicable Acceptable 477001-70

850.1010

Acute Freshwater 

Invertebrate

BAS 651 00 F

Water flea

(Daphnia 

magna)

EC50: >77.9 mg EP/L

(>21.2 mg a.i./L)

NOAEC: 77.9 mg EP/L

(21.2 mg a.i./L)

(no effects)

Not applicable Acceptable 477003-17

850.5400

Non-vascular Plant

BAS 650 00 F

Green algae

(Pseudokirchneriella 

subcapitata)

EC50: >100 mg EP/L

(>18.4 mg a.i./L)

NOAEC: 50 mg EP/L

(9.2 mg a.i./L)

(yield and cell density)

Not applicable Acceptable 477001-74

850.5400

Non-vascular Plant

BAS 651 00 F

Green algae

(Pseudokirchneriella 

subcapitata)

EC50: 72.6 mg EP/L

(19.8 mg a.i./L)

(yield)

NOAEC: 24.9 mg EP/L

(6.8 mg a.i./L)

(yield and cell density)

Not applicable Acceptable 477003-15

850.1740

10-day

Estuarine/Marine 

Sediment Toxicity

BAS 650 00 F

Leptocheirus 

plumulosus

EC50: >70 mg a.i./kg sediment

NOAEC: 5.2 mg a.i./kg 

sediment

EC50: >0.500 mg a.i./L pore 

water

NOAEC: 0.178 mg a.i./L pore 

water

(survival)

Not applicable Supplemental 477001-81

Non-guideline

Chronic Sediment 

Toxicity

BAS 650 00 F

Freshwater 

midge

(Chironomus 

riparius)

NOAEC: 221.59 mg a.i./kg 

dw sediment

NOAEC: 0.242 mg a.i./L pore 

water

Not applicable Supplemental 477001-82
37

Table 4.1. Toxic Effects in Aquatic Organisms Exposed to Ametoctradin

Study Type & 

Purity or Product Species Toxicity Value Toxicity Classification+

Study 

Classification MRID #

*Denotes value used for RQ calculation.

+Toxicity classifications are unknown due to the low solubility of ametoctradin under test conditions; the chemical was not 

tested up to levels that are meaningful for acute toxicity classifications (i.e., >100 mg/L = practically non-toxic, >10 to 100 

mg/L = slightly toxic, >1 to 10 mg/L = moderately toxic, 0.1 to 1 mg/L = highly toxic, <0.1 mg/L = very highly toxic).

^BAS 650 00 F contains ametoctradin only (19.2%); BAS 651 00 F contains ametoctradin (~27%) and dimethomorph (~20%).

4.2 Terrestrial Effects Summary

Seventeen studies were submitted that evaluated the effects of ametoctradin to terrestrial nontarget organisms. For the most part, ametoctradin was practically non-toxic to birds, mammals, 

invertebrates, and plants. 

4.2.1 Toxic Effects on Birds

Toxicity studies with ametoctradin were performed with bobwhite quail (Colinus virginianus), 

mallard duck (Anas platyrhynchus), and zebra finch (Taeniopygia guttata). An acute toxicity 

study was also conducted with the end-use product (EP) BAS 651 00 F. An overview of avian

toxicity data is given in Table 4.2.

Acute and short-term dietary toxicity 

The acute effects of the active ingredient ametoctradin on birds was studied in single-dose oral 

(gavage) tests with bobwhite quail, mallard duck and zebra finch at nominal concentrations up to 

2000 mg a.i./kg bw. No mortality, clinical signs of toxicity or treatment related effects were 

observed during the study with any of the bird species (acute LD50 and NOAEL were >2000 and 

2000 mg a.i./kg bw, respectively). The EP BAS 651 00 F was similarly not acutely toxic to 

bobwhite quail (oral LD50 value >2000 mg/kg bw). 

The short-term dietary toxicity of ametoctradin was studied in 5-day dietary exposure studies 

with bobwhite quail and mallard duck at nominal concentrations up to 5000 mg a.i./kg diet. No 

treatment-related mortality was observed during the study with either bird species (LC50 >5000 

mg a.i./kg diet). The NOAEC for bobwhite quail was 5000 mg a.i./kg diet based on mortality and 

sublethal effects. Mallard ducks however, exhibited a statistically significant decrease in body 

weight (15%) at the highest dose (5000 mg a.i./kg diet) compared to controls at the end of the 3-

day recovery period. This was considered to be treatment-related, and the NOAEC was set to the 

next lowest concentration of 2000 mg a.i./kg diet.

Sub-chronic and reproduction toxicity

The reproductive effects of ametoctradin on birds was studied in 21-week dietary dose-response 

studies with bobwhite quail and mallard duck at concentrations up to 1400 mg a.i./kg diet. For 

bobwhite quail, there were no significant treatment-related effects on reproduction or any adult 

parameter. A statistically significant reduction in two reproductive parameters at the mid dose

was determined not to be dose-related as no comparable effect was observed at the high dose. 

Therefore, the NOAEC was 1400 mg a.i./kg diet. For mallard duck, a higher than usual egg 

production at the start of the egg-laying period in the control group led to an apparent statistically 

significant reduction in some reproduction parameters; however, these were deemed not be 
38

treatment-related. Within the test substance groups, no dose-related trend was observed, and 

mean female fecundity for all test groups were within the data range of historical control groups 

of 11 studies. As there were no treatment-related effects on any reproductive parameter at all 

dose levels and no adverse effects on the parental generation, the NOAEC was 1400 mg a.i./kg 

diet. 

Table 4.2. Toxic Effects in Birds Due to Exposure to Ametoctradin

Study Type & 

Purity or Product Species Toxicity Value(Endpoints)

Toxicity 

Classification

Study 

Classification MRID #

Toxicity of Technical Grade Active Ingredient

850.2100

Oral Toxicity

99.3%

Bobwhite Quail 

(Colinus 

virginianus)

LD50: >2000 mg a.i./kg-bw

NOAEL: 2000 mg a.i./kg-bw 

(no effects)

Practically 

Non-toxic Acceptable 477001-48

850.2100

Oral Toxicity

99.3%

Mallard Duck

(Anas 

platyrhynchos)

LD50: >2000 mg a.i./kg-bw

NOAEL: 2000 mg a.i./kg-bw 

(no effects)

Practically 

Non-toxic Acceptable 477001-49

850.2100

Oral Toxicity

99.3%

Zebra Finch

(Taeniopygia 

guttata)

LD50: >2000 mg a.i./kg-bw

NOAEL: 2000 mg a.i./kg-bw 

(no effects)

Practically 

Non-toxic Acceptable 477001-50

850.2200

Dietary Toxicity

99.5%

Bobwhite Quail 

(Colinus 

virginianus)

LC50: >5000 mg a.i./kg-diet

NOAEC: 5000 mg a.i./kg-diet

(no effects)

Practically 

Non-toxic Acceptable 477001-51

850.2200

Dietary Toxicity

99.5%

Mallard Duck

(Anas 

platyrhynchos)

LC50: >5000 mg a.i./kg-diet

NOAEC: 2000 mg a.i./kg-diet

(decreased body weight)

Practically

Non-toxic Acceptable 477001-52

850.2300

Chronic Toxicity

99.9%

Bobwhite Quail 

(Colinus 

virginianus)

LC50: >1400 mg a.i./kg-diet

NOAEC: 1400 mg a.i./kg-diet

(no effects)

Not applicable Acceptable 477001-53

850.2300

Chronic Toxicity

99.3%

Mallard Duck

(Anas 

platyrhynchos)

LC50: >1400 mg a.i./kg-diet

NOAEC: 1400 mg a.i./kg-diet

(no effects)

Not applicable Acceptable 477001-54

Toxicity of End-use Product^

850.2100

Oral Toxicity

BAS 651 00 F

Bobwhite Quail

(Colinus 

virginianus)

LD50: >2000 mg EP/kg-bw

(>545 mg a.i./kg-bw)

NOAEL: 2000 mg EP/kg-bw

(545 mg a.i./kg-bw)

(no effects)

Not applicable Acceptable 477003-14

^BAS 650 00 F contains ametoctradin only (19.2%); BAS 651 00 F contains ametoctradin (~27%) and dimethomorph 

(~20%).

4.2.2 Toxic Effects on Mammals

The toxicity of ametoctradin was reviewed in Ametoctradin Vol. 3 Annex B.6. Ametoctradin

was not acutely toxic to rats, with an acute oral LD50 value of >2000 mg a.i./kg bw (OECD 

Annex IIA 5.2.1/01). Ametoctradin is not a reproductive toxicant in rats, as there was no 

evidence of a treatment related effect on reproduction or development at the highest 

concentration tested in submitted studies (NOAEL = 939 mg a.i./kg bw/day; OECD Annex IIA 

5.6/01). 

Results of the two relevant mammalian toxicity studies are summarized in Table 4.3. 
39

4.2.3 Toxic Effects on Invertebrates

The results from both the acute oral and contact honey bee toxicity tests are summarized in 

Table 4.4. Based on the lack of effects observed in the acute contact and acute oral honey bee 

studies, no additional honey bee studies (foliage residue or field) are needed at this time.

Table 4.4. Toxic Effects in Honey Bees (Apis mellifera) Due to Acute Exposure to Ametoctradin

Study Type & Purity 

or Product Toxicity Value Toxicity Classification

Study 

Classification MRID #

Toxicity of Technical Grade Active Ingredient

850.3020

99.3%

Oral LD50 > 111.5 μg a.i./bee

NOAEL = 111.5 μg a.i./bee

Contact LD50 > 100 μg a.i./bee

NOAEL = 100 μg a.i./bee

Practically Nontoxic Acceptable 477001-83

Toxicity of End-use Product^

850.3020

BAS 650 00 F

Oral LD50 > 568.9 μg EP/bee

(> 109.3 μg a.i./bee)

NOAEL = 568.9 μg EP/bee

(109.3 μg a.i./bee)

Contact LD50 > 520.5 μg EP/bee

(> 100 μg a.i./bee)

NOAEL = 520.5 μg EP/bee

(100 μg a.i./bee)

Practically Nontoxic Acceptable 477748-11

830.3020

BAS 651 00 F

Oral LD50 > 282.2 μg EP/bee

(> 67.6 μg a.i./bee)

NOAEL = 282.2 μg EP/bee

(67.6 μg a.i./bee)

Contact LD50 > 211.81 μg EP/bee

(> 57.7 μg a.i./bee)

NOAEL = 211.81 μg EP/bee

(57.7 μg a.i./bee)

Practically Nontoxic Acceptable 477003-18

The Agency does not have a data requirement or a guideline for an acute oral toxicity test. The oral studies would normally 

be classified as supplemental; however, they were submitted in the same study as the acute contact toxicity test, which was 

classified as acceptable. 

^BAS 650 00 F contains ametoctradin only (19.2%); BAS 651 00 F contains ametoctradin (~27%) and dimethomorph 

(~20%).

Table 4.3. Toxic Effects in Mammals Due to Exposure to Ametoctradin (TGAI)

Study Type Species Toxicity Value

(Endpoints)

Toxicity 

Classification

Study 

Classification MRID #

870.1100

Mammalian Acute 

Oral

Laboratory rat LD50: >2000 mg a.i./kg bw

EFED defers 

to the 

Registration 

Division

EFED defers 

to the 

Registration 

Division

477000-42

870.3800

Mammalian TwoGeneration 

Reproduction 

Laboratory rat NOAEL = 939 mg a.i./kg bw

(no effects)

EFED defers 

to the Health 

Effects 

Division

EFED defers 

to the Health 

Effects 

Division

477000-66

Formal reviews of mammalian data were conducted by the Registration Division and the Health Effects Division.
40

4.2.4 Toxic Effects on Plants

The toxicity of the EPs BAS 650 00 F (204.4 g/L ametoctradin) and BAS 651 00 F (300 g/L 

ametoctradin and 225 g/L BAS 550 F [dimethomorph]) to non-target plants was determined with 

vegetative vigor and seedling emergence assays using standard crop species. Plants were 

exposed to a single spray application at a rate of 2.8 L EP/ha (BAS 650 00 F) or 5.0 L EP/ha 

(BAS 651 00 F). These rates are higher than the proposed maximum single application rates. 

No significant adverse effects (i.e., >25% effect) were observed in any plant species in either the 

vegetative vigor or seedling emergence assays with either BAS 650 00 F or BAS 651 00 F. 

The results of these two studies are summarized in Table 4.5. 

Table 4.5. Non-target Terrestrial Plant Seedling Emergence and Vegetative Vigor Toxicity 

Data for Ametoctradin

Organism Exposure Test Substance Endpoint Value* Reference

Toxicity of End-use Product^

Sunflower (Helianthus 

annuus), oilseed rape 

(Brassica napus), sugar 

beet (Beta vulgaris), 

soybean (Glycine max), 

pea (Pisum sativum), 

tomato (Lycopersicon 

esculentum), onion 

(Allium cepa), oat 

(Avena sativa), barley 

(Hordeum vulgare), corn 

(Zea mays)

Vegetative 

vigor (21 

days 

observation)

BAS 650 00 F EC25 > 0.51 lb a.i./acre

NOAEC = 0.51 lb a.i./acre

(no effects)

MRID 477002-05

Acceptable

(Limit test at single 

application rate)

Seedling 

emergence 

(21 days 

observation) 

BAS 650 00 F EC25 > 0.51 lb a.i./acre

NOAEC = 0.51 lb a.i./acre

(no effects)

MRID 477002-06

Acceptable

(Limit test at single 

application rate)

Oilseed rape (Brassica 

napus), carrot (Daucus 

carota), soybean

(Glycine max), cabbage 

(Brassica oleracea), 

tomato (Lycopersicon 

esculentum), lettuce 

(Lactuca sativa), 

ryegrass (Lolium 

perenne), wheat 

(Triticum aestivum), 

onion (Allium cepa), 

corn (Zea mays)

Vegetative 

vigor (21 

days 

observation)

BAS 651 00 F EC25 > 1.34 lb a.i./acre

NOAEC = 1.34 lb a.i./acre 

(no effects)

MRID 477003-28

Acceptable

(NOAEC at highest 

test rate)

Seedling 

emergence 

(21 days 

observation) 

BAS 651 00 F EC25 > 1.34 lb a.i./acre

NOAEC = 1.34 lb a.i./acre 

(no effects)

MRID 477003-29

Acceptable

(NOAEC at highest 

test rate)

^BAS 650 00 F contains ametoctradin only ( ~19.2%) ; BAS 651 00 F contains ametoctradin (~27%) and 

dimethomorph (~20%).

5 Risk Characterization

Risk characterization is the integration of exposure and effects characterization to determine the 

potential for ecological risks to non-target organisms including aquatic life, wildlife, and plants 

from the use of ametoctradin according to the proposed labels. The risk characterization provides 

an estimation and description of the risk; articulates risk assessment assumptions, limitations, 
41

and uncertainties; synthesizes an overall conclusion; and provides the risk managers with 

information to make regulatory decisions.

5.1 Risk Estimation: Integration of Exposure and Effects Data

Results of the exposure and toxicity effects data are used to evaluate the potential for adverse 

ecological effects on non-target species. For the assessment of potential risks of ametoctradin

(technical grade active ingredient), the risk quotient (RQ) method is used to compare exposure 

and measured acute or chronic toxicity values:

RQ = EEC / Toxicity Value

where the EEC is the estimated environmental concentration generated by the exposure 

scenarios. The RQs are compared to the Agency’s levels of concern (LOCs). These LOCs are the 

Agency’s interpretive policy and are used to analyze potential risk to non-target organisms and 

the need to consider regulatory action (see Appendix E). These criteria are used to indicate when 

a pesticide’s use as directed on the label has the potential to cause adverse effects on non-target 

organisms. 

5.1.1 Non-target Aquatic Fish, Invertebrates, and Plants

Tier I GENEEC peak EECs were compared to definitive acute toxicity endpoints to derive acute 

risk quotients. The 21-day EECs were compared to chronic toxicity endpoints (NOAEC values) 

to derive chronic risk quotients for invertebrates. The 60-day EECs were compared to chronic 

toxicity endpoints (NOAEC values) to derive chronic risk quotients for fish. When an LOC 

exceedance occurred using the Tier I GENEEC EEC, the risk estimation was recalculated using 

the more refined Tier II PRZM/EXAMS EEC. The following risk estimations apply to technical 

grade active ingredient toxicity endpoints. 

Freshwater and Estuarine/Marine Fish

For the technical grade active ingredient, a median lethal concentration was not observed at the 

highest concentrations tested (64.6 – 129 μg a.i./L), which were also the functional solubility 

limits, for freshwater and estuarine/marine fish. The non-definitive LC50s exceed the highest Tier 

I peak EEC of 5.24 μg a.i./L (aerial application to grapes). Although mortality and sublethal 

effects (tottering) were noted in the rainbow trout study (NOAEC = 36.6 μg a.i./L; MRID 

477001-55) and the highest concentration tested was not 20 times greater than the EEC (64.6 μg 

a.i./L compared to 5.24 μg a.i./L), it would be impractical to repeat the test because

concentrations cannot exceed the functional solubility limit. Therefore, acute risk quotients were 

not calculated, and RQs would not be expected to exceed LOCs for non-listed species; the same 

holds true for listed species, although there is some uncertainty regarding this due to the lack of a 

20x factor. The NOAEC observed in the early life stage freshwater fish study was 48 μg a.i./L

(based on survival; MRID 477001-64). The Tier I 60-day EEC for aerial application to grapes 

was used to calculate the RQ. The chronic RQ for freshwater fish is calculated as follows:

RQ = 60-day EEC/NOAEC = 0.48 μg a.i./L / 48 μg a.i./L = 0.01
42

Therefore, the chronic RQ does not exceed the LOC (1.0). A chronic estuarine/marine fish study 

was not submitted; therefore, an RQ was not calculated. 

Freshwater and Estuarine/Marine Invertebrates

For the technical grade active ingredient, neither a median lethal concentration nor sublethal 

effects were observed at the highest concentrations tested (94 – 155 μg a.i./L), which were also 

the functional solubility limits, for freshwater and estuarine/marine invertebrates. Therefore, 

acute risk quotients were not calculated, and RQs would not be expected to exceed LOCs for 

non-listed and listed species, as the highest Tier I peak EEC for grapes (aerial application) was 

5.24 μg a.i./L. The NOAEC observed in the life cycle freshwater invertebrate study was 44 μg 

a.i./L based on reproduction and length. The Tier I 21-day EEC for aerial application to grapes 

was used to calculate the RQ. The chronic RQ for freshwater invertebrates is calculated as 

follows:

RQ = 21-day EEC/NOAEC = 1.36 μg a.i./L / 44 μg a.i./L = 0.03

Therefore, the chronic RQ does not exceed the LOC (1.0). A chronic estuarine/marine 

invertebrate study was not submitted; therefore an RQ was not calculated. 

An EC50 was not established in the Eastern oyster shell deposition toxicity test; however, a 

NOAEC of 37 μg a.i./L was observed based on reduction in shell deposition. The peak EEC for 

aerial application to grapes was 5.24 μg a.i./L, which is not 20 times less than the highest

concentration tested (94 μg a.i./L). However, the test was conducted at the functional solubility 

limit; therefore, it would be impractical to repeat the test because concentrations cannot exceed 

the functional solubility limit. Acute risk quotients were not calculated, and RQs would not be 

expected to exceed LOCs for non-listed species; the same holds true for listed species, although 

there is some uncertainty regarding this due to the lack of a 20x factor. For the use that resulted 

in the lowest peak EEC, the highest concentration tested was greater than 20 times the peak EEC 

(hops; 4.16 μg/L). 

Aquatic Plants

The EC50 for vascular aquatic plants was 132 μg a.i./L, and the NOAEC was 13 μg a.i./L. The 

acute RQ for non-listed vascular aquatic plants is calculated as follows:

RQ = Peak EEC/EC50 = 5.24 μg a.i./L / 132 μg a.i./L = 0.04

The acute RQ does not exceed the LOC (1.0) for non-listed species. For potential risks to listed 

species, the NOAEC should be used as the toxicity value. The acute RQ for listed vascular plants 

is calculated as follows:

RQ = Peak EEC/NOAEC = 5.24 μg a.i./L / 13 μg a.i./L = 0.40

The acute RQ does not exceed the LOC (1.0) for listed species.
43

Of the four non-vascular plant studies submitted, the freshwater diatom produced the lowest 

EC50 at 7.8 μg a.i./L, and the NOAEC was 1.4 μg a.i./L. The acute RQ for non-listed nonvascular aquatic plants is calculated as follows:

RQ = Peak EEC/EC50 = 5.24 μg a.i./L / 7.8 μg a.i./L = 0.67

Therefore, the acute RQ does not exceed the LOC (1.0) for non-listed species. For potential risks 

to listed species, the NOAEC should be used as the toxicity value. The acute RQ for listed nonvascular plants is calculated as follows:

RQ = Peak EEC/NOAEC = 5.24 μg a.i./L / 1.4 μg a.i./L = 3.74

Therefore, the acute RQ exceeds the LOC (1.0), and the risk quotient must be refined using Tier 

II PRZM/EXAMS generated EECs. Refined acute RQs for listed non-vascular aquatic plants are 

located in Table 5.1. 

Table 5.1. Listed Non-vascular Aquatic Plant RQs Based on Tier II PRZM/EXAMS 

EECs for the Proposed Uses

PRZM/EXAMS 

Scenario Method

Application Rate

(Interval between 

Applications) 

Peak 

EEC

(μg/L)

RQ

FL Cabbage

Aerial 3 apps @ 0.274 lb/A

(7 days)

1.23 0.88

Ground 0.80 0.57

GA Onion

Aerial

3 apps @ 0.274 lb/A

(5 days)

1.76 1.26*

Ground 0.95 0.68

FL Cucumber

Aerial 2.43 1.74*

Ground 1.87 1.34*

FL Pepper

Aerial 3.17 2.26*

Ground 2.81 2.01*

FL Tomato

Aerial 3.17 2.26*

Ground 3.28 2.34*

PA Tomato

Aerial 2.61 1.86*

Ground 2.40 1.71*

CA Lettuce

Aerial 1.06 0.76

Ground 0.36 0.26

FL Carrot

Aerial 1.40 1.00*

Ground 0.82 0.59

ID Potato

Aerial 1.06 0.76

Ground 0.38 0.27

ME Potato

Aerial 2.10 1.50*

Ground 1.40 1.00*

CA Grape Aerial

4 apps @ 0.274 lb/A

(7 days)

0.82 0.59

Ground 0.16 0.11

NY Grape Aerial 3.11 2.22*

Ground 3.02 2.16*

OR Hops Aerial 3 apps @ 0.274 lb/A

(10 days)

0.83 0.59

Ground 0.52 0.37
44

Table 5.1. Listed Non-vascular Aquatic Plant RQs Based on Tier II PRZM/EXAMS 

EECs for the Proposed Uses

PRZM/EXAMS 

Scenario Method

Application Rate

(Interval between 

Applications) 

Peak 

EEC

(μg/L)

RQ

MI Nursery Ground 4 apps @ 0.274 lb/A

(10 days)

0.40 0.29

FL Nursery Ground 0.69 0.49

FL Turf Ground

4 apps @ 0.274 lb/A

(10 days)

0.46 0.33

PA Turf Ground 0.35 0.25

CA Residential Ground 0.22 0.16

RQ based on NOAEC of 1.4 μg a.i./L for freshwater diatom.

*Exceeds listed species LOC (1.0).

The refined acute RQs still exceed the LOC (1.0) for listed species for the following 

PRZM/EXAMS scenarios: FL Tomato (ground application), GA Onion (aerial), FL Cucumber 

(ground and aerial), FL Pepper (ground and aerial), FL Tomato (ground and aerial), PA Tomato 

(ground and aerial), FL Carrot (aerial), ME Potato (ground and aerial), and NY Grape (ground 

and aerial). 

RQs did not exceed LOCs for the following PRZM/EXAMS scenarios: FL Cabbage (ground and 

aerial), GA Onion (ground), CA Lettuce (ground and aerial), FL Carrot (ground), ID Potato 

(ground and aerial), CA Grape (ground and aerial), OR Hops (ground and aerial), MI Nursery 

(ground), FL Nursery (ground), FL Turf (ground), PA Turf (ground), CA Residential (ground). 

Benthic Invertebrates

Because ametoctradin tends to adsorb strongly to soil and sediment, sediment toxicity tests are 

required under 40 CFR Part 158 for the technical grade active ingredient. However, studies were 

submitted for formulated products. Useful information can still be gained from these tests, as 

recovery rates in the spiked sediment were high, even though the solubility of the formulated 

product was much greater than the technical grade active ingredient. For the 10-day 

estuarine/marine sediment toxicity test, median effects concentrations were not observed at the 

highest concentration tested; therefore, RQs were not calculated. A statistically significant 

reduction in survival (81%) was observed at the middle test concentration (13 mg a.i./kg 

sediment; 0.208 mg a.i./L pore water); at the highest test concentration (70 mg a.i./kg sediment; 

0.500 mg a.i./L pore water), survival was 78%. Therefore, the NOAEC based on survival was 5.2 

mg a.i./kg sediment or 0.178 mg a.i./L pore water (MRID 477001-81). Although the EC50/LC50s 

were non-definitive and mortality was observed in the study, the highest concentration tested was 

580 times (based on sediment concentration) to 649 times (based on pore water concentration) 

greater than the maximum EECs; therefore, RQs would not be expected to exceed LOCs.

For the chronic freshwater sediment toxicity study, treatment-related statistically significant 

adverse effects on emergence rate were recorded at the two highest test concentrations and on 

development rate at the highest test concentration only. The NOAEC for emergence rate 221.59 

mg a.i./kg dry sediment or 0.242 mg a.i./L pore water. Chronic RQs are calculated as follows:

RQ = 21-day Sediment EEC/NOAEC = 112.68 μg/kg / 1000 μg/mg / 221.59 mg/kg = <0.01
45

RQ = 21-day Pore Water EEC/NOAEC = 0.72 μg/L / 1000 μg/mg / 0.242 mg/L = <0.01

Neither of the RQs exceed the chronic LOC (1.0) for risks to benthic invertebrates.

5.1.2 Non-target Terrestrial Animals

Birds

For the technical grade active ingredient, no mortality or effects were observed in the bobwhite 

quail, mallard duck, and zebra finch acute oral toxicity tests (LD50 > 2000 mg a.i./kg-bw; 

NOAEL = 2000 mg a.i./kg-bw) and the bobwhite quail dietary toxicity test (LC50 > 5000 mg 

a.i./kg-diet; NOAEC = 5000 mg a.i./kg-bw). In the mallard duck dietary toxicity study, no 

mortalities were observed, but decreased body weight was observed at the highest concentration 

tested (LC50 > 5000 mg a.i./kg-diet; NOAEC = 2000 mg a.i./kg-diet). Acute risk quotients for 

birds were not calculated because LD/LC50s were greater than EECs, and RQs would not be 

expected to exceed LOCs for listed and non-listed species, as the highest concentration tested 

(5000 mg a.i./kg-diet) in the dietary study that produced a sublethal effect was greater than 10 

times the highest dietary EEC (216.23 mg/kg-food item). 

No effects were observed in the submitted avian reproduction studies (LC50 > 1400 mg a.i./kgdiet; NOAEC = 1400 mg a.i./kg-diet for both bobwhite quail and mallard duck). Chronic dietary 

RQs were calculated for the scenario that produced the highest dietary EECs (grapes – 4 

applications @ 0.274 lb a.i./acre, 7-day interval; Table 3.7) and are located in Table 5.2. None 

of the chronic RQs exceeded the LOC (1.0).

Table 5.2 Avian Chronic Dietary RQs as a Result of the Proposed 

Application of Ametoctradin on Grapes

Food Item RQ

Short grass 0.15

Tall grass 0.07

Broadleaf plants/small insects 0.09

Fruits/pods/seeds/large insects 0.01

Mammals

No morality or signs of sublethal effects were observed in the acute oral rat study submitted for 

the technical grade active ingredient. Therefore, acute risk quotients were not calculated, and 

RQs would not be expected to exceed LOCs.

No effects were observed in the submitted two-generation rat reproduction study; the NOAEL 

was 939 mg a.i./kg-bw. Chronic RQs were calculated for the scenario that produced the highest 

EECs (grapes – 4 applications @ 0.274 lb a.i./acre, 7-day interval; Table 3.8) and are located in 

Table 5.3 and 5.4. None of the chronic RQs exceeded the LOC (1.0).
46

Table 5.3 Mammalian Chronic Dose-based RQs as a Result of the Proposed Application of 

Ametoctradin on Grapes

Food Item RQ

Small Mammal (15 g) Medium Mammal (35 g) Large Mammal (1000 g)

Short grass 0.10 0.09 0.05

Tall grass 0.05 0.04 0.02

Broadleaf plants/small insects 0.06 0.05 0.03

Fruits/pods/large insects 0.01 0.01 <0.01

Seeds (granivore) <0.01 <0.01 <0.01

Table 5.4 Mammalian Chronic Dietary-based RQs as a Result of the 

Proposed Application of Ametoctradin on Grapes

Food Item RQ

Short grass 0.01

Tall grass 0.01

Broadleaf plants/small insects 0.01

Fruits/pods/seeds/large insects <0.01

Terrestrial Invertebrates

EFED does not currently quantify risks to non-listed terrestrial non-target insects. Risk quotients 

are not calculated for these organisms. The honey bee is used as a surrogate for all terrestrial 

invertebrates. For the technical grade active ingredient, ametoctradin is classified as practically 

non-toxic based on the acute contact honey bee study (LD50 >100 μg a.i./bee). Similarly, the 

acute oral study resulted in a non-definitive LD50 (>111.5 μg a.i./bee). 

5.1.3 Terrestrial and Semi-aquatic Plants

Terrestrial and semi-aquatic plants may be exposed to pesticides from runoff and spray drift. 

Semi-aquatic plants are those that inhabit low-lying wet areas that may be dry at certain times of 

the year. EECs for terrestrial and semi-aquatic plants are derived for areas adjacent to the 

treatment site. Acute RQs for terrestrial plants are derived by dividing the EEC by the EC25 from 

seedling emergence and vegetative vigor toxicity tests. Acute RQs for listed plant species are 

calculated by dividing the EEC by the NOAEC (if not available, an EC05 is used) value from 

toxicity tests.

Terrestrial plant EECs and toxicity endpoints are provided in Tables 3.9 and 4.5, respectively. 

Because no effects were noted in the studies using the end-use product with ametoctradin only, 

RQs were not calculated for non-listed species. For listed species, the NOAEC of 0.51 lb a.i./acre 

(note: this application rate is greater than the maximum single application rate), was used to 

calculate RQs using TerrPlant v1.2.2 (Appendix D) and RQs are summarized in Table 5.5. 

None of the RQs exceeded the LOC for listed species. 
47

Table 5.5. Risk quotient (RQ) values for plants in dry and semi-aquatic areas 

exposed to ametoctradin through runoff and/or spray drift

Listed Status Dry Semi-Aquatic Spray Drift

All uses – aerial 

application (spray)

0.274 lb a.i./acre

Monocot Listed <0.1 <0.1 <0.1

Dicot Listed <0.1 <0.1 <0.1

5.2 Risk Description

A screening-level (Level I) risk assessment, based on the proposed uses of ametoctradin, 

produced RQs that exceeded LOCs for listed aquatic non-vascular plants based on use of the 

conservative Tier I GENEEC screening model, as well as the refined EECs produced by the Tier 

II PRZM/EXAMS model. The risk description will detail whether or not risks to a given taxa are 

likely based on the results of risk estimation and additional lines of qualitative evidence.

5.2.1 Risks of Ametoctradin to Aquatic Organisms

Fish

Mortality (10%) and sublethal effects (tottering, 20%) were reported at the highest concentration 

tested in the acute rainbow trout study (NOAEC = 36.6 μg a.i./L; MRID 477001-55). Since the 

functional solubility limit in this test was about half of the laboratory tested solubility, there are 

inherent uncertainties as to whether effects would be seen in the environment if the functional 

solubility were to increase, but these uncertainties are unlikely to be resolved by repeating the 

study to develop a definitive LC50 endpoint. However, given that three other species of 

freshwater fish were tested and one species of estuarine/marine fish was tested and no effects 

were seen in any of these studies at concentrations closer to the laboratory tested solubility limit, 

acute risks to freshwater and estuarine/marine fish are unlikely. 

For chronic effects to freshwater fish (fathead minnow), 100% mortality was observed at the 

highest concentration tested (NOAEC = 48 μg a.i./L; MRID 477001-64). However, the 60-day 

EEC was two orders of magnitude lower than the NOAEC, and the RQ did not exceed the LOC. 

Data for chronic effects of ametoctradin on estuarine/marine fish were not submitted, and the 

acute-to-chronic ratio cannot be used to predict potential chronic risks to estuarine/marine fish 

because the acute freshwater and estuarine/marine fish studies produced non-definitive LC50s. 

However, since there was no significant difference in acute effects on freshwater fish compared 

to estuarine/marine fish, an estuarine/marine medium is not likely to increase the toxicity of 

ametoctradin. If ametoctradin’s chronic toxicity to estuarine/marine fish is within two orders of 

magnitude of the toxicity of ametoctradin to freshwater fish, then RQs will not exceed the LOC.

Therefore, chronic risks to both freshwater and estuarine/marine fish are unlikely at the proposed 

application rates. 

Invertebrates

Acute risks to freshwater and estuarine/marine invertebrates are unlikely due to lack of mortality 

or sublethal effects in either the daphnid or mysid shrimp studies. For acute effects to 

estuarine/marine mollusks, there was a 36% reduction in shell growth at the highest 

concentration tested (NOAEC = 37 μg a.i./L; MRID 477001-61). An RQ was not calculated due 
48

to the lack of an EC50. Since the functional solubility limit (97 μg a.i./L) in this test was lower 

than the laboratory tested solubility limit (150 μg a.i./L), there are inherent uncertainties as to 

whether effects would be seen in the environment if the functional solubility were to increase, 

but these uncertainties are unlikely to be resolved by repeating the study to obtain a definitive 

EC50. Therefore, acute risks to estuarine/marine mollusks are unlikely.

For chronic effects to freshwater invertebrates, reduced reproduction and length were observed at 

the second lowest test concentration (NOAEC = 44 μg a.i./L; MRID 477001-71). However, the

21-day EEC was more than an order of magnitude lower than the NOAEC, and the RQ did not 

exceed the LOC. Data for chronic effects of ametoctradin on estuarine/marine invertebrates were 

not submitted, and the acute-to-chronic ratio cannot be used to predict potential chronic risks to 

estuarine/marine invertebrates because the acute freshwater and estuarine/marine invertebrate 

studies produced non-definitive EC50s (i.e., no effects were observed). However, since there was 

no significant difference in acute effects on freshwater invertebrates compared to 

estuarine/marine invertebrates, an estuarine/marine medium is not likely to increase the toxicity 

of ametoctradin. If ametoctradin’s chronic toxicity to estuarine/marine invertebrates is within an 

order of magnitude of the toxicity of ametoctradin to freshwater invertebrates, then RQs will not

exceed the LOC. Therefore, chronic risks to both freshwater and estuarine/marine invertebrates 

are unlikely at the proposed application rates. 

Plants

For vascular aquatic plants, the EC50 was calculated to be 132 μg a.i./L, with significant 

reductions in dry weight occurring at the second lowest concentration tested (NOAEC = 13 μg 

a.i./L; MRID 477001-80). RQs did not exceed LOCs for listed and non-listed species. Therefore, 

acute risks to non-listed and listed vascular plants are unlikely at the proposed application rates. 

For non-vascular aquatic plants, the EC50 for the freshwater diatom was calculated to be 7.8 μg 

a.i./L, with significant reductions in growth rate, yield, and cell density occurring at the second 

lowest concentration tested (NOAEC = 1.4 μg a.i./L; MRID 477001-78). The highest refined 

peak EEC (3.28 μg a.i./L, ground application to FL Tomato; Table 3.5) was greater than the 

NOAEC, and the RQ for listed aquatic non-vascular plants exceeded the LOC based on the Tier 

II PRZM/EXAMS EEC. Therefore, there is potential for acute risks to listed non-vascular 

aquatic plants for the following uses: bulb vegetables, cucurbit vegetables, fruiting vegetables, 

tuberous and corm vegetables, and grapes. Risks to listed non-vascular aquatic plants are 

unlikely for the following uses: Brassica leafy vegetables, leafy vegetables, hops, nursery, turf, 

and residential uses. 

Benthic Invertebrates

While there were mortalities in the 10-day estuarine/marine sediment toxicity test, the 

EC50/LC50s were non-definitive, and the highest concentration tested was several hundred times 

greater than the EECs. Therefore, acute risks to estuarine/marine benthic invertebrates are 

unlikely. Similarly, chronic RQs for freshwater benthic invertebrates did not exceed LOCs, and 

chronic risks to freshwater benthic invertebrates are unlikely. It should be noted that reproductive 

endpoints were not measured in the test, but the effects observed in the chronic daphnid study 

occurred at much higher concentrations than predicted EECs. The chronic daphnid NOAEC (44 
49

μg a.i./L) is more than 60 times greater than the maximum 21-day pore water EEC (0.72 μg 

a.i./L).

There is some uncertainty associated with the use of a formulated product rather than the 

technical grade active ingredient for both the 10-day and the chronic studies. However, due to 

the high recovery of ametoctradin in sediment, a study with the technical grade active ingredient 

is unlikely to change the risk call. Additionally, while 10-day freshwater sediment toxicity study 

and chronic estuarine/marine sediment toxicity studies are data gaps according to 40 CFR Part 

158 data requirements, submission of these studies is unlikely to add value to this risk 

assessment because it is unlikely that EC50/LC50/NOAECs will exceed EECs since differential 

toxicity between media types has not been observed in other taxa. 

5.2.2 Risks of Ametoctradin to Terrestrial Organisms

Birds and Mammals

There were no mortalities or sublethal effects in the acute oral bobwhite quail, mallard, or zebra 

finch studies or the bobwhite quail subacute dietary toxicity test. However, reduced body weight 

was observed at the highest concentration tested in the mallard duck subacute dietary toxicity test 

(NOAEC = 2000 mg a.i./kg diet; MRID 477001-52). Because there were no mallard duck 

mortalities reported and the highest concentration tested was greater than 10 times the EEC 

(5000 mg a.i./kg diet compared to the highest dietary EEC – 216.23 mg a.i./kg; Table 3.7), acute 

risks to birds are unlikely due to use of ametoctradin at the proposed application rates. 

No effects were observed in the chronic avian reproduction studies, and RQs did not exceed 

LOCs (Table 5.1). Therefore, chronic risks to birds are unlikely due to the use of ametoctradin at 

the proposed application rates.

Similarly, for mammals, no mortalities or sublethal effects were observed in the acute or chronic 

studies. Acute RQs were not calculated, and chronic dietary and dose-based RQs did not exceed 

the LOC (1.0) (Table 5.2 and Table 5.3). Therefore, acute and chronic risks to mammals are 

unlikely due to the use of ametoctradin at the proposed application rates.

Terrestrial Plants

RQs were not calculated for non-listed terrestrial plant species because there were no effects in 

the submitted studies. None of the RQs for listed terrestrial plant species exceeded the LOC (1.0) 

(Table 5.4). Therefore, risks to terrestrial plants are unlikely because ametoctradin exposure at 

rates higher than the proposed maximum single application rate failed to elicit adverse effects in 

any of the submitted terrestrial plant toxicity studies (0.51 lb a.i./acre tested rate compared to the 

0.274 lb a.i./acre proposed rate).

Terrestrial Invertebrates

Acute contact and oral honey bee toxicity data did not yield definitive endpoints, and 

ametoctradin was classified as practically non-toxic to honey bees. Therefore, higher tier honey 

bee studies are not necessary at this time. There is considerable uncertainty in using the honey 
50

bee as a surrogate for all terrestrial invertebrates due to the drastic differences in life histories of 

the honey bee, a social, colonial organism, and solitary organisms. 

Several other studies were also submitted that evaluated the effects of formulated products on 

parasitic wasps, predatory mites, and green lacewings in the laboratory and the field (see 

Appendix F). Only the 48-hour acute contact toxicity study with the parasitic wasp yielded a 

definitive LR50 (median lethal rate) for the ametoctradin-only formulation (BAS 650 00 F) of 

0.21 lb a.i./acre (MRID 477748-16).

Although no acute oral or contact toxicity was observed in the honey bee studies, there is 

uncertainty as to how fungicides interact with insecticides and whether fungicides may disrupt 

the process of fermentation of pollen stores, which may have significant effects on honey bee 

nutrition and health (Alarcon et al., 2009). While EFED does not have a quantitative method for 

assessing potential risk of this nature, additional studies evaluating the effects of ametoctradin on 

honey bee health may be of value. Considering this and the toxicity data for the predatory wasp, 

an appropriate exposure reduction strategy may be to restrict applications of ametoctradin during 

bloom. 

5.3 Threatened and Endangered Species Concern

To determine whether the proposed use sites for a pesticide are geographically associated with 

known locations of listed species, a screening-level search of the LOCATES (version 2.10.3)

database should be conducted. The database compares county-level location data for listed 

species with county-level crop production data (as available in the 2002 agricultural census) to 

identify any coarse overlaps of listed species with the proposed labeled uses of ametoctradin. 

Listed species are those that are currently on the Federal list of endangered and threatened 

wildlife and plants. After refinement, the proposed use of ametoctradin on bulb vegetables, 

cucurbit vegetables, fruiting vegetables, tuberous and corm vegetables, and grapes still produced 

RQs that exceed the LOC for listed non-vascular aquatic plants. LOCATES was run to identify 

species that may be indirectly affected by the proposed uses of ametoctradin (see Appendix G).

5.3.1 Action Area

For listed species assessment purposes, the action area is considered to be the area affected 

directly or indirectly by the Federal action and not merely the immediate area involved in the 

action. At the initial screening-level, the risk assessment considers broadly described taxonomic 

groups and so conservatively assumes that listed species within those broad groups are colocated with the pesticide treatment area. This means that terrestrial plants and wildlife are 

assumed to be located on or adjacent to the treated site and aquatic organisms are assumed to be 

located in a surface water body adjacent to the treated site. The assessment also assumes that

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. This risk assessment presents the use of ametoctradin and establishes initial colocation of species with treatment areas. 

If the assumptions associated with the screening-level action area result in RQs that are below 

the listed species LOCs, a "no effect" determination conclusion is made with respect to listed 

species in that taxa, and no further refinement of the action area is necessary. Furthermore, RQs 
51

below the listed species LOCs for a given taxonomic group indicate no concern for indirect 

effects upon listed species that depend upon the taxonomic group covered by the RQ as a 

resource. 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 could be considered to determine the extent to which 

screening assumptions regarding an action area apply to a particular listed organism. These 

subsequent refinement steps could consider how this information would impact the action area 

for a particular listed organism and may potentially include areas of exposure that are downwind 

and downstream of the pesticide use site.

5.3.2 Taxonomic Groups Potentially at Risk: Direct Effects

Based on available screening level information, for the proposed uses of ametoctradin, there are 

potential direct effects on listed non-vascular aquatic plants. A summary of the risk conclusions 

and direct and indirect effects determinations is presented in Table 5.6.

Table 5.6. Potential Listed Species Risks Associated with Direct or Indirect Effects 

Due to the Proposed Applications of Ametoctradin

Listed Taxonomy Direct Effects Indirect Effects

Terrestrial and semi-aquatic plants –

monocots No No

Terrestrial and semi-aquatic plants – dicots No No

Terrestrial invertebrates No No

Birds (surrogate for terrestrial-phase 

amphibians and reptiles) No No

Mammals No No

Aquatic vascular plants No Yes*

Aquatic non-vascular plants Yes+ Yes*

Freshwater fish (surrogate for aquaticphase amphibians) No Yes*

Freshwater Invertebrates No Yes*

Freshwater Benthic Invertebrates Acute – No^

Chronic – No Yes*

Estuarine/Marine Benthic Invertebrates Acute – No

Chronic – No^ Yes*

Estuarine/Marine Fish Acute – No

Chronic – No^ Yes*

Estuarine/Marine Crustaceans Acute – No

Chronic – No^ Yes*

Estuarine/Marine Mollusks No Yes*

+No aquatic non-vascular plants have been designated as endangered or threatened; however, the potential 

for risk to these organisms exists.

*For indirect effects, all aquatic taxa have been identified due to the potential direct effects on listed nonvascular aquatic plants. However, any species identified for potential indirect effects would require an 

obligate relationship with the directly affected listed non-vascular aquatic plant. Because there are no listed 

non-vascular aquatic plants, the taxa identified for indirect effects are very conservative assumptions.

^While data were not submitted, a weight of evidence approach was used to discount potential risks to these 

taxa.
52

5.3.3 Use of Probit Slope Response Relationship to Provide Information on the 

Endangered Species Levels of Concern

The Individual Effect Chance Model (Version 1.1), developed by the Environmental Fate and 

Effects Division, is used by the Agency to calculate the chance or probability of an individual 

mortality (effect) corresponding to the listed species’ acute LOCs and calculated RQs. The 

model, which is an Excel spreadsheet tool, allows for calculations by entering the mean slope 

estimate (and the 95% confidence bounds of that estimate) as the slope parameter for the 

spreadsheet. The generated information serves as a guide to establish the need for and the extent 

of additional analysis that may be performed as well as evaluations of the geographical and 

temporal nature of the exposure to make an effect determination. 

Because screening-level acute LOCs were calculated and exceeded for only non-vascular aquatic 

plants in this assessment, probit analysis was not conducted. The endpoints of aquatic plant 

studies include growth rate, yield, and cell density rather than single mortality events. 

5.3.4 Indirect Effects Analysis

The Agency acknowledges that pesticides have the potential to exert indirect effects upon the 

listed organisms by, for example, perturbing forage or prey availability, altering the extent of 

nesting habitat, etc. In conducting a screen for indirect effects, direct effect LOCs for each 

taxonomic group are used to make inferences concerning the potential for indirect effects upon 

listed species that rely upon non-endangered organisms in these taxonomic groups as resources 

critical to their life cycle.

Based on direct effects to listed non-vascular aquatic plants, indirect effects to all aquatic taxa 

are identified (vascular plants, non-vascular plants, freshwater fish (surrogate for aquatic-phase 

amphibians), freshwater invertebrates, freshwater benthic invertebrates, estuarine/marine fish, 

estuarine/marine crustaceans, and estuarine/marine mollusks). A list of species that may be 

indirectly affected is included in Appendix G. However, any indirect effects would require an 

obligate relationship with the directly affected listed non-vascular aquatic plant. Because there 

are no listed non-vascular aquatic plants, the indirect effects identified are very conservative 

assumptions.

6 Description of Assumptions and Limitations

6.1 Assumptions and Limitations Related to Exposure for all Taxa

There are a number of areas of uncertainty in the aquatic and terrestrial risk assessments. The 

toxicity assessment for terrestrial and aquatic animals is limited by the number of species tested 

in the available toxicity studies. Use of toxicity data on representative species does not provide 

information on the potential variability in susceptibility to acute and chronic exposures. 

Additionally, the Agency does not currently study the effects of pesticides on representative 

fungi species. Fungi are important to terrestrial and aquatic ecosystems, functioning as both 

decomposers in the food web and as biocontrol agents (entomopathogenic fungi, such as 

Beauveria bassiana). The lack of risk assessment for beneficial fungi is a key uncertainty in this 

ecological risk assessment.
53

This screening-level risk assessment relies on labeled statements of the maximum rate of

ametoctradin application, the maximum number of applications, and the shortest interval 

between applications. Together, these assumptions constitute a maximum use scenario. The 

frequency at which actual uses approach these maximums is dependent on pest pressure,

resistance to the fungicide, timing of applications, and market forces. 

6.2 Assumptions and Limitations Related to Exposure for Terrestrial Species

Variation in habitat and dietary requirements

For screening terrestrial risk assessments, a generic bird or mammal is assumed to occupy either 

the treated field or adjacent areas receiving pesticide at a rate commensurate with the treatment 

rate on the field. The habitat and feeding requirements of the modeled species and the wildlife 

species may be different. It is assumed that species occupy, exclusively and permanently, the 

treated area being modeled. This assumption leads to a maximum level of exposure in the risk

assessment. 

The acute studies have a fixed exposure period, not allowing for the differences in response of 

individuals to different durations of exposure. Further, for the acute oral study, ametoctradin is 

administered in a single dose which does not mimic wild birds' exposure through multiple 

feedings. Also, it does not account for the effect of different environmental matrices on the 

absorption rate of the chemical into the animal. Because exposure occurs over several days, both 

the accumulated dose and elimination of the chemical from the body for the duration of the 

exposure determine the exact exposure to wildlife; however, they are not taken into account in 

the screening assessment. There was also no assumption of an effect of repeated doses that

change the tolerance of an individual to successive doses. 

Variation in diet composition

The risk assessment and calculated RQs assume 100% of the diet is relegated to single food 

types foraged only from treated fields. The assumption of 100% diet from a single food type 

may be realistic for acute exposures, but diets are likely to be more variable over longer periods 

of time. This assumption is likely to be conservative and will tend to overestimate potential risks 

for chronic exposure, especially for larger organisms that have larger home ranges. These large 

animals (e.g., deer and geese) will tend to forage from a variety of areas and move on and off of 

treated fields. Small animals (e.g., mice, voles, and small birds) may have home ranges smaller 

than the size of a treated field and will have little or no opportunity to obtain foodstuffs that have 

not been treated with ametoctradin. Even if their home range does cover area outside the treated 

field, ametoctradin may have run off to areas adjacent to the treated field. 

Exposure routes other than dietary

Only dietary and incidental ingestion of contaminated soils exposures are included in the 

exposure assessment. Other exposure routes are possible for animals in treated areas. These 

routes include ingestion of contaminated drinking water, dermal contact, inhalation, and 

preening. Because ametoctradin does not volatilize appreciably, inhalation does not appear to be 

a significant contributor to the overall exposure. Given ametoctradin’s low solubility in water, it 
54

is not likely that ametoctradin will be found in water above the functional solubility limit, but it 

is likely that ametoctradin will sorb to soil and/or sediment and move off-site dominantly sorbed 

to soil and/or sediment. If toxicity is expected through any of these other routes of exposure, then 

the risks of a toxic response to ametoctradin may be underestimated in this risk assessment.

Dietary Intake - The Differences between Laboratory and Field Conditions

There are several aspects of the dietary test that introduce uncertainty into calculation of the LC50

value (Mineau, et al., 1994; ECOFRAM, 1999). The endpoint of this test is reported as the 

concentration mixed with food that produces a response rather than as the dose ingested. 

Although food consumption sometimes allows for the estimate of a dose, calculations of the 

mg/kg/day are confounded by undocumented spillage of feed and how consumption is measured 

over the duration of the test. Usually, if measured at all, food consumption is estimated once at 

the end of the five-day exposure period. Further, group housing of birds undergoing testing only 

allows for a measure of the average consumption per day for a group; consumption estimates can 

be further confounded if birds die within a treatment group. The exponential growth of young 

birds also complicates the estimate of the dose; controls often nearly double in size over the 

duration of the test. Since weights are only taken at the initiation of the exposure period and at 

the end, the dose per body weight (mg/kg) is difficult to estimate with any precision. The 

interpretation of this test is also confounded because the response of birds is not only a function 

of the intrinsic toxicity of the pesticide, but also the willingness of the birds to consume treated 

food.

Further, the acute and chronic characterization of risk rely on comparisons of wildlife dietary 

residues with LC50 or NOAEC values expressed in concentrations of pesticides in laboratory 

feed. These comparisons assume that ingestion of food items in the field occurs at rates 

commensurate with those in the laboratory. Although the screening assessment process adjusts 

dry-weight estimates of food intake to reflect the increased mass in fresh-weight wildlife food 

intake estimates, it does not allow for gross energy and assimilative efficiency differences 

between wildlife food items and laboratory feed. On gross energy content alone, direct 

comparison of a laboratory dietary concentration- based effects threshold to a fresh-weight 

pesticide residue estimate would result in an underestimation of field exposure by food 

consumption by a factor of 1.25 - 2.5 for most food items. Only for seeds would the direct 

comparison of dietary threshold to residue estimate lead to an overestimate of exposure.

Differences in assimilative efficiency between laboratory and wild diets suggest that current 

screening assessment methods do not account for a potentially important aspect of food 

requirements. Depending upon species and dietary matrix, bird assimilation of wild diet energy 

ranges from 23 - 80%, and mammal's assimilation ranges from 41 - 85% (U.S. EPA, 1993). If it 

is assumed that laboratory chow is formulated to maximize assimilative efficiency (e.g., a value 

of 85%), a potential for underestimation of exposure may exist by assuming that consumption of 

food in the wild is comparable with consumption during laboratory testing. In the screening 

process, exposure may be underestimated because metabolic rates are not related to food 

consumption.

Finally, the screening procedure does not account for situations where the feeding rate may be 

above or below requirements to meet free living metabolic requirements. Gorging behavior is a 
55

possibility under some specific wildlife scenarios (e.g., bird migration) where the food intake 

rate may be greatly increased. Kirkwood (1983) has suggested that an upper-bound limit to this 

behavior might be the typical intake rate multiplied by a factor of 5. In contrast is the potential 

for avoidance, operationally defined as animals responding to the presence of noxious chemicals 

in their food by reducing consumption of treated dietary elements. This response is seen in 

nature where herbivores avoid plant secondary compounds.

In the absence of additional information, the acute oral LD50 test provides the best estimate of 

acute effects for chemicals where exposure can be considered to occur over relatively short 

feeding periods, such as the diurnal feeding peaks common to avian species (ECOFRAM, 1999).

Incidental Pesticide Releases Associated with Use

This risk assessment is based on the assumption that the entire treatment area is subject to 

ametoctradin application at the rates specified on the label. In reality, there is the potential for 

uneven application of ametoctradin through such plausible incidents as changes in calibration of 

application equipment, spillage, and localized releases at specific areas of the treated field that 

are associated with specifics of the type of application equipment used (e.g., increased 

application at turnabouts when using older application equipment).

6.3 Assumptions and Limitations Related to Exposure for Aquatic Species

The fate and transport database for ametoctradin was sufficient to conduct aquatic modeling for 

exposure assessment of aquatic species. The GENEEC model was used to produce conservative 

estimated exposure concentrations. The aquatic listed non-vascular plant RQ exceeded the LOC; 

therefore, EECs were refined using the PRZM/EXAMS model. Because ametoctradin is a new 

chemical, no monitoring data were available to compare to the model estimates.

Aquatic organisms were not tested up to 100 mg/L (see OCSPP 850.1000 guideline for details) 

due to the low solubility of ametoctradin (0.150 mg/L). Therefore, aquatic organisms were tested 

at concentrations up to the functional solubility of the chemical in laboratory test media. 

Attempts were made to create saturated solutions through the use of glass wool and saturator 

columns. For aquatic plants, suspensions were centrifuged prior to test initiation. Test solutions 

were visually confirmed to be clear and free of precipitate during the studies, and concentrations 

were generally maintained throughout the studies, as evidenced by high recovery rates. However, 

the uncertainty that the functional solubility of the chemical may increase in certain 

environmental conditions (e.g., tank mixture) remains and, if this is the case, could potentially 

result in risk to aquatic organisms not predicted in this assessment. The likelihood of the 

assessment underestimating risks to aquatic organisms is low because RQs were not close to 

LOCs and the high Kfoc for ametoctradin suggests that it is not likely to remain dissolved in 

water for a long period of time.

6.4 Assumptions and Limitations Related to Effects Assessment

Age class and sensitivity of effects thresholds

It is generally recognized that test organism age may have a significant impact on the observed 

sensitivity to a toxicant. The screening risk assessment acute toxicity data for fish are collected 
56

on juvenile fish between 0.1 and 5 grams. Aquatic invertebrate acute testing is performed on 

recommended immature age classes (e.g., first instar for daphnids, second instar for amphipods, 

stoneflies and mayflies, and third instar for midges). Similarly, acute dietary testing with birds is 

also performed on juveniles, with mallards being 5-10 days old and quail being 10-14 days old.

Testing of juveniles may overestimate toxicity of older age classes for pesticide active 

ingredients, such as ametoctradin, that act directly (without metabolic transformation) because 

younger age classes may not have the enzymatic systems associated with detoxifying 

xenobiotics. The screening risk assessment has no current provisions for a generally applied 

method that accounts for this uncertainty. In so far as the available toxicity data may provide 

ranges of sensitivity information with respect to age class, the risk assessment uses the most 

sensitive life-stage information as the conservative screening endpoint.

Use of the Most Sensitive Species Tested

Although the screening-level risk assessment relies on a selected toxicity endpoint from the most 

sensitive species tested, it does not necessarily mean that the selected toxicity endpoint reflects

sensitivity of the most sensitive species existing in a given environment. The relative position of 

the most sensitive species tested in the distribution of all possible species is a function of the 

overall variability among species to a particular chemical. In the case of listed species, there is 

uncertainty regarding the relationship of the listed species' sensitivity and the most sensitive 

species tested.

The Agency is not limited to a base set of surrogate toxicity information in establishing risk 

assessment conclusions. The Agency also considers toxicity data on non-standard test species 

when available. 
57

7 Literature Cited

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Potential. Western Farm Press. Vol 31(7) pp. 17 & 21.

Arnot, J.A. and F.A.P.C. Gobas. 2004. A food web bioaccumulation model for organic chemicals 

in aquatic ecosystems. Environmental Toxicology and Chemistry, v23 (10), 2343-2355.

Beyer, W. N., E. E. Connor and S. Gerould. 1994. Estimates of Soil Ingestion by Wildlife. 

Journal of Wildlife Management. 58(2):375-382. 

Bhatti, M.A., K. Al- Khatib, A.S. Felsot, R. Parker and S. Kadir. 1995. Effects of Simulated 

Chlorsulfuron Drift on Fruit Yield and Quality of Sweet Cherries (Prunus Avium L.). 

Environ. Tox. Chem. Vol 14 No. 3, pp. 537-544. 

Briggs GG, Bromilow RH, Evans AA (1982) Relationships between lipophilicity and root uptake 

and translocation of non-ionised chemicals by barley. Pestic Sci 13: 495-504.

ECOFRAM. 1999. ECOFRAM Terrestrial Draft Report. Ecological Committee on FIFRA Risk 

Assessment Methods. U.S. EPA, Washington D.C.

Fahl GM, Kreft L, Altenburger R, Faust M, Boedeker W, Grimme LH (1995) pH-dependent 

sorption, bioconcentration and algal toxicity of sulfonurea herbicides. Aquat Toxicol 31: 

175-187.

FAO 2000. Food and Agriculture Organization of the United Nations. FAO PESTICIDE 

DISPOSAL SERIES 8. Assessing Soil Contamination: A Reference Manual. Appendix 

2. Parameters of pesticides that influence processes in the soil. Editorial Group, FAO 

Information Division: Rome, 2000. 

http://www.fao.org/DOCREP/003/X2570E/X2570E00.htm

Fletcher, J.S. 1991. Horse Heaven Hills/Badger Canyon, A case Study of Alleged Pesticide Drift 

Damage. Presentation at the 84th Annual Meeting & Exhibition, Vancouver, British 

Columbia 91-150.7 

Fletcher J.S., T. G. Pfleeger and H.C. Ratsch 1993. Potential Environmental Risks Associated 

with the New Sulfonylurea Herbicides. Environ. Sci. Technol. Vol 27, No 10, pp. 2250-

2252.

Fletcher, J.S., J.E. Nellesson, and T. G. Pfleeger. 1994. Literature review and evaluation of the 

EPA food-chain (Kenaga) nomogram, an instrument for estimating pesticide residues on 

plants. Environ Toxicol Chem 13(9):1383–1391.

Fletcher J.S., T. G. Pfleeger and H.C. Ratsch 1995. Chlorsulfuron Influence on Garden Pea 

Reproduction. Physiologia Plantarum 94: pp 261-267.
58

Fletcher J.S., T. G. Pfleeger, H.C. Ratsch and R. Hayes 1996. Potential Impacts of Low Levels 

of Chlorsulfuron and Other Herbicides on Growth and Yields of Non-target Plants. 

Environ, Tox. and Chem. Vol. 15, No. 7. pp 1189-1196.

Food and Agriculture Organization of the United Nations. FAO PESTICIDE DISPOSAL 

SERIES 8. Assessing Soil Contamination: A Reference Manual. Appendix 2. 

Parameters of pesticides that influence processes in the soil. Editorial Group, FAO 

Information Division: Rome, 2000. 

http://www.fao.org/DOCREP/003/X2570E/X2570E00.htm

Gusey W.F., Z.D. Maturgo. 1973. Wildlife Utilization of Croplands. Environmental 

Conservation Department. Shell Oil Company, Houston, TX.

Hoerger, F. and E.E. Kenaga. 1972. Pesticide residues on plants: correlation of representative 

data as a basis for estimation of their magnitude in the environment. In F. Coulston and F. 

Korte, eds., Environmental Quality and Safety: Chemistry, Toxicology, and Technology, 

Georg Thieme Publ, Stuttgart, West Germany, pp. 9–28.

HSDB, 2002 [Hazardous Substances Data Bank]. National Library of Medicine. Last update: 6-

8-2002. Access date: 6-5-2003. http://toxnet.nlm.nih.gov/cgibin/sis/htmlgen?HSDB.

Kirkwood, J. 1983. A limit to metabolizable energy intake in mammals and birds. Comp. 

Biochem. Physiol. 75A:1-3.

Martin, C. M., H. S. Zim & A. C. Nelson, 1951. American Wildlife and Plants - A Guide to 

Wildlife Food Habits, Dover Publ. Inc., New York.

Merritt, R. W. and K. W. Cummins, eds. 1984. An Introduction to the Aquatic Insects of North 

America 2nd ed. Kendall/Hunt Publishing Company, Dubuque, Idaho. 722 pp.

Mineau, P., B. Jobin and A. Baril. 1994. A critique of the avian 5-day dietary test (LC50) as the 

basis of avian risk assessment. Technical Report No. 215, Headquarters, Canadian 

Wildlife Service, Hull, Quebec. p. 23.

NatureServe. 2005. NatureServe Explorer: An online encyclopedia of life [web application]. 

Version 4.5. NatureServe, Arlington, Virginia. Available 

http://www.natureserve.org/explorer.

Schwarzenbach, R.P., Gschwend, P. M., and Imboden, D.M., 1993. Environmental Organic 

Chemistry. John Wiley and Sons, Inc. New York.

Syracuse Research Corporation. 2006. Surface Water Scenario Development for the Pesticide 

Root Zone Model (PRZM) for Modeling Pesticide Exposure in Outdoor Nurseries: 

Supplement to Metadata. GSA Contract No. GS-00F-0019L, Report No. SRC TR-06-

081, North Syracuse, NY.

Tomlin CDS (ed) (2000) The Pesticide Manual, 12th Edition. British Crop Protection Council, 
59

UK.

Uesugi Y, Ueji M, Koshioka M (ed) (1997) Pesticide Data Book, 3rd Edition. Soft Science 

Publications, Tokyo, Japan.

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, DC.

USDA Crop Profiles. http://www.ipmcenters.org/cropprofiles/CP_form.cfm

U.S. EPA. 1993. Wildlife Exposure Factors Handbook. Volume I of II. EPA/600/R-93/187a. 

Office of Research and Development, Washington, D. C. 20460. EPA/600/R-93/187a. 

U.S. EPA. 1998. Guidance for Ecological Risk Assessment. Risk Assessment Forum. 

EPA/630/R-95/002F, April 1998.

U.S. EPA. 2002. Guidance for Selecting Input Parameters in Modeling the Environmental Fate 

and Transport of Pesticides Input Parameter Guidance. Version II February 28, 2002. 

U.S. Environmental Protection Agency, Office of Pesticide Programs, Environmental 

Fate and Effects Division.

U.S. EPA. 2004. Overview of the Ecological Risk Assessment Process in the Office of Pesticide 

Programs. Office of Prevention, Pesticides, and Toxic Substances. Office of Pesticide 

Programs. Washington, D.C. January 23, 2004.

U.S.EPA. 2011. Ametoctradin (BAS650): Report of the Residues of Concern Knowledgebase 

Sub-committee (ROCKS), DP Code: D386857. 

Wolfe, N.L., M.E-S. Metwally and A.E. Moftah. 1989. Hydrolytic Transformations of Organic 

Chemicals in the Environment. In: Reactions and Movement of Organic Chemicals in 

Soils. B.L. Sawhney and K. Brown, (Eds), Soil Science of America and American 

Society of Agronomy, Madison, WI. P.229-242.

Wolfe, N.L. 1990. Abiotic Transformations of Toxic Organic Chemicals in the Liquid Phase and 

Sediments. In: Toxic Organic Chemicals in Porous Media. Z. Gerstl, Y. Chen, U. 

Mingelgrin and B. Yaron. (Eds.). Springer-Verlag, New York. p.136-147.
60

Appendix A. Environmental Fate Data

Table A-1. Summary of transformation products identified in soil and water studies1

Compound 

code

Chemical name 

(IUPAC)

Molecular 

weight

Structure Physico-chemical properties

Major transformation products (> 10 %)

M650F01 4-(7-amino-5-

ethyl[1,2,4]triazolo[1,5-

a]pyrimidin-6-

yl)butanoic

acid

249.3 Water solubility (pure water 

at 20°C): 3.8 (± 0.1) g/L

pH of saturated solution with 

hydro-chloride: 2.5

Log Kow: 0.69 at acidic 

conditions

pKa: 4.3 when titrated with 

0.002 M NaOH

M650F02 3-(7-amino-5-

ethyl[1,2,4]triazolo[1,5-

a]pyrimidin-6-

yl)propanoic

acid

235.3 Water solubility (pure water 

at 20°C): 79 (± 2) g/L

pH of saturated solution with 

hydro-chloride: 0.5

Log Kow: 0.33 at acidic 

conditions and 1.0 at neutral 

conditions

pKa: 4.0 when titrated with 

0.01 M NaOH

M650F03 (7-amino-5-

ethyl[1,2,4]triazolo[1,5-

a]pyrimidin-6-yl)acetic 

acid

221.2 Water solubility (pure water 

at 20°C): 2.9 (± 0.2) g/L

pH of saturated solution with 

hydro-chloride: 2.0

Log Kow: 0.16 at acidic 

conditions 

pKa: 3.8 when titrated with 

0.002 M NaOH
61

Table A-1. Summary of transformation products identified in soil and water studies1

Compound 

code

Chemical name 

(IUPAC)

Molecular 

weight

Structure Physico-chemical properties

M650F04 7-amino-5-

ethyl[1,2,4]triazolo[1,5-

a]pyrimidine-6-

carboxylic acid

207.2 Water solubility (pure water 

at 20°C): 0.35 (± 0.01) g/L

pH of saturated solution: 3.5

Log Kow: 0.87 at acidic 

conditions 

pKa: 4.0 when titrated with 

0.002 M NaOH

Minor transformation products (< 10 %)

M650F05* 263

N

N N

N

NH2

OH

O

M650F06* 277

OH

O

N

N N

N

NH2

M650F09* 305

N

N N

N

NH2

OH

O

M650F18* 305

N

N N

N

NH2

OH

O

M650F28** 205

M650F31 249

M650F32** 193

M650F33 191

M650F39** 177
62

Table A-1. Summary of transformation products identified in soil and water studies1

Compound 

code

Chemical name 

(IUPAC)

Molecular 

weight

Structure Physico-chemical properties

M650F48** 221

M650F51 

(isomer of 

M650F39)**

177

N

N N

N

NH2

1 Review of Environmental Fate Studies for Soil and Water for New Chemical Registration of Ametoctradin(DP 

392115

Table A-2. Summary of Biotransformation Rates for Ametoctradin and Its Major Transformation 

Products in Laboratory Aerobic and Anaerobic Aquatic System Studies

Compound Compartment Water/ sediment 

system

Kinetics 

modela DT50 (d) DT90 (d)

Study:

MRID #

Aerobic water/sediment system (dark trials only)

Ametoctradin

water

Berghäuser 

Altrhein SFO 0.69 2.29

47700145

Ranschgraben SFO 0.89 2.94

sediment

Berghäuser 

Altrhein DFOP 2.07 21.8

Ranschgraben DFOP 2.12 7.81

total system

Berghäuser 

Altrhein SFO 1.72 5.71

Ranschgraben SFO 1.51 5.01

M650F01

water

Berghäuser 

Altrhein IORE 2.55 20.3

Ranschgraben SFO 3.15 10.4

sediment

Berghäuser 

Altrhein / 

Ranschgraben

Insufficient data points

total system

Berghäuser 

Altrhein IORE 3.09 39.8

Ranschgraben SFO 3.1 10.3

M650F02

water

Berghäuser 

Altrhein SFO 14 46.4

Ranschgraben IORE 16.3 89.2

sediment

Berghäuser 

Altrhein IORE 19.3 138

Ranschgraben Insufficient data points

total system

Berghäuser 

Altrhein SFO 17.1 56.7

Ranschgraben SFO 33.5 111

M650F03 water Berghäuser 

Altrhein SFO 226 749
63

Table A-2. Summary of Biotransformation Rates for Ametoctradin and Its Major Transformation 

Products in Laboratory Aerobic and Anaerobic Aquatic System Studies

Compound Compartment Water/ sediment 

system

Kinetics 

modela DT50 (d) DT90 (d)

Study:

MRID #

Ranschgraben SFO 344 1140

sediment

Berghäuser 

Altrhein Insufficient data points

Ranschgraben SFO 208 692

total system

Berghäuser 

Altrhein SFO 377 1250

Ranschgraben SFO 479 1590

M650F04

water Berghäuser 

Altrhein / 

Ranschgraben

sediment Insufficient data points

total system

Anaerobic water/sediment system

Ametoctradin

water

White Lake, SD

IORE 1.6 10.3

47700221

sediment IORE 13.8 227

total system DFOP 7.4 60.1

M650F01 water (total systemb) SFO 8.02 26.6

M650F03

water

n.d.c sediment

total system a SFO = single first-order, DFOP = double first-order in parallel, IORE = intermediate-order rate equation. The choice of 

which model to use to best describe the dissipation pattern is based on the model with the lowest model error (%) 

and/or the least bias in residuals of regression data points.

b

M650F01 was detected only in the water layer, therefore, the total system is the same as the water layer. c

Dissipation rates (DT50 and DT90 values) were not determined due to insufficient degradation in each of

the environmental compartments.
64

Figure A-1. Proposed Route of Degradation of Ametoctradin in Water/Sediment Systems
65

Table A-3. Summary of Degradation Rates of Ametoctradin and Associated 

Transformation Products Obtained in Laboratory Soil Studies

Test Material Soil type

(USDA)

Study duration 

[days]

Temp. 

[°C]

Kinetics modela DT50

[days]

DT90

[days]

χ2

Errorb

(%)

Study:

MRID #

Aerobic Soil

Ametoctradin Bruch West

(sandy loam)

360 20

DFOP

1.3 7.3 4.4 47700117

LUFA 5M

(sandy loam)

120 20

DFOP

1.5 8.4 6.2

47700121

LUFA 2.2

(loamy sand)

120 20

DFOP

1.8 7.6 7.0

Li 10

(loamy sand)

120 20

DFOP

3.2 12.8 6.4

Li 10

(loamy sand)

120 10

DFOP

6.4 24.9 6.3

Idaho

(sandy loam)

365 25 DFOP 9.6 192 16

47700118

Illinois

(loam)

365 25 SFO 6.9 22.9 13

New Jersey

(loam)

365 25 SFO 7.1 23.5 11

Wisconsin

(loamy sand)

365 25 DFOP 16.7 267 12

M650F03 LUFA 3A

(loam)

120 20 SFO 75.1 249 6.4

IIA 7.2.3/01

2008/1010539

LUFA 2.2

(loamy sand)

120 20 SFO 43.5 144 8.4

LUFA 2.3

(sandy loam)

120 20 SFO 28.8 95.7 4.1

Wisconsin

(sand)

120 20 SFO 35.0 116 5.8

M650F04 LUFA 3A

(loam)

120 20 DFOP 28.0 139 5.9

IIA 7.2.3/02

2007/1057457

LUFA 2.3

(sandy loam)

120 20 SFO 106 351 4.8

Birkenheide

(loamy sand)

120 20 DFOP 289 1020 1.2

Wisconsin

(loamy sand)

120 20 SFO 132 439 2.5

Anaerobic Soil
66

Table A-3. Summary of Degradation Rates of Ametoctradin and Associated 

Transformation Products Obtained in Laboratory Soil Studies

Test Material Soil type

(USDA)

Study duration 

[days]

Temp. 

[°C]

Kinetics modela DT50

[days]

DT90

[days]

χ2

Errorb

(%)

Study:

MRID #

Ametoctradin Bruch West

(sandy loam)

118 20 SFO 182 606 2.2

47700119

47700145 a SFO = single first-order, DFOP = double first-order in parallel, IORE = intermediate-order rate equation

b The choice of which model to use to best describe the dissipation pattern is based on the model with the lowest 

model error (%) and/or the least bias in residuals of regression data points.

Figure A-2. Proposed Metabolic Transformation Pathway of Ametoctradin in Soil
67

Table A-4. Summary of adsorption of major metabolites of BAS650F

Soil Source and Properties Freundlich isotherm adsorption KFOC (mL/g)

Soil Soil Type

(USDA)

pH

(CaCl2)

Organic 

Carbon 

(%)

BAS650F01 BAS650F02 BAS650F03 BAS650F04

Münster Sandy loam 5.0 1.44 NA NA 62.6 47.0

LUFA 2.2, 

F2.24306 Loamy Sand 5.7 1.72 62.3 33.6 50.6 40.0

New Jersey Loam 6.2 1.10 162.0 89.0 58.5 43.6

1680 Loamy Sand 5.9 0.88 67.5 33.4 15.3 11.4

LUFA 3A, 

F3A4206

Loam 7.2 3.23 28.0 16.0 10.7 8.1

Studernheim Sandy Loam 7.6 1.51 21.8 14.0 11.8 7.7

California Sandy Loam 8.0 0. 35 78.4 36.0 30.9 17.1

Schifferstadt1 Loamy Sand 4.9 0.90 193.0 31.0 NA NA

Schifferstadt1 Sand 4.1 0.76 NA NA 47.0 118.0

LUFA 2.1 Sand 5.2 0.52 NA NA 25.0 11.0

Große Erde Loamy sand 6.8 0.92 NA NA 11.0 9.0

LUFA 2.3 Sandy loam 7.2 1.0 NA NA 33.0 23.0

La Gironda Silty clay 

loam

7.5 3.84 NA NA 13.0 8.0

NA- Not applicable 1 Even though these soils have same name but they have slightly dissimilar soil properties 
68

Appendix B. Aquatic Modeling

GENEEC Output

Aerial Application

 RUN No. 1 FOR BAS650F ON Vegetables * INPUT VALUES * 

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

 RATE (#/AC) No.APPS & SOIL SOLUBIL APPL TYPE NO-SPRAY INCORP

 ONE(MULT) INTERVAL Koc (PPB ) (%DRIFT) (FT) (IN)

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

 .274( .632) 3 5 3912.5 140.0 AERL_B( 13.0) .0 .0

 FIELD AND STANDARD POND HALFLIFE VALUES (DAYS) 

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

 METABOLIC DAYS UNTIL HYDROLYSIS PHOTOLYSIS METABOLIC COMBINED

 (FIELD) RAIN/RUNOFF (POND) (POND-EFF) (POND) (POND) 

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

 11.90 2 N/A 76.80- 9523.20 1.94 1.94

 GENERIC EECs (IN MICROGRAMS/LITER (PPB)) Version 2.0 Aug 1, 2001

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

 PEAK MAX 4 DAY MAX 21 DAY MAX 60 DAY MAX 90 DAY

 GEEC AVG GEEC AVG GEEC AVG GEEC AVG GEEC

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

 5.18 4.02 1.36 .48 .32

 RUN No. 2 FOR BAS650F ON Grape * INPUT VALUES * 

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

 RATE (#/AC) No.APPS & SOIL SOLUBIL APPL TYPE NO-SPRAY INCORP

 ONE(MULT) INTERVAL Koc (PPB ) (%DRIFT) (FT) (IN)

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

 .274( .658) 4 7 3912.5 140.0 AERL_B( 13.0) .0 .0

 FIELD AND STANDARD POND HALFLIFE VALUES (DAYS) 

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

 METABOLIC DAYS UNTIL HYDROLYSIS PHOTOLYSIS METABOLIC COMBINED

 (FIELD) RAIN/RUNOFF (POND) (POND-EFF) (POND) (POND) 

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

 11.90 2 N/A 76.80- 9523.20 1.94 1.94

 GENERIC EECs (IN MICROGRAMS/LITER (PPB)) Version 2.0 Aug 1, 2001

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

 PEAK MAX 4 DAY MAX 21 DAY MAX 60 DAY MAX 90 DAY

 GEEC AVG GEEC AVG GEEC AVG GEEC AVG GEEC

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

 5.24 4.05 1.36 .48 .32

 RUN No. 3 FOR BAS650F ON Hops * INPUT VALUES * 
69

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

 RATE (#/AC) No.APPS & SOIL SOLUBIL APPL TYPE NO-SPRAY INCORP

 ONE(MULT) INTERVAL Koc (PPB ) (%DRIFT) (FT) (IN)

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

 .274( .513) 3 10 3912.5 140.0 AERL_B( 13.0) .0 .0

 FIELD AND STANDARD POND HALFLIFE VALUES (DAYS) 

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

 METABOLIC DAYS UNTIL HYDROLYSIS PHOTOLYSIS METABOLIC COMBINED

 (FIELD) RAIN/RUNOFF (POND) (POND-EFF) (POND) (POND) 

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

 11.90 2 N/A 76.80- 9523.20 1.94 1.94

 GENERIC EECs (IN MICROGRAMS/LITER (PPB)) Version 2.0 Aug 1, 2001

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

 PEAK MAX 4 DAY MAX 21 DAY MAX 60 DAY MAX 90 DAY

 GEEC AVG GEEC AVG GEEC AVG GEEC AVG GEEC

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

 4.16 3.22 1.09 .39 .26

Ground Application

 RUN No. 4 FOR BAS650F ON Ornamental * INPUT VALUES * 

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

 RATE (#/AC) No.APPS & SOIL SOLUBIL APPL TYPE NO-SPRAY INCORP

 ONE(MULT) INTERVAL Koc (PPB ) (%DRIFT) (FT) (IN)

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

 .274( .560) 4 10 3912.5 140.0 GRHIFI( 6.6) .0 .0

 FIELD AND STANDARD POND HALFLIFE VALUES (DAYS) 

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

 METABOLIC DAYS UNTIL HYDROLYSIS PHOTOLYSIS METABOLIC COMBINED

 (FIELD) RAIN/RUNOFF (POND) (POND-EFF) (POND) (POND) 

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

 11.90 2 N/A 76.80- 9523.20 1.94 1.94

 GENERIC EECs (IN MICROGRAMS/LITER (PPB)) Version 2.0 Aug 1, 2001

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

 PEAK MAX 4 DAY MAX 21 DAY MAX 60 DAY MAX 90 DAY

 GEEC AVG GEEC AVG GEEC AVG GEEC AVG GEEC

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

 4.26 3.26 1.09 .39 .26

RUN No. 5 FOR BAS650F ON Grape (Ground) * INPUT 

VALUES * 

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

 RATE (#/AC) No.APPS & SOIL SOLUBIL APPL TYPE NO-SPRAY INCORP

 ONE(MULT) INTERVAL Koc (PPM ) (%DRIFT) (FT) (IN)

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

 .274( .658) 4 7 3912.5 140.0 GRHIFI( 6.6) .0 .0
70

 FIELD AND STANDARD POND HALFLIFE VALUES (DAYS) 

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

 METABOLIC DAYS UNTIL HYDROLYSIS PHOTOLYSIS METABOLIC COMBINED

 (FIELD) RAIN/RUNOFF (POND) (POND-EFF) (POND) (POND) 

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

 11.90 2 N/A 76.80- 9523.20 1.94 1.94

 GENERIC EECs (IN MICROGRAMS/LITER (PPB)) Version 2.0 Aug 1, 2001

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

 PEAK MAX 4 DAY MAX 21 DAY MAX 60 DAY MAX 90 DAY

 GEEC AVG GEEC AVG GEEC AVG GEEC AVG GEEC

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

 5.00 3.82 1.28 .46 .30

PRZM/EXAMS Example Output

stored as NY Grape _A.out

Chemical: 

BAS650F

PRZM 

environ

ment: 

NYGra

pesSTD

.txt

modified Tueday, 29 May 2007 at 

13:59:44

EXAM

S 

environ

ment: 

pond29

8.exv

modified Tueday, 26 August 2008 at 06:14:08

Metfile: 

w14860

.dvf

modified Tueday, 26 August 2008 at 06:15:12

Water segment concentrations (ppb)

Year Peak 96 hr 21 Day 60 Day 90 Day Yearly

1961 0.29 0.17 0.12 0.06 0.04 0.01

1962 0.39 0.27 0.11 0.09 0.07 0.02

1963 0.28 0.16 0.11 0.07 0.05 0.01

1964 0.78 0.43 0.18 0.12 0.08 0.02

1965 1.45 0.85 0.30 0.16 0.11 0.03

1966 0.32 0.21 0.13 0.07 0.05 0.02

1967 1.64 0.95 0.32 0.17 0.12 0.03

1968 0.29 0.17 0.12 0.06 0.04 0.01
71

1969 0.39 0.24 0.15 0.07 0.05 0.01

1970 1.06 0.62 0.28 0.16 0.11 0.03

1971 0.47 0.28 0.15 0.10 0.07 0.02

1972 1.16 0.85 0.46 0.23 0.16 0.04

1973 0.28 0.16 0.11 0.06 0.04 0.01

1974 1.50 0.91 0.38 0.17 0.12 0.03

1975 0.65 0.36 0.12 0.09 0.07 0.02

1976 1.03 0.62 0.27 0.13 0.09 0.03

1977 1.76 0.99 0.34 0.17 0.13 0.03

1978 0.84 0.47 0.15 0.10 0.08 0.02

1979 0.55 0.32 0.17 0.11 0.08 0.02

1980 1.67 0.95 0.32 0.17 0.12 0.03

1981 0.70 0.41 0.19 0.10 0.08 0.02

1982 0.55 0.35 0.20 0.11 0.07 0.02

1983 0.83 0.58 0.23 0.14 0.10 0.03

1984 0.57 0.33 0.19 0.09 0.06 0.02

1985 0.98 0.55 0.25 0.13 0.09 0.02

1986 0.28 0.16 0.12 0.06 0.04 0.01

1987 0.52 0.28 0.17 0.10 0.07 0.02

1988 0.39 0.21 0.11 0.07 0.05 0.01

1989 0.52 0.37 0.19 0.09 0.06 0.02

1990 0.30 0.19 0.12 0.06 0.05 0.01

Sorted results

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

0.03 1.76 0.99 0.46 0.23 0.16 0.04

0.06 1.67 0.95 0.38 0.17 0.13 0.03

0.10 1.64 0.95 0.34 0.17 0.12 0.03

0.13 1.50 0.91 0.32 0.17 0.12 0.03

0.16 1.45 0.85 0.32 0.17 0.12 0.03

0.19 1.16 0.85 0.30 0.16 0.11 0.03

0.23 1.06 0.62 0.28 0.16 0.11 0.03

0.26 1.03 0.62 0.27 0.14 0.10 0.03

0.29 0.98 0.58 0.25 0.13 0.09 0.03

0.32 0.84 0.55 0.23 0.13 0.09 0.02

0.35 0.83 0.47 0.20 0.12 0.08 0.02

0.39 0.78 0.43 0.19 0.11 0.08 0.02

0.42 0.70 0.41 0.19 0.11 0.08 0.02

0.45 0.65 0.37 0.19 0.10 0.08 0.02

0.48 0.57 0.36 0.18 0.10 0.07 0.02

0.52 0.55 0.35 0.17 0.10 0.07 0.02

0.55 0.55 0.33 0.17 0.10 0.07 0.02

0.58 0.52 0.32 0.15 0.09 0.07 0.02

0.61 0.52 0.28 0.15 0.09 0.07 0.02

0.65 0.47 0.28 0.15 0.09 0.06 0.02
72

0.68 0.39 0.27 0.13 0.09 0.06 0.02

0.71 0.39 0.24 0.12 0.07 0.05 0.02

0.74 0.39 0.21 0.12 0.07 0.05 0.01

0.77 0.32 0.21 0.12 0.07 0.05 0.01

0.81 0.30 0.19 0.12 0.07 0.05 0.01

0.84 0.29 0.17 0.12 0.06 0.05 0.01

0.87 0.29 0.17 0.11 0.06 0.04 0.01

0.90 0.28 0.16 0.11 0.06 0.04 0.01

0.94 0.28 0.16 0.11 0.06 0.04 0.01

0.97 0.28 0.16 0.11 0.06 0.04 0.01

0.10 1.62 0.94 0.33 0.17 0.12 0.03

Averag

e of 

yearly 

average

s:

0.02

Inputs generated by pe5.pl - Novemeber 2006

Data used for this run:

Output File: NY Grape _A

Metfile: w14860.dvf

PRZM 

scenario

:

NYGrapesSTD.txt

EXAM

S 

environ

ment 

file:

pond298.exv

Chemic

al 

Name:

BAS65

0F

Descrip

tion

Variabl

e Name

Value Units Comments

Molecul

ar 

weight

mwt 275.4 g/mol

Henry's 

Law 

Const.

henry 3.10E09atm-m^3/mol

Vapor 

Pressur

e

vapr 4.50E12torr

Solubili sol 0.15 mg/L
73

ty

Kd Kd mg/L

Koc Koc 3912.5 mg/L

Photoly

sis halflife

kdp 76.8 days Halflife

Aerobic 

Aquatic 

Metabol

ism

kbacw 1.94 days Halfife

Anaero

bic 

Aquatic 

Metabol

ism

kbacs 26.6 days Halfife

Aerobic 

Soil 

Metabol

ism

asm 11.9 days Halfife

Hydroly

sis:

pH 7 0 days Halflife

Method

:

CAM 2 integer See PRZM 

manual

Incorpo

ration 

Depth:

DEPI cm

Applica

tion 

Rate:

TAPP 0.1 kg/ha

Applica

tion 

Efficien

cy:

APPEF

F

0.95 fraction

Spray 

Drift

DRFT 0.05 fraction of application rate applied to pond

Applica

tion 

Date

Date 15-06 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 kg/ha

Interval 

2

interval 7 days Set to 0 or delete line for single app.

app. 

rate 2

apprate kg/ha

Interval interval 7 days Set to 0 or delete line for single app.
74

3

app. 

rate 3

apprate kg/ha

Record 

17:

FILTR

A

IPSCN

D

1

UPTKF

Record 

18:

PLVKR

T

PLDKR

T

FEXTR

C

0.5

Flag for 

Index 

Res. 

Run

IR EPA 

Pond

Flag for 

runoff 

calc.

RUNO

FF

none none, monthly or total(average of entire run)

Pore Water

stored as NY Grape 

_Aben.out

Chemical: 

BAS650F

PRZM 

environ

ment: 

NYGra

pesSTD

.txt

modified Tueday, 29 May 2007 at 

13:59:44

EXAM

S 

environ

ment: 

pond29

8.exv

modified Tueday, 26 August 2008 at 06:14:08

Metfile: 

w14860

.dvf

modified Tueday, 26 August 2008 at 06:15:12

Benthic segment concentrations (ppb)

Year Peak 96 hr 21 Day 60 Day 90 Day Yearly

1961 0.03 0.03 0.03 0.02 0.02 0.01

1962 0.13 0.13 0.11 0.07 0.06 0.02
75

1963 0.06 0.05 0.05 0.04 0.03 0.01

1964 0.17 0.16 0.13 0.11 0.09 0.03

1965 0.29 0.29 0.25 0.16 0.12 0.04

1966 0.06 0.06 0.05 0.04 0.04 0.01

1967 0.33 0.32 0.28 0.18 0.14 0.04

1968 0.04 0.04 0.03 0.03 0.02 0.01

1969 0.07 0.07 0.06 0.04 0.03 0.01

1970 0.27 0.27 0.24 0.16 0.12 0.04

1971 0.12 0.12 0.10 0.07 0.06 0.02

1972 0.35 0.34 0.29 0.23 0.18 0.05

1973 0.03 0.03 0.02 0.02 0.02 0.01

1974 0.30 0.30 0.26 0.17 0.14 0.04

1975 0.14 0.14 0.12 0.08 0.06 0.02

1976 0.19 0.19 0.17 0.12 0.09 0.03

1977 0.32 0.32 0.27 0.18 0.14 0.04

1978 0.17 0.17 0.14 0.10 0.08 0.03

1979 0.14 0.14 0.12 0.08 0.07 0.02

1980 0.32 0.32 0.27 0.18 0.14 0.04

1981 0.11 0.11 0.09 0.08 0.07 0.02

1982 0.09 0.09 0.08 0.07 0.06 0.02

1983 0.18 0.17 0.15 0.13 0.11 0.03

1984 0.10 0.10 0.09 0.06 0.05 0.02

1985 0.23 0.23 0.19 0.13 0.09 0.03

1986 0.05 0.05 0.04 0.03 0.02 0.01

1987 0.15 0.15 0.12 0.09 0.07 0.02

1988 0.09 0.08 0.07 0.05 0.04 0.01

1989 0.09 0.09 0.09 0.06 0.05 0.02

1990 0.04 0.04 0.03 0.03 0.03 0.01

Sorted results

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

0.03 0.35 0.34 0.29 0.23 0.18 0.05

0.06 0.33 0.32 0.28 0.18 0.14 0.04

0.10 0.32 0.32 0.27 0.18 0.14 0.04

0.13 0.32 0.32 0.27 0.18 0.14 0.04

0.16 0.30 0.30 0.26 0.17 0.14 0.04

0.19 0.29 0.29 0.25 0.16 0.12 0.04

0.23 0.27 0.27 0.24 0.16 0.12 0.04

0.26 0.23 0.23 0.19 0.13 0.11 0.03

0.29 0.19 0.19 0.17 0.13 0.09 0.03

0.32 0.18 0.17 0.15 0.12 0.09 0.03

0.35 0.17 0.17 0.14 0.11 0.09 0.03

0.39 0.17 0.16 0.13 0.10 0.08 0.03

0.42 0.15 0.15 0.12 0.09 0.07 0.02

0.45 0.14 0.14 0.12 0.08 0.07 0.02
76

0.48 0.14 0.14 0.12 0.08 0.07 0.02

0.52 0.13 0.13 0.11 0.08 0.06 0.02

0.55 0.12 0.12 0.10 0.07 0.06 0.02

0.58 0.11 0.11 0.09 0.07 0.06 0.02

0.61 0.10 0.10 0.09 0.07 0.06 0.02

0.65 0.09 0.09 0.09 0.06 0.05 0.02

0.68 0.09 0.09 0.08 0.06 0.05 0.02

0.71 0.09 0.08 0.07 0.05 0.04 0.01

0.74 0.07 0.07 0.06 0.04 0.04 0.01

0.77 0.06 0.06 0.05 0.04 0.03 0.01

0.81 0.06 0.05 0.05 0.04 0.03 0.01

0.84 0.05 0.05 0.04 0.03 0.03 0.01

0.87 0.04 0.04 0.03 0.03 0.02 0.01

0.90 0.04 0.04 0.03 0.03 0.02 0.01

0.94 0.03 0.03 0.03 0.02 0.02 0.01

0.97 0.03 0.03 0.02 0.02 0.02 0.01

0.10 0.32 0.32 0.27 0.18 0.14 0.04

Averag

e of 

yearly 

average

s:

0.02

Inputs generated by pe5.pl - Novemeber 2006

Data used for this run:

Output File: NY Grape _A

Metfile: w14860.dvf

PRZM 

scenario

:

NYGrapesSTD.txt

EXAM

S 

environ

ment 

file:

pond298.exv

Chemic

al 

Name:

BAS65

0F

Descrip

tion

Variabl

e Name

Value Units Comments

Molecul

ar 

weight

mwt 275.4 g/mol

Henry's henry 3.10E- atm-m^3/mol
77

Law 

Const.

09

Vapor 

Pressur

e

vapr 4.50E12torr

Solubili

ty

sol 0.15 mg/L

Kd Kd mg/L

Koc Koc 3912.5 mg/L

Photoly

sis halflife

kdp 76.8 days Halflife

Aerobic 

Aquatic 

Metabol

ism

kbacw 1.94 days Halfife

Anaero

bic 

Aquatic 

Metabol

ism

kbacs 26.6 days Halfife

Aerobic 

Soil 

Metabol

ism

asm 11.9 days Halfife

Hydroly

sis:

pH 7 0 days Halflife

Method

:

CAM 2 integer See PRZM 

manual

Incorpo

ration 

Depth:

DEPI cm

Applica

tion 

Rate:

TAPP 0.1 kg/ha

Applica

tion 

Efficien

cy:

APPEF

F

0.95 fraction

Spray 

Drift

DRFT 0.05 fraction of application rate applied to pond

Applica

tion 

Date

Date 15-06 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. apprate kg/ha
78

rate 1

Interval 

2

interval 7 days Set to 0 or delete line for single app.

app. 

rate 2

apprate kg/ha

Interval 

3

interval 7 days Set to 0 or delete line for single app.

app. 

rate 3

apprate kg/ha

Record

17:

FILTR

A

IPSCN

D

1

UPTKF

Record 

18:

PLVKR

T

PLDKR

T

FEXTR

C

0.5

Flag for 

Index 

Res. 

Run

IR EPA 

Pond

Flag for 

runoff 

calc.

RUNO

FF

none none, monthly or total(average of entire run)

 
79

Appendix C. Example T-REX Output

Ornamentals & Golf Courses : 4 apps @ 0.274 lb a.i./acre (10-day interval)

Dietary-based EECs 

(ppm)

Kenaga

Values

Short Grass 200.26

Tall Grass 91.79

Broadleaf plants/sm Insects 112.65

Fruits/pods/seeds/lg insects 12.52

Avian

Dose-based EECs (mg/kg-bw)

Avian Classes and Body Weights (grams)

small mid large Granivores(grams)

20 100 1000 20 100 1000

Short Grass 228.08 130.06 58.23

Tall Grass 104.54 59.61 26.69

Broadleaf plants/sm Insects 128.29 73.16 32.75

Fruits/pods/seeds/lg insects 14.25 8.13 3.64 3.17 1.81 0.81

Mammalian

Dose-Based EECs 

(mg/kg-bw)

Mammalian Classes and Body weight

Herbivores/ insectivores 

(grams) Granivores(grams)

15 35 1000 15 35 1000

Short Grass 190.93 131.96 30.60

Tall Grass 87.51 60.48 14.02

Broadleaf plants/sm Insects 107.40 74.23 17.21

Fruits/pods/seeds/lg insects 11.93 8.25 1.91 2.65 1.83 0.42
80

Appendix D. TerrPlant Output

TerrPlant v. 1.2.2

Green values signify user inputs (Tables 1, 2 and 4). 

Input and output guidance is in popups indicated by red arrows.

Table 1. Chemical Identity.

Chemical Name ametoctradin

PC code 119201

Use all

Application Method aerial

Application Form Spray 

Solubility in Water 

(ppm) 0.15

Table 2. Input parameters used to derive EECs.

Input Parameter Symbol Value Units

Application Rate A 0.274 y

Incorporation I 1 none

Runoff Fraction R 0.01 none

Drift Fraction D 0.05 none

Table 3. EECs for ametoctradin. Units in y.

Description Equation EEC

Runoff to dry areas (A/I)*R 0.00274

Runoff to semi-aquatic areas (A/I)*R*10 0.0274

Spray drift A*D 0.0137

Total for dry areas ((A/I)*R)+(A*D) 0.01644

Total for semi-aquatic areas ((A/I)*R*10)+(A*D) 0.0411

Table 4. Plant survival and growth data used for RQ derivation. Units are in y.

Seedling Emergence Vegetative Vigor

Plant type EC25 NOAEC EC25 NOAEC 

Monocot x 0.51 x 0.51

Dicot x 0.51 x 0.51

Table 5. RQ values for plants in dry and semi-aquatic areas exposed to ametoctradin through runoff 

and/or spray drift.*

Plant Type Listed Status Dry Semi-Aquatic Spray Drift

Monocot non-listed #VALUE! #VALUE! #DIV/0!

Monocot listed <0.1 <0.1 <0.1

Dicot non-listed #VALUE! #VALUE! #DIV/0!

Dicot listed <0.1 <0.1 <0.1

*If RQ > 1.0, the LOC is exceeded, resulting in potential for risk to that plant group.
81

Appendix E. RQ Methods and LOC Definitions 

The Risk Quotient Method is the means by which the Environmental Fate and Effects Division 

(EFED) integrates the results of exposure and ecotoxicity data. In this method, both acute and 

chronic risk quotients (RQs) are calculated by dividing exposure estimates by the most sensitive 

ecotoxicity values derived from the studies. Calculated RQs are then compared to OPP's levels of 

concern (LOCs). The LOCs are the criteria used by OPP to indicate potential risk to non-target 

organisms and the need to consider regulatory action. EFED has defined LOCs for acute risk, 

potential restricted use, and for listed species. Risk presumptions, along with the corresponding 

RQs and LOCs are summarized in the table below.

Table E-1. Levels of Concern for Assessed Taxa

Risk Presumption RQ LOC

Birds

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/kg)

0.2

Acute Listed Species EEC/LC50 or LD50/sqft or LD50/day 0.1

Chronic Risk EEC/NOAEC 1

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/kg)

0.2

Acute Listed Species EEC/LC50 or LD50/sqft or LD50/day 0.1

Chronic Risk EEC/NOAEC 1

Aquatic Animals

Acute Risk EEC/LC50 or EC50 0.5

Acute Restricted Use EEC/LC50 or EC50 0.1

Acute Listed Species EEC/LC50 or EC50 0.05

Chronic Risk EEC/NOAEC 1

Terrestrial and Semi-Aquatic Plants 

Acute Risk EEC/EC25 1

Acute Listed Species EEC/EC05 or NOAEC 1

Aquatic Plants

Acute Risk EEC/EC50 1

Acute Listed Species EEC/EC05 or NOAEC 1
82

Appendix F. Toxicity Data for Terrestrial Invertebrates Other Than the 

Honey Bee

See Ecotoxicity monograph (DP 393441) for complete discussion of data.

The acute and chronic toxicity of the end-use products (EP) BAS 650 00 F and BAS 651 00 F 

was determined for a variety of terrestrial arthropod species. Toxicity endpoints were expressed 

according to the amount of EP applied (L EP/ha) as well as the amount of active ingredient (g 

a.i./ha, as BAS 650 F) present in the formulation. An overview of the accepted toxicity data for 

all test substances is given in Table F-1.

Acute toxicity 

End-use Products

Acute laboratory toxicity studies with BAS 650 00 F and BAS 651 00 F were conducted with the 

parasitic wasp Aphidius rhopalosiphi, the predatory mite Typhlodromus pyri, and the green 

lacewing Chrysoperlea carnea. Arthropods were exposed to dried residues on glass plates. BAS 

651 00 F was not acutely toxic to all species tested, with LR50 values greater than the highest 

concentration tested (i.e., >3.2 L EP/ha, or 970 g a.i./ha). BAS 650 00 F, was not acutely toxic to 

T. pyri or C. carnea within the range of concentrations tested, however A. rhopalosiphi exhibited 

a strong dose-response, with an LR50 of 1.22 L EP/ha (234 g a.i./ha or 0.209 lb a.i./acre). 

Extended laboratory toxicity studies with BAS 650 00 F and BAS 651 00 F were conducted with 

A. rhopalosiphi exposed to dried residues on barley seedlings. Neither end-use product caused 

significant mortality to A. rhopalosiphi. A significant reduction in reproduction (up to 37% 

reduction in number of mummies produced per female) was observed after exposure to BAS 650 

00 F (NOEC = 2.4 L EP/ha or 490 g a.i./ha). The LR50 and ER50 were greater than the highest 

tested concentrations for BAS 650 00 F (9.6 L EP/ha or 1962 g BAS 650 F/ha) and BAS 651 00 

F (2.4 L EP/ha or 717 g BAS 650 F/ha).

Chronic toxicity 

End-use Products

Field studies in Germany and France were performed with BAS 650 00 F to assess effects on 

predatory mites in vineyards. Four applications of 2.4 L EP/ha were made at 10 – 15 day 

intervals. Nearly all mites identified at all six trial sites were T. pyri. Relative to untreated control 

areas, no adverse effects on predatory mite populations were observed in five of the six 

vineyards studied in Southern Germany and France after 4 applications (April – July) of 2.4 L/ha 

BAS 650 00 F (equivalent to 491 g a.i./ha) in 400 – 800 L water/ha. In one vineyard in Southern 

France, slight and transient effects were seen, with a significant reduction in mite populations 

(24.2% reduction) nine days after the first application only; no significant differences between 

treated and control population levels occurred thereafter.

Table F-1. Summary of toxicity of the end-use products BAS 650 00 F and BAS 651 

00 F to non-target beneficial arthropods.

Organism Exposure Test Substance Endpoint Value Reference / 

Comments

Parasitic arthropod Acute contact 48-

hour 

BAS 650 00 F LR50 1.22 L EP/ha 

or =234 g a.i./ha

IIIA, 10.5.1/05

Endpoint based on 
83

Table F-1. Summary of toxicity of the end-use products BAS 650 00 F and BAS 651 

00 F to non-target beneficial arthropods.

Organism Exposure Test Substance Endpoint Value Reference / 

Comments

Parasitic wasp

(Aphidius 

rhopalosiphi)

(laboratory-treated 

glass plates)

mortality

BAS 651 00 F LR50 >3.2 L EP/ha 

(PMRA, APVMA, 

USEPA, 

NZERMA)

IIIA, 10.5.1/01

LR50 >970 g BAS 

650 F/ha

(PMRA, USEPA, 

NZERMA)

48-hour exposure, 

11-day observation 

(dry residues on 

barley seedlings) 

BAS 650 00 F LR50 >9.6 L EP/ha 

or >1962 g a.i./ha

IIIA, 10.5.2/02

BAS 651 00 F LR50 >2.4 L EP/ha 

(PMRA, APVMA, 

USEPA, 

NZERMA)

IIIA, 10.5.2/01

LR50 >717 g BAS 

650 F/ha

(PMRA, USEPA, 

NZERMA)

Predatory 

arthropod

Predaceous mite

(Typhlodromus 

pyri)

Acute contact 7-

day (laboratorytreated glass 

plates)

BAS 650 00 F LR50 >9.6 L EP/ha 

or >1843 g a.i./ha

IIIA, 10.5.1/04

BAS 651 00 F LR50 >3.2 L EP/ha 

(PMRA, APVMA, 

USEPA, 

NZERMA)

IIIA, 10.5.1/02

LR50 >970 g BAS 

650 F/ha

(PMRA, USEPA, 

NZERMA)

Field study 

(Germany): 4 

applications, 68-

day period, MayJune

BAS 650 00 F No adverse effects 

at 4 applications of 

2.4 L EP/ha or 491 

g a.i./ha

IIIA, 10.5.3/01

Field study 

(France): 4 

applications, 63-

day period, AprilJune

BAS 650 00 F Slight/transient 

effects at 4 

applications of 

2.28 L EP/ha or 

468 g a.i./ha

IIIA, 10.5.3/02

Slight/transient 

effects on 

populations

Field study 

(France): 4 

applications, 66-

day period, MayJune

BAS 650 00 F No adverse effects 

at 4 applications of 

2.4 L EP/ha or 491 

g a.i./ha

IIIA, 10.5.3/03

Field study 

(Germany): 4 

applications, 62-

day period, JuneJuly

BAS 650 00 F No adverse effects 

at 4 applications of 

2.4 L EP/ha or 491 

g a.i./ha

IIIA, 10.5.3/04

Field study 

(France): 4 

BAS 650 00 F No adverse effects 

at 4 applications of 

IIIA, 10.5.3/05
84

Table F-1. Summary of toxicity of the end-use products BAS 650 00 F and BAS 651 

00 F to non-target beneficial arthropods.

Organism Exposure Test Substance Endpoint Value Reference / 

Comments

applications, 61-

day period, JuneJuly

2.4 L EP/ha or 491 

g a.i./ha

Field study 

(France): 4 

applications, 60-

day period, JuneJuly

BAS 650 00 F No adverse effects 

at 4 applications of 

2.4 L EP/ha or 491 

g a.i./ha

IIIA, 10.5.3/06

Green lacewing

(Chrysoperlea 

carnea)

Contact, up to 15 

day observation 

(laboratory-treated 

glass plates)

BAS 650 00 F LR50 >3.6 L EP/ha 

or >735.8 g a.i./ha

IIIA, 10.5.1/06

Acute contact 7-

day

BAS 651 00 F LR50 >3.2 L EP/ha 

(PMRA, APVMA, 

USEPA, 

NZERMA)

IIIA, 10.5.1/03

LR50 >956 g BAS 

650 F/ha

(PMRA, USEPA, 

NZERMA)
85

Appendix G. LOCATES Output

Includes the following crop groups: bulb vegetables, cucurbit vegetables, fruiting vegetables, 

tuberous and corm vegetables, and grapes

Species Listing by State with Use Criteria

No species were excluded

Minimum of 1 Acre.

Freshwater, Brackish, Saltwater, Vernal pool, Coastal, Floodplain, Seas. wetland, Perm. wetland

Generic taxon {Amphibian, Arachnid, Bird, Bivalve, Conf/cycds, Coral, Crustacean, Dicot, Ferns, Fish, 

Gastropod, Insect, Lichen, Mammal, Monocot, Reptile}

garlic, onions-dry, onions-green, bittermelons, cantaloupes, cucumbers and pickles, honeydew 

melons, muskmelons and pepinos, other vegetables and melons harvested, pumpkins, squash-all, 

squash-summer, squash-winter, watermelons, eggplant, okra, peppers harvested, peppers other 

than bell (including chile), peppers-bell (excluding pimientos), tomatoes in the open, vegetablesother, artichokes-excluding jerusalem, beets, carrots, cassava, celery, chicory, daikon, dasheens, 

gado, ginger root, ginseng, horseradish, other root crops, potatoes, radishes, sugarbeets for seed, 

sugarbeets for sugar, sweet potatoes, taniers, taro, turnips, yam (lesser), yams, grapes

Alabama ( 74) species: E/T Medium Taxon

Salamander, Frosted Flatwoods (Ambystoma cingulatum) T Terrestrial, 

Amphibian

Freshwater, Vernal 

pool

Salamander, Red Hills (Phaeognathus hubrichti) T Terrestrial, 

Amphibian

Freshwater

Bankclimber, Purple (Elliptoideus sloatianus) T Freshwater Bivalve

Combshell, Southern (=Penitent (Epioblasma penita) E Freshwater Bivalve

mussel)

Combshell, Upland (Epioblasma metastriata) E Freshwater Bivalve

Fanshell (Cyprogenia stegaria) E Freshwater Bivalve

Kidneyshell, Triangular (Ptychobranchus greenii) E Freshwater Bivalve

Mucket, Orange-nacre (Lampsilis perovalis) T Freshwater Bivalve

Mucket, Pink (Pearlymussel) (Lampsilis abrupta) E Freshwater Bivalve

Mussel, Acornshell Southern (Epioblasma othcaloogensis) E Freshwater Bivalve

Mussel, Alabama Moccasinshell (Medionidus acutissimus) T Freshwater Bivalve

Mussel, Coosa Moccasinshell (Medionidus parvulus) E Freshwater Bivalve

Mussel, Cumberland Combshell (Epioblasma brevidens) E Freshwater Bivalve

Mussel, Dark Pigtoe (Pleurobema furvum) E Freshwater Bivalve

Mussel, Fine-lined Pocketbook (Lampsilis altilis) T Freshwater Bivalve

Mussel, Fine-rayed Pigtoe (Fusconaia cuneolus) E Freshwater Bivalve

Mussel, Flat Pigtoe (=Marshall's (Pleurobema marshalli) E Freshwater Bivalve

Mussel)

Mussel, Gulf Moccasinshell (Medionidus penicillatus) E Freshwater Bivalve

Mussel, Heavy Pigtoe (=Judge (Pleurobema taitianum) E Freshwater Bivalve

Tait's Mussel)

Mussel, Heelsplitter Inflated (Potamilus inflatus) T Freshwater Bivalve

Mussel, Oval Pigtoe (Pleurobema pyriforme) E Freshwater Bivalve

Mussel, Ovate Clubshell (Pleurobema perovatum) E Freshwater Bivalve
86

Mussel, Ring Pink (=Golf Stick (Obovaria retusa) E Freshwater Bivalve

Pearly)

Mussel, Rough Pigtoe (Pleurobema plenum) E Freshwater Bivalve

Mussel, Shiny Pigtoe (Fusconaia cor) E Freshwater Bivalve

Mussel, Shiny-rayed Pocketbook (Lampsilis subangulata) E Freshwater Bivalve

Mussel, Southern Clubshell (Pleurobema decisum) E Freshwater Bivalve

Mussel, Southern Pigtoe (Pleurobema georgianum) E Freshwater Bivalve

Pearlymussel, Alabama Lamp (Lampsilis virescens) E Freshwater Bivalve

Pearlymussel, Cracking (Hemistena lata) E Freshwater Bivalve

Pearlymussel, Cumberland (Quadrula intermedia) E Freshwater Bivalve

Monkeyface

Pearlymussel, Orange-footed (Plethobasus cooperianus) E Freshwater Bivalve

Pearlymussel, Pale Lilliput (Toxolasma cylindrellus) E Freshwater Bivalve

Pearlymussel, Turgid-blossom (Epioblasma turgidula) E Freshwater Bivalve

Pearlymussel, White Wartyback (Plethobasus cicatricosus) E Freshwater Bivalve

Stirrupshell (Quadrula stapes) E Freshwater Bivalve

Shrimp, Alabama Cave (Palaemonias alabamae) E Freshwater

Crustacean

Amphianthus, Little (Amphianthus pusillus) T Freshwater Dicot

Harperella (Ptilimnium nodosum) E Freshwater Dicot

Pitcher-plant, Alabama Canebrake (Sarracenia rubra alabamensis) E Terrestrial, Dicot

Freshwater

Pitcher-plant, Green (Sarracenia oreophila) E Terrestrial, Dicot

Freshwater

Quillwort, Louisiana (Isoetes louisianensis) E Terrestrial, Ferns

Freshwater

Cavefish, Alabama (Speoplatyrhinus poulsoni) E Freshwater Fish

Chub, Spotfin (Erimonax monachus) T Freshwater Fish

Darter, Boulder (Etheostoma wapiti) E Freshwater Fish

Darter, Goldline (Percina aurolineata) T Freshwater Fish

Darter, Slackwater (Etheostoma boschungi) T Freshwater Fish

Darter, Snail (Percina tanasi) T Freshwater Fish

Darter, Vermilion (Etheostoma chermocki) E Freshwater Fish

Darter, Watercress (Etheostoma nuchale) E Freshwater Fish

Sculpin, Pygmy (Cottus paulus (=pygmaeus)) T Freshwater Fish

Shiner, Blue (Cyprinella caerulea) T Freshwater Fish

Shiner, Cahaba (Notropis cahabae) E Freshwater Fish

Shiner, Palezone (Notropis albizonatus) E Freshwater Fish

Sturgeon, Alabama (Scaphirhynchus suttkusi) E Freshwater Fish

Sturgeon, Gulf (Acipenser oxyrinchus desotoi) T Freshwater, Fish

Campeloma, Slender (Campeloma decampi) E Freshwater

Gastropod

Elimia, Lacy (Elimia crenatella) T Freshwater

Gastropod

Pebblesnail, Flat (Lepyrium showalteri) E Freshwater

Gastropod

Riversnail, Anthony's (Athearnia anthonyi) E Freshwater

Gastropod

Rocksnail, Painted (Leptoxis taeniata) T Freshwater

Gastropod

Rocksnail, Plicate (Leptoxis plicata) E Freshwater

Gastropod

Rocksnail, Round (Leptoxis ampla) T Freshwater

Gastropod

Snail, Armored (Pyrgulopsis (=Marstonia) pachyta) E Freshwater

Gastropod

Snail, Lioplax Cylindrical (Lioplax cyclostomaformis) E Freshwater

Gastropod

Butterfly, Mitchell's Satyr (Neonympha mitchellii mitchellii) E Terrestrial, Perm. Insect
87

wetland

Dragonfly, Hine's Emerald (Somatochlora hineana) E Terrestrial, Insect

Freshwater

Manatee, West Indian (Trichechus manatus) E Saltwater

Mammal

Mouse, Alabama Beach (Peromyscus polionotus ammobates) E Terrestrial, Coastal

Mammal

Mouse, Perdido Key Beach (Peromyscus polionotus trissyllepsis) E Coastal

Mammal

Bulrush, Northeastern (=Barbed (Scirpus ancistrochaetus) E Terrestrial, 

Monocot

Bristle) Freshwater

Water-plantain, Kral's (Sagittaria secundifolia) T Freshwater

Monocot

Turtle, Alabama Red-bellied (Pseudemys alabamensis) E Terrestrial, Reptile

Freshwater

Turtle, Flattened Musk (Sternotherus depressus) T Terrestrial, Reptile

Freshwater

Alaska ( 4) species: E/T Medium Taxon

Albatross, Short-tailed (Phoebastria (=Diomedea) albatrus) E Terrestrial, Saltwater Bird

Eider, Steller's (Polysticta stelleri) T Terrestrial, Saltwater Bird

Otter, Northern Sea (Enhydra lutris kenyoni) T Saltwater

Mammal

Seal, spotted (Phoca largha) T Saltwater

Mammal

Arizona ( 23) species: E/T Medium Taxon

Frog, Chiricahua Leopard (Rana chiricahuensis) T Terrestrial, 

Amphibian

Freshwater

Salamander, Sonora Tiger (Ambystoma tigrinum stebbinsi) E Terrestrial, 

Amphibian

Freshwater, Vernal 

pool

Umbel, Huachuca Water (Lilaeopsis schaffneriana var. recurva) E Terrestrial, Dicot

Freshwater

Catfish, Yaqui (Ictalurus pricei) T Freshwater Fish

Chub, Bonytail (Gila elegans) E Freshwater Fish

Chub, Gila (Gila intermedia) E Freshwater Fish

Chub, Humpback (Gila cypha) E Freshwater Fish

Chub, Sonora (Gila ditaenia) T Freshwater Fish

Chub, Virgin River (Gila seminuda (=robusta)) E Freshwater Fish

Chub, Yaqui (Gila purpurea) E Freshwater Fish

Minnow, Loach (Tiaroga cobitis) T Freshwater Fish

Pupfish, Desert (Cyprinodon macularius) E Freshwater Fish

Shiner, Beautiful (Cyprinella formosa) T Freshwater Fish

Spikedace (Meda fulgida) T Freshwater Fish

Spinedace, Little Colorado (Lepidomeda vittata) T Freshwater Fish

Squawfish, Colorado (Ptychocheilus lucius) E Freshwater Fish

Steelhead (Oncorhynchus (=Salmo) mykiss) E Freshwater, Fish

Brackish, Saltwater

Sucker, Razorback (Xyrauchen texanus) E Freshwater Fish

Topminnow, Gila (Yaqui) (Poeciliopsis occidentalis) E Freshwater Fish

Trout, Apache (Oncorhynchus apache) T Freshwater Fish

Trout, Gila (Oncorhynchus gilae) E Freshwater Fish

Woundfin (Plagopterus argentissimus) E Freshwater Fish

Ambersnail, Kanab (Oxyloma haydeni kanabensis) E Terrestrial, 

Gastropod

Freshwater
88

Arkansas ( 16) species: E/T Medium Taxon

Fatmucket, Arkansas (Lampsilis powelli) T Freshwater Bivalve

Mucket, Pink (Pearlymussel) (Lampsilis abrupta) E Freshwater Bivalve

Mussel, Scaleshell (Leptodea leptodon) E Freshwater Bivalve

Mussel, Speckled Pocketbook (Lampsilis streckeri) E Freshwater Bivalve

Mussel, Winged Mapleleaf (Quadrula fragosa) E Freshwater Bivalve

Pearlymussel, Curtis' (Epioblasma florentina curtisii) E Freshwater Bivalve

Pearlymussel, Fat Pocketbook (Potamilus capax) E Freshwater Bivalve

Pearlymussel, Turgid-blossom (Epioblasma turgidula) E Freshwater Bivalve

Rock-pocketbook, Ouachita (Arkansia wheeleri) E Freshwater Bivalve

(=Wheeler's pm)

Crayfish, Cave (Cambarus (Cambarus aculabrum) E Freshwater

Crustacean

aculabrum)

Harperella (Ptilimnium nodosum) E Freshwater Dicot

Cavefish, Ozark (Amblyopsis rosae) T Freshwater Fish

Darter, Leopard (Percina pantherina) T Freshwater Fish

Shiner, Arkansas River (Notropis girardi) T Freshwater Fish

Sturgeon, Pallid (Scaphirhynchus albus) E Freshwater Fish

Trout, Bull (Salvelinus confluentus) T Freshwater Fish

California ( 87) species: E/T Medium Taxon

Frog, California Red-legged (Rana aurora draytonii) T Terrestrial, 

Amphibian

Freshwater

Frog, Mountain Yellow-legged (Rana muscosa) E Terrestrial, 

Amphibian

Freshwater

Salamander, California Tiger (Ambystoma californiense) E Terrestrial, Vernal 

Amphibian

pool

Salamander, Desert Slender (Batrachoseps aridus) E Terrestrial, 

Amphibian

Freshwater

Salamander, Santa Cruz Long-toed (Ambystoma macrodactylum croceum) E Terrestrial, 

Amphibian

Freshwater, Vernal 

pool

Toad, Arroyo Southwestern (Bufo californicus (=microscaphus)) E Terrestrial, 

Amphibian

Freshwater

Albatross, Short-tailed (Phoebastria (=Diomedea) albatrus) E Terrestrial, Saltwater Bird

Murrelet, Marbled (Brachyramphus marmoratus) T Terrestrial, Bird

Freshwater, 

Crayfish, Shasta (Pacifastacus fortis) E Freshwater

Crustacean

Fairy Shrimp, Conservancy Fairy (Branchinecta conservatio) E Vernal pool

Crustacean

Fairy Shrimp, Longhorn (Branchinecta longiantenna) E Vernal pool

Crustacean

Fairy Shrimp, Riverside (Streptocephalus woottoni) E Vernal pool

Crustacean

Fairy Shrimp, San Diego (Branchinecta sandiegonensis) E Vernal pool

Crustacean

Fairy Shrimp, Vernal Pool (Branchinecta lynchi) T Vernal pool

Crustacean

Shrimp, California Freshwater (Syncaris pacifica) E Freshwater

Crustacean

Tadpole Shrimp, Vernal Pool (Lepidurus packardi) E Vernal pool

Crustacean

Allocarya, Calistoga (Plagiobothrys strictus) E Vernal pool Dicot
89

Bird's-beak, salt marsh (Cordylanthus maritimus ssp. maritimus) E Saltwater Dicot

Bird's-beak, Soft (Cordylanthus mollis ssp. mollis) E Brackish, Saltwater Dicot

Checker-mallow, Kenwood Marsh (Sidalcea oregana ssp. valida) E Terrestrial Dicot

Clover, Fleshy Owl's (Castilleja campestris ssp. succulenta) T Vernal pool Dicot

Crownscale, San Jacinto Valley (Atriplex coronata var. notatior) E Terrestrial Dicot

Daisy, Parish's (Erigeron parishii) T Freshwater Dicot

Grass, Hairy Orcutt (Orcuttia pilosa) E Vernal pool Dicot

Grass, Sacramento Orcutt (Orcuttia viscida) E Vernal pool Dicot

Grass, Slender Orcutt (Orcuttia tenuis) T Vernal pool Dicot

Howellia, Water (Howellia aquatilis) T Freshwater Dicot

Layia, Beach (Layia carnosa) E Terrestrial, Coastal Dicot

Lupine, Clover (Lupinus tidestromii) E Coastal Dicot

Lupine, Nipomo Mesa (Lupinus nipomensis) E Coastal Dicot

Meadowfoam, Butte County (Limnanthes floccosa ssp. californica) E Vernal pool Dicot

Meadowfoam, Sebastopol (Limnanthes vinculans) E Terrestrial, Dicot

Freshwater

Milk-vetch, Ventura Marsh (Astragalus pycnostachyus var. E Terrestrial, Dicot

lanosissimus) Freshwater

Navarretia, Few-flowered (Navarretia leucocephala ssp. Pauciflora) E Terrestrial, Vernal Dicot

pool

Navarretia, Many-flowered (Navarretia leucocephala ssp. plieantha) E Terrestrial, Vernal Dicot

pool

Navarretia, Spreading (Navarretia fossalis) T Vernal pool Dicot

Sandwort, Marsh (Arenaria paludicola) E Terrestrial, Dicot

Freshwater

Spurge, Hoover's (Chamaesyce hooveri) T Vernal pool Dicot

Stickyseed, Baker's (Blennosperma bakeri) E Vernal pool Dicot

Stonecrop, Lake County (Parvisedum leiocarpum) E Vernal pool Dicot

Thistle, Chorro creek Bog (Cirsium fontinale var. obispoense) E Terrestrial, Dicot

Freshwater

Thistle, La Graciosa (Cirsium loncholepis) E Freshwater, Dicot

Brackish, Coastal

Thistle, Suisun (Cirsium hydrophilum var. hydrophilum) E Terrestrial, Brackish Dicot

Tuctoria, Green's (Tuctoria greenei) E Vernal pool Dicot

Watercress, Gambel's (Rorippa gambellii) E Terrestrial, Dicot

Freshwater, Brackish

Chub, Bonytail (Gila elegans) E Freshwater Fish

Chub, Mohave Tui (Gila bicolor mohavensis) E Freshwater Fish

Chub, Owens Tui (Gila bicolor snyderi) E Freshwater Fish

Goby, Tidewater (Eucyclogobius newberryi) E Freshwater Fish

Pupfish, Desert (Cyprinodon macularius) E Freshwater Fish

Pupfish, Owens (Cyprinodon radiosus) E Freshwater Fish

Salmon, Chinook (Oncorhynchus (=Salmo) tshawytscha) E/T Freshwater, Fish

Brackish, Saltwater

Salmon, Coho (Oncorhynchus (=Salmo) kisutch) E Freshwater, Fish

Brackish, Saltwater

Smelt, Delta (Hypomesus transpacificus) T Freshwater, Brackish Fish

Squawfish, Colorado (Ptychocheilus lucius) E Freshwater Fish

Steelhead (Oncorhynchus (=Salmo) mykiss) E Freshwater, Fish

Brackish, Saltwater

Stickleback, Unarmored (Gasterosteus aculeatus williamsoni) E Freshwater Fish

Threespine

Sturgeon, North American green (Acipenser medirostris) T Freshwater, Fish

Sucker, Lost River (Deltistes luxatus) E Freshwater Fish

Sucker, Modoc (Catostomus microps) E Freshwater Fish

Sucker, Razorback (Xyrauchen texanus) E Freshwater Fish

Sucker, Santa Ana (Catostomus santaanae) T Freshwater Fish

Sucker, Shortnose (Chasmistes brevirostris) E Freshwater Fish
90

Trout, Lahontan Cutthroat (Oncorhynchus clarki henshawi) T Freshwater Fish

Trout, Little Kern Golden (Oncorhynchus aguabonita whitei) T Freshwater Fish

Trout, Paiute Cutthroat (Oncorhynchus clarki seleniris) T Freshwater Fish

Abalone, White (Haliotis sorenseni) E Saltwater

Gastropod

Beetle, Delta Green Ground (Elaphrus viridis) T Terrestrial, Vernal Insect

pool

Mountain Beaver, Point Arena (Aplodontia rufa nigra) E Terrestrial, 

Mammal

Freshwater

Otter, Southern Sea (Enhydra lutris nereis) T Saltwater

Mammal

Seal, Guadalupe Fur (Arctocephalus townsendi) T Saltwater, Coastal

Mammal

Sea-lion, Steller (Eumetopias jubatus) E/T Saltwater, Coastal

Mammal

Whale, Finback (Balaenoptera physalus) E Saltwater

Mammal

Whale, Humpback (Megaptera novaeangliae) E Saltwater

Mammal

Whale, North Atlantic right (Eubalaena glacialis (incl. australis)) E Saltwater

Mammal

Whale, Sei (Balaenoptera borealis) E Saltwater

Mammal

Whale, Sperm (Physeter catodon (=macrocephalus)) E Saltwater

Mammal

Alopecurus, Sonoma (Alopecurus aequalis var. sonomensis) E Terrestrial

Monocot

Bluegrass, Napa (Poa napensis) E Terrestrial, 

Monocot

Freshwater

Grass, California Orcutt (Orcuttia californica) E Terrestrial, Vernal 

Monocot

pool

Grass, Colusa (Neostapfia colusana) T Vernal pool

Monocot

Grass, San Joaquin Valley Orcutt (Orcuttia inaequalis) T Vernal pool

Monocot

Grass, Solano (Tuctoria mucronata) E Terrestrial, Vernal 

Monocot

pool

Lily, Pitkin Marsh (Lilium pardalinum ssp. pitkinense) E Freshwater

Monocot

Sedge, White (Carex albida) E Terrestrial,

Monocot

Freshwater

Snake, Giant Garter (Thamnophis gigas) T Terrestrial, Reptile

Freshwater

Snake, San Francisco Garter (Thamnophis sirtalis tetrataenia) E Terrestrial, Reptile

Freshwater

Colorado ( 8) species: E/T Medium Taxon

Crane, Whooping (Grus americana) E Terrestrial, Bird

Freshwater

Mustard, Penland Alpine Fen (Eutrema penlandii) T Terrestrial, Dicot

Freshwater

Chub, Bonytail (Gila elegans) E Freshwater Fish

Chub, Humpback (Gila cypha) E Freshwater Fish

Squawfish, Colorado (Ptychocheilus lucius) E Freshwater Fish

Sturgeon, Pallid (Scaphirhynchus albus) E Freshwater Fish

Sucker, Razorback (Xyrauchen texanus) E Freshwater Fish

Trout, Greenback Cutthroat (Oncorhynchus clarki stomias) T Freshwater Fish
91

Connecticut ( 3) species: E/T Medium Taxon

Mussel, Dwarf Wedge (Alasmidonta heterodon) E Freshwater Bivalve

Beetle, Puritan Tiger (Cicindela puritana) T Terrestrial, Coastal Insect

Turtle, Bog (Clemmys muhlenbergii) T Terrestrial, Reptile

Freshwater

Delaware ( 2) species: E/T Medium Taxon

Amaranth, Seabeach (Amaranthus pumilus) T Coastal Dicot

Turtle, Bog (Clemmys muhlenbergii) T Terrestrial, Reptile

Freshwater

Florida ( 28) species: E/T Medium Taxon

Salamander, Frosted Flatwoods (Ambystoma cingulatum) T Terrestrial, 

Amphibian

Freshwater, Vernal 

pool

Crane, Whooping (Grus americana) E Terrestrial, Bird

Freshwater

Bankclimber, Purple (Elliptoideus sloatianus) T Freshwater Bivalve

Mussel, Fat Threeridge (Amblema neislerii) E Freshwater Bivalve

Mussel, Gulf Moccasinshell (Medionidus penicillatus) E Freshwater Bivalve

Mussel, Ochlockonee (Medionidus simpsonianus) E Freshwater Bivalve

Moccasinshell

Mussel, Oval Pigtoe (Pleurobema pyriforme) E Freshwater Bivalve

Mussel, Shiny-rayed Pocketbook (Lampsilis subangulata) E Freshwater Bivalve

Slabshell, Chipola (Elliptio chipolaensis) T Freshwater Bivalve

Shrimp, Squirrel Chimney Cave (Palaemonetes cummingi) T Freshwater, 

Crustacean

Subterraneous

Butterwort, Godfrey's (Pinguicula ionantha) T Terrestrial, Dicot

Freshwater

Jacquemontia, Beach (Jacquemontia reclinata) E Terrestrial, Coastal Dicot

Darter, Okaloosa (Etheostoma okaloosae) E Freshwater Fish

Sawfish, Smalltooth (Pristis pectinata) E Freshwater, Fish

Brackish, Saltwater

Sturgeon, Gulf (Acipenser oxyrinchus desotoi) T Freshwater, Fish

Sturgeon, Shortnose (Acipenser brevirostrum) E Freshwater, Fish

Manatee, West Indian (Trichechus manatus) E Saltwater

Mammal

Mouse, Anastasia Island Beach (Peromyscus polionotus phasma) E Terrestrial, Coastal

Mammal

Mouse, Choctawhatchee Beach (Peromyscus polionotus allophrys) E Terrestrial, Coastal

Mammal

Mouse, Perdido Key Beach (Peromyscus polionotus trissyllepsis) E Coastal

Mammal

Mouse, Southeastern Beach (Peromyscus polionotus niveiventris) T Terrestrial, Coastal

Mammal

Mouse, St. Andrew Beach (Peromyscus polionotus peninsularis) E Terrestrial, Coastal

Mammal

Vole, Florida Salt Marsh (Microtus pennsylvanicus dukecampbelli) E Terrestrial, Brackish

Mammal

Beauty, Harper's (Harperocallis flava) E Terrestrial, 

Monocot

Freshwater

Seagrass, Johnson's (Halophila johnsonii) T Saltwater, Coastal

Monocot

Alligator, American (Alligator mississippiensis) T Terrestrial, Reptile

Freshwater, Brackish

Crocodile, American (Crocodylus acutus) T Terrestrial, Reptile

Freshwater

Snake, Atlantic Salt Marsh (Nerodia clarkii taeniata) T Terrestrial, Brackish, Reptile
92

Saltwater

Georgia ( 37) species: E/T Medium Taxon

Salamander, Frosted Flatwoods (Ambystoma cingulatum) T Terrestrial, 

Amphibian

Freshwater, Vernal 

pool

Bankclimber, Purple (Elliptoideus sloatianus) T Freshwater Bivalve

Combshell, Upland (Epioblasma metastriata) E Freshwater Bivalve

Kidneyshell, Triangular (Ptychobranchus greenii) E Freshwater Bivalve

Mussel, Acornshell Southern (Epioblasma othcaloogensis) E Freshwater Bivalve

Mussel, Alabama Moccasinshell (Medionidus acutissimus) T Freshwater Bivalve

Mussel, Coosa Moccasinshell (Medionidus parvulus) E Freshwater Bivalve

Mussel, Fat Threeridge (Amblema neislerii) E Freshwater Bivalve

Mussel, Fine-lined Pocketbook (Lampsilis altilis) T Freshwater Bivalve

Mussel, Gulf Moccasinshell (Medionidus penicillatus) E Freshwater Bivalve

Mussel, Ochlockonee (Medionidus simpsonianus) E Freshwater Bivalve

Moccasinshell

Mussel, Oval Pigtoe (Pleurobema pyriforme) E Freshwater Bivalve

Mussel, Ovate Clubshell (Pleurobema perovatum) E Freshwater Bivalve

Mussel, Shiny-rayed Pocketbook (Lampsilis subangulata) E Freshwater Bivalve

Mussel, Southern Clubshell (Pleurobema decisum) E Freshwater Bivalve

Mussel, Southern Pigtoe (Pleurobema georgianum) E Freshwater Bivalve

Amphianthus, Little (Amphianthus pusillus) T Freshwater Dicot

Dropwort, Canby's (Oxypolis canbyi) E Terrestrial, Dicot

Freshwater

Harperella (Ptilimnium nodosum) E Freshwater Dicot

Pitcher-plant, Green (Sarracenia oreophila) E Terrestrial, Dicot

Freshwater

Quillwort, Black-spored (Isoetes melanospora) E Vernal pool Ferns

Quillwort, Mat-forming (Isoetes tegetiformans) E Vernal pool Ferns

Darter, Amber (Percina antesella) E Freshwater Fish

Darter, Cherokee (Etheostoma scotti) T Freshwater Fish

Darter, Etowah (Etheostoma etowahae) E Freshwater Fish

Darter, Goldline (Percina aurolineata) T Freshwater Fish

Darter, Snail (Percina tanasi) T Freshwater Fish

Logperch, Conasauga (Percina jenkinsi) E Freshwater Fish

Shiner, Blue (Cyprinella caerulea) T Freshwater Fish

Sturgeon, Shortnose (Acipenser brevirostrum) E Freshwater, Fish

Snail, Lioplax Cylindrical (Lioplax cyclostomaformis) E Freshwater

Gastropod

Manatee, West Indian (Trichechus manatus) E Saltwater

Mammal

Whale, Humpback (Megaptera novaeangliae) E Saltwater

Mammal

Whale, North Atlantic right (Eubalaena glacialis (incl. australis)) E Saltwater

Mammal

Pink, Swamp (Helonias bullata) T Terrestrial, 

Monocot

Freshwater

Water-plantain, Kral's (Sagittaria secundifolia) T Freshwater

Monocot

Turtle, Bog (Clemmys muhlenbergii) T Terrestrial, Reptile

Freshwater

Guam ( 4) species: E/T Medium Taxon

Sea turtle, green (Chelonia mydas) E/T Saltwater Reptile

Sea turtle, hawksbill (Eretmochelys imbricata) E Saltwater, Coastal Reptile

Sea turtle, leatherback (Dermochelys coriacea) E Saltwater, Coastal Reptile

Sea turtle, loggerhead (Caretta caretta) T Saltwater, Coastal Reptile
93

Hawaii ( 7) species: E/T Medium Taxon

Duck, Hawaiian (Koloa) (Anas wyvilliana) E Terrestrial, Bird

Freshwater

Goose, Hawaiian (Nene) (Branta (=Nesochen) sandvicensis) E Terrestrial, Bird

Freshwater

Shearwater, Newell's Townsend's (Puffinus auricularis newelli) T Terrestrial, Saltwater Bird

Amphipod, Kauai Cave (Spelaeorchestia koloana) E Freshwater, 

Crustacean

Subterraneous

'Ihi'Ihi (Marsilea villosa) (Marsilea villosa) E Terrestrial, Vernal Ferns

pool

Snail, Newcomb's (Erinna newcombi) T Freshwater

Gastropod

Seal, Hawaiian Monk (Monachus schauinslandi) E Saltwater, Coastal

Mammal

Idaho ( 10) species: E/T Medium Taxon

Howellia, Water (Howellia aquatilis) T Freshwater Dicot

Peppergrass, Slick Spot (Lepidium papilliferum) T Terrestrial, Dicot

Salmon, Chinook (Oncorhynchus (=Salmo) tshawytscha) E/T Freshwater, Fish

Brackish, Saltwater

Salmon, Sockeye (Oncorhynchus (=Salmo) nerka) E Freshwater, Fish

Brackish, Saltwater

Steelhead (Oncorhynchus (=Salmo) mykiss) E Freshwater, Fish

Brackish, Saltwater

Sturgeon, White (Acipenser transmontanus) E Freshwater, Fish

Trout, Bull (Salvelinus confluentus) T Freshwater Fish

Limpet, Banbury Springs (Lanx sp.) E Freshwater

Gastropod

Snail, Bliss Rapids (Taylorconcha serpenticola) T Freshwater

Gastropod

Springsnail, Bruneau Hot (Pyrgulopsis bruneauensis) E Freshwater

Gastropod

Illinois ( 11) species: E/T Medium Taxon

Fanshell (Cyprogenia stegaria) E Freshwater Bivalve

Mucket, Pink (Pearlymussel) (Lampsilis abrupta) E Freshwater Bivalve

Mussel, Clubshell (Pleurobema clava) E Freshwater Bivalve

Pearlymussel, Fat Pocketbook (Potamilus capax) E Freshwater Bivalve

Pearlymussel, Higgins' Eye (Lampsilis higginsii) E Freshwater Bivalve

Pearlymussel, Orange-footed (Plethobasus cooperianus) E Freshwater Bivalve

Amphipod, Illinois Cave (Gammarus acherondytes) E Freshwater, 

Crustacean

Subterraneous

Aster, Decurrent False (Boltonia decurrens) T Terrestrial, Dicot

Freshwater

Daisy, Lakeside (Hymenoxys herbacea) T Freshwater Dicot

Sturgeon, Pallid (Scaphirhynchus albus) E Freshwater Fish

Dragonfly, Hine's Emerald (Somatochlora hineana) E Terrestrial, Insect

Freshwater

Indiana ( 9) species: E/T Medium Taxon

Fanshell (Cyprogenia stegaria) E Freshwater Bivalve

Mucket, Pink (Pearlymussel) (Lampsilis abrupta) E Freshwater Bivalve

Mussel, Clubshell (Pleurobema clava) E Freshwater Bivalve

Mussel, Rough Pigtoe (Pleurobema plenum) E Freshwater Bivalve

Pearlymussel, Fat Pocketbook (Potamilus capax) E Freshwater Bivalve

Pearlymussel, White Cat's Paw (Epioblasma obliquata perobliqua) E Freshwater Bivalve

Riffleshell, Northern (Epioblasma torulosa rangiana) E Freshwater Bivalve

Butterfly, Mitchell's Satyr (Neonympha mitchellii mitchellii) E Terrestrial, Perm. Insect
94

Snake, Northern Copperbelly Water(Nerodia erythrogaster neglecta) T Terrestrial, Reptile

Freshwater

Iowa ( 4) species: E/T Medium Taxon

Mussel, Dwarf Wedge (Alasmidonta heterodon) E Freshwater Bivalve

Pearlymussel, Higgins' Eye (Lampsilis higginsii) E Freshwater Bivalve

Shiner, Topeka (Notropis topeka (=tristis)) E Freshwater Fish

Sturgeon, Pallid (Scaphirhynchus albus) E Freshwater Fish

Kansas ( 5) species: E/T Medium Taxon

Crane, Whooping (Grus americana) E Terrestrial, Bird

Freshwater

Madtom, Neosho (Noturus placidus) T Freshwater Fish

Shiner, Arkansas River (Notropis girardi) T Freshwater Fish

Shiner, Topeka (Notropis topeka (=tristis)) E Freshwater Fish

Sturgeon, Pallid (Scaphirhynchus albus) E Freshwater Fish

Kentucky ( 27) species: E/T Medium Taxon

Fanshell (Cyprogenia stegaria) E Freshwater Bivalve

Mucket, Pink (Pearlymussel) (Lampsilis abrupta) E Freshwater Bivalve

Mussel, Clubshell (Pleurobema clava) E Freshwater Bivalve

Mussel, Cumberland Combshell (Epioblasma brevidens) E Freshwater Bivalve

Mussel, Cumberland Elktoe (Alasmidonta atropurpurea) E Freshwater Bivalve

Mussel, Oyster (Epioblasma capsaeformis) E Freshwater Bivalve

Mussel, Ring Pink (=Golf Stick (Obovaria retusa) E Freshwater Bivalve

Pearly)

Mussel, Rough Pigtoe (Pleurobema plenum) E Freshwater Bivalve

Mussel, Winged Mapleleaf (Quadrula fragosa) E Freshwater Bivalve

Pearlymussel, Appalachian (Quadrula sparsa) E Freshwater Bivalve

Monkeyface

Pearlymussel, Cracking (Hemistena lata) E Freshwater Bivalve

Pearlymussel, Cumberland Bean (Villosa trabalis) E Freshwater Bivalve

Pearlymussel, Dromedary (Dromus dromas) E Freshwater Bivalve

Pearlymussel, Fat Pocketbook (Potamilus capax) E Freshwater Bivalve

Pearlymussel, Little-wing (Pegias fabula) E Freshwater Bivalve

Pearlymussel, Orange-footed (Plethobasus cooperianus) E Freshwater Bivalve

Pearlymussel, Purple Cat's Paw (Epioblasma obliquata obliquata) E Freshwater Bivalve

Pearlymussel, Tubercled- (Epioblasma torulosa torulosa) E Freshwater Bivalve

Pearlymussel, White Wartyback (Plethobasus cicatricosus) E Freshwater Bivalve

Pearlymussel, Yellow-blossom (Epioblasma florentina florentina) E Freshwater Bivalve

Riffleshell, Northern (Epioblasma torulosa rangiana) E Freshwater Bivalve

Riffleshell, Tan (Epioblasma florentina walkeri (=E. E Freshwater Bivalve

Shrimp, Kentucky Cave (Palaemonias ganteri) E Freshwater

Crustacean

Dace, Blackside (Phoxinus cumberlandensis) T Freshwater Fish

Darter, Relict (Etheostoma chienense) E Freshwater Fish

Shiner, Palezone (Notropis albizonatus) E Freshwater Fish

Sturgeon, Pallid (Scaphirhynchus albus) E Freshwater Fish

Louisiana ( 8) species: E/T Medium Taxon

Mucket, Pink (Pearlymussel) (Lampsilis abrupta) E Freshwater Bivalve

Mussel, Heelsplitter Inflated (Potamilus inflatus) T Freshwater Bivalve

Pearlshell, Louisiana (Margaritifera hembeli) T Freshwater Bivalve

Quillwort, Louisiana (Isoetes louisianensis) E Terrestrial, Ferns

Freshwater

Sturgeon, Gulf (Acipenser oxyrinchus desotoi) T Freshwater, Fish

Sturgeon, Pallid (Scaphirhynchus albus) E Freshwater Fish

Manatee, West Indian (Trichechus manatus) E Saltwater

Mammal
95

Turtle, Ringed Map (Graptemys oculifera) T Terrestrial, Reptile

Freshwater

Maine ( 2) species: E/T Medium Taxon

Salmon, Atlantic (Salmo salar) E Freshwater, Fish

Brackish, Saltwater

Sturgeon, Shortnose (Acipenser brevirostrum) E Freshwater, Fish

Maryland ( 10) species: E/T Medium Taxon

Mussel, Dwarf Wedge (Alasmidonta heterodon) E Freshwater Bivalve

Amaranth, Seabeach (Amaranthus pumilus) T Coastal Dicot

Dropwort, Canby's (Oxypolis canbyi) E Terrestrial, Dicot

Freshwater

Harperella (Ptilimnium nodosum) E Freshwater Dicot

Joint-vetch, Sensitive (Aeschynomene virginica) T Terrestrial, Brackish Dicot

Darter, Maryland (Etheostoma sellare) E Freshwater Fish

Beetle, Puritan Tiger (Cicindela puritana) T Terrestrial, Coastal Insect

Bulrush, Northeastern (=Barbed (Scirpus ancistrochaetus) E Terrestrial, 

Monocot

Bristle) Freshwater

Pink, Swamp (Helonias bullata) T Terrestrial, 

Monocot

Freshwater

Turtle, Bog (Clemmys muhlenbergii) T Terrestrial, Reptile

Freshwater

Massachusetts ( 5) species: E/T Medium Taxon

Mussel, Dwarf Wedge (Alasmidonta heterodon) E Freshwater Bivalve

Sturgeon, Shortnose (Acipenser brevirostrum) E Freshwater, Fish

Beetle, Puritan Tiger (Cicindela puritana) T Terrestrial, Coastal Insect

Bulrush, Northeastern (=Barbed (Scirpus ancistrochaetus) E Terrestrial, 

Monocot

Bristle) Freshwater

Turtle, Bog (Clemmys muhlenbergii) T Terrestrial, Reptile

Freshwater

Michigan ( 8) species: E/T Medium Taxon

Mussel, Clubshell (Pleurobema clava) E Freshwater Bivalve

Riffleshell, Northern (Epioblasma torulosa rangiana) E Freshwater Bivalve

Daisy, Lakeside (Hymenoxys herbacea) T Freshwater Dicot

Monkey-flower, Michigan (Mimulus glabratus var. michiganensis) E Terrestrial, Dicot

Freshwater

Beetle, Hungerford's Crawling (Brychius hungerfordi) E Freshwater Insect

Water

Butterfly, Mitchell's Satyr (Neonympha mitchellii mitchellii) E Terrestrial, Perm. Insect

wetland

Dragonfly, Hine's Emerald (Somatochlora hineana) E Terrestrial, Insect

Freshwater

Snake, Northern Copperbelly Water(Nerodia erythrogaster neglecta) T Terrestrial, Reptile

Freshwater

Minnesota ( 3) species: E/T Medium Taxon

Mussel, Winged Mapleleaf (Quadrula fragosa) E Freshwater Bivalve

Pearlymussel, Higgins' Eye (Lampsilis higginsii) E Freshwater Bivalve

Shiner, Topeka (Notropis topeka (=tristis)) E Freshwater Fish

Mississippi ( 20) species: E/T Medium Taxon

Frog, Dusky Gopher (Mississippi (Rana capito sevosa) E Terrestrial, 

Amphibian

DPS) Freshwater

Crane, Mississippi Sandhill (Grus canadensis pulla) E Terrestrial, Bird
96

Freshwater

Combshell, Southern (=Penitent (Epioblasma penita) E Freshwater Bivalve

mussel)

Mucket, Orange-nacre (Lampsilis perovalis) T Freshwater Bivalve

Mussel, Alabama Moccasinshell (Medionidus acutissimus) T Freshwater Bivalve

Mussel, Black (=Curtus' Mussel) (Pleurobema curtum) E Freshwater Bivalve

Clubshell

Mussel, Cumberland Combshell (Epioblasma brevidens) E Freshwater Bivalve

Mussel, Heavy Pigtoe (=Judge (Pleurobema taitianum) E Freshwater Bivalve

Tait's Mussel)

Mussel, Heelsplitter Inflated (Potamilus inflatus) T Freshwater Bivalve

Mussel, Ovate Clubshell (Pleurobema perovatum) E Freshwater Bivalve

Mussel, Southern Clubshell (Pleurobema decisum) E Freshwater Bivalve

Pearlymussel, Fat Pocketbook (Potamilus capax) E Freshwater Bivalve

Quillwort, Louisiana (Isoetes louisianensis) E Terrestrial, Ferns

Freshwater

Darter, Bayou (Etheostoma rubrum) T Freshwater Fish

Sturgeon, Gulf (Acipenser oxyrinchus desotoi) T Freshwater, Fish

Sturgeon, Pallid (Scaphirhynchus albus) E Freshwater Fish

Manatee, West Indian (Trichechus manatus) E Saltwater

Mammal

Turtle, Alabama Red-bellied (Pseudemys alabamensis) E Terrestrial, Reptile

Freshwater

Turtle, Ringed Map (Graptemys oculifera) T Terrestrial, Reptile

Freshwater

Turtle, Yellow-blotched Map (Graptemys flavimaculata) T Terrestrial, Reptile

Freshwater

Missouri ( 15) species: E/T Medium Taxon

Mucket, Pink (Pearlymussel) (Lampsilis abrupta) E Freshwater Bivalve

Mussel, Scaleshell (Leptodea leptodon) E Freshwater Bivalve

Mussel, Winged Mapleleaf (Quadrula fragosa) E Freshwater Bivalve

Pearlymussel, Curtis' (Epioblasma florentina curtisii) E Freshwater Bivalve

Pearlymussel, Fat Pocketbook (Potamilus capax) E Freshwater Bivalve

Pearlymussel, Higgins' Eye (Lampsilis higginsii) E Freshwater Bivalve

Aster, Decurrent False (Boltonia decurrens) T Terrestrial, Dicot

Freshwater

Sneezeweed, Virginia (Helenium virginicum) T Vernal pool Dicot

Cavefish, Ozark (Amblyopsis rosae) T Freshwater Fish

Darter, Niangua (Etheostoma nianguae) T Freshwater Fish

Madtom, Neosho (Noturus placidus) T Freshwater Fish

Shiner, Topeka (Notropis topeka (=tristis)) E Freshwater Fish

Sturgeon, Pallid (Scaphirhynchus albus) E Freshwater Fish

Cavesnail, Tumbling Creek (Antrobia culveri) E Freshwater, 

Gastropod

Subterraneous

Dragonfly, Hine's Emerald (Somatochlora hineana) E Terrestrial, Insect

Freshwater

Montana ( 4) species: E/T Medium Taxon

Crane, Whooping (Grus americana) E Terrestrial, Bird

Freshwater

Howellia, Water (Howellia aquatilis) T Freshwater Dicot

Sturgeon, Pallid (Scaphirhynchus albus) E Freshwater Fish

Trout, Bull (Salvelinus confluentus) T Freshwater Fish

Nebraska ( 3) species: E/T Medium Taxon

Crane, Whooping (Grus americana) E Terrestrial, Bird

Freshwater
97

Shiner, Topeka (Notropis topeka (=tristis)) E Freshwater Fish

Sturgeon, Pallid (Scaphirhynchus albus) E Freshwater Fish

Nevada ( 23) species: E/T Medium Taxon

Poolfish, Pahrump (= Pahrump (Empetrichthys latos) E Freshwater Dicot

Killifish)

Chub, Humpback (Gila cypha) E Freshwater Fish

Chub, Pahranagat Roundtail (Gila robusta jordani) E Freshwater Fish

Chub, Virgin River (Gila seminuda (=robusta)) E Freshwater Fish

Cui-ui (Chasmistes cujus) E Freshwater Fish

Dace, Ash Meadows Speckled (Rhinichthys osculus nevadensis) E Freshwater Fish

Dace, Clover Valley Speckled (Rhinichthys osculus oligoporus) E Freshwater Fish

Dace, Desert (Eremichthys acros) T Freshwater Fish

Dace, Independence Valley (Rhinichthys osculus lethoporus) E Freshwater Fish

Speckled

Dace, Moapa (Moapa coriacea) E Freshwater Fish

Pupfish, Ash Meadows Amargosa (Cyprinodon nevadensis mionectes) E Freshwater Fish

Pupfish, Devils Hole (Cyprinodon diabolis) E Freshwater Fish

Pupfish, Warm Springs (Cyprinodon nevadensis pectoralis) E Freshwater Fish

Spinedace, Big Spring (Lepidomeda mollispinis pratensis) T Freshwater Fish

Spinedace, White River (Lepidomeda albivallis) E Freshwater Fish

Springfish, Hiko White River (Crenichthys baileyi grandis) E Freshwater Fish

Springfish, Railroad Valley (Crenichthys nevadae) T Freshwater Fish

Springfish, White River (Crenichthys baileyi baileyi) E Freshwater Fish

Sucker, Razorback (Xyrauchen texanus) E Freshwater Fish

Sucker, Warner (Catostomus warnerensis) T Freshwater Fish

Trout, Bull (Salvelinus confluentus) T Freshwater Fish

Trout, Lahontan Cutthroat (Oncorhynchus clarki henshawi) T Freshwater Fish

Woundfin (Plagopterus argentissimus) E Freshwater Fish

New Hampshire ( 2) species: E/T Medium Taxon

Mussel, Dwarf Wedge (Alasmidonta heterodon) E Freshwater Bivalve

Bulrush, Northeastern (=Barbed (Scirpus ancistrochaetus) E Terrestrial, 

Monocot

Bristle) Freshwater

New Jersey ( 5) species: E/T Medium Taxon

Mussel, Dwarf Wedge (Alasmidonta heterodon) E Freshwater Bivalve

Amaranth, Seabeach (Amaranthus pumilus) T Coastal Dicot

Joint-vetch, Sensitive (Aeschynomene virginica) T Terrestrial, Brackish Dicot

Pink, Swamp (Helonias bullata) T Terrestrial, 

Monocot

Freshwater

Turtle, Bog (Clemmys muhlenbergii) T Terrestrial, Reptile

Freshwater

New Mexico ( 20) species: E/T Medium Taxon

Frog, Chiricahua Leopard (Rana chiricahuensis) T Terrestrial, 

Amphibian

Freshwater

Amphipod, Noel's (Gammarus desperatus) E Freshwater

Crustacean

Isopod, Socorro (Thermosphaeroma thermophilus) E Freshwater

Crustacean

Sunflower, Pecos (Helianthus paradoxus) T Terrestrial, Perm. Dicot

wetland

Chub, Chihuahua (Gila nigrescens) T Freshwater Fish

Chub, Gila (Gila intermedia) E Freshwater Fish

Gambusia, Pecos (Gambusia nobilis) E Freshwater Fish

Minnow, Loach (Tiaroga cobitis) T Freshwater Fish
98

Minnow, Rio Grande Silvery (Hybognathus amarus) E Freshwater Fish

Shiner, Arkansas River (Notropis girardi) T Freshwater Fish

Shiner, Beautiful (Cyprinella formosa) T Freshwater Fish

Shiner, Pecos Bluntnose (Notropis simus pecosensis) T Freshwater Fish

Spikedace (Meda fulgida) T Freshwater Fish

Squawfish, Colorado (Ptychocheilus lucius) E Freshwater Fish

Sucker, Razorback (Xyrauchen texanus) E Freshwater Fish

Topminnow, Gila (Yaqui) (Poeciliopsis occidentalis) E Freshwater Fish

Trout, Gila (Oncorhynchus gilae) E Freshwater Fish

Snail, Pecos Assiminea (Assiminea pecos) E Freshwater

Gastropod

Springsnail, Alamosa (Tryonia alamosae) E Freshwater

Gastropod

Springsnail, Roswell (Pyrgulopsis roswellensis) E Freshwater

Gastropod

New York ( 6) species: E/T Medium Taxon

Mussel, Clubshell (Pleurobema clava) E Freshwater Bivalve

Mussel, Dwarf Wedge (Alasmidonta heterodon) E Freshwater Bivalve

Amaranth, Seabeach (Amaranthus pumilus) T Coastal Dicot

Sturgeon, Shortnose (Acipenser brevirostrum) E Freshwater, Fish

Snail, Chittenango Ovate Amber (Succinea chittenangoensis) T Terrestrial, 

Gastropod

Freshwater

Turtle, Bog (Clemmys muhlenbergii) T Terrestrial, Reptile

Freshwater

North Carolina ( 24) species: E/T Medium Taxon

Elktoe, Appalachian (Alasmidonta raveneliana) E Freshwater Bivalve

Mussel, Dwarf Wedge (Alasmidonta heterodon) E Freshwater Bivalve

Mussel, Heelsplitter Carolina (Lasmigona decorata) E Freshwater Bivalve

Pearlymussel, Cumberland Bean (Villosa trabalis) E Freshwater Bivalve

Pearlymussel, Little-wing (Pegias fabula) E Freshwater Bivalve

Riffleshell, Tan (Epioblasma florentina walkeri (=E. E Freshwater Bivalve

Spinymussel, James River (Pleurobema collina) E Freshwater Bivalve

Spinymussel, Tar River (Elliptio steinstansana) E Freshwater Bivalve

Amaranth, Seabeach (Amaranthus pumilus) T Coastal Dicot

Dropwort, Canby's (Oxypolis canbyi) E Terrestrial, Dicot

Freshwater

Harperella (Ptilimnium nodosum) E Freshwater Dicot

Joint-vetch, Sensitive (Aeschynomene virginica) T Terrestrial, Brackish Dicot

Pitcher-plant, Green (Sarracenia oreophila) E Terrestrial, Dicot

Freshwater

Pitcher-plant, Mountain Sweet (Sarracenia rubra ssp. jonesii) E Terrestrial, Dicot

Freshwater

Chub, Spotfin (Erimonax monachus) T Freshwater Fish

Logperch, Roanoke (Percina rex) E Freshwater Fish

Shiner, Cape Fear (Notropis mekistocholas) E Freshwater Fish

Silverside, Waccamaw (Menidia extensa) T Freshwater Fish

Sturgeon, Shortnose (Acipenser brevirostrum) E Freshwater, Fish

Manatee, West Indian (Trichechus manatus) E Saltwater

Mammal

Arrowhead, Bunched (Sagittaria fasciculata) E Freshwater

Monocot

Pink, Swamp (Helonias bullata) T Terrestrial, 

Monocot

Freshwater

Alligator, American (Alligator mississippiensis) T Terrestrial, Reptile

Freshwater, Brackish

Turtle, Bog (Clemmys muhlenbergii) T Terrestrial, Reptile
99

Freshwater

North Dakota ( 2) species: E/T Medium Taxon

Crane, Whooping (Grus americana) E Terrestrial, Bird

Freshwater

Sturgeon, Pallid (Scaphirhynchus albus) E Freshwater Fish

Ohio ( 11) species: E/T Medium Taxon

Fanshell (Cyprogenia stegaria) E Freshwater Bivalve

Mucket, Pink (Pearlymussel) (Lampsilis abrupta) E Freshwater Bivalve

Mussel, Clubshell (Pleurobema clava) E Freshwater Bivalve

Pearlymussel, Purple Cat's Paw (Epioblasma obliquata obliquata) E Freshwater Bivalve

Pearlymussel, White Cat's Paw (Epioblasma obliquata perobliqua) E Freshwater Bivalve

Riffleshell, Northern (Epioblasma torulosa rangiana) E Freshwater Bivalve

Daisy, Lakeside (Hymenoxys herbacea) T Freshwater Dicot

Madtom, Scioto (Noturus trautmani) E Freshwater Fish

Butterfly, Mitchell's Satyr (Neonympha mitchellii mitchellii) E Terrestrial, Perm. Insect

wetland

Snake, Lake Erie Water (Nerodia sipedon insularum) T Terrestrial, Reptile

Freshwater

Snake, Northern Copperbelly Water(Nerodia erythrogaster neglecta) T Terrestrial, Reptile

Freshwater

Oklahoma ( 9) species: E/T Medium Taxon

Crane, Whooping (Grus americana) E Terrestrial, Bird

Freshwater

Mussel, Scaleshell (Leptodea leptodon) E Freshwater Bivalve

Mussel, Winged Mapleleaf (Quadrula fragosa) E Freshwater Bivalve

Rock-pocketbook, Ouachita (Arkansia wheeleri) E Freshwater Bivalve

(=Wheeler's pm)

Cavefish, Ozark (Amblyopsis rosae) T Freshwater Fish

Darter, Leopard (Percina pantherina) T Freshwater Fish

Madtom, Neosho (Noturus placidus) T Freshwater Fish

Shiner, Arkansas River (Notropis girardi) T Freshwater Fish

Alligator, American (Alligator mississippiensis) T Terrestrial, Reptile

Freshwater, Brackish

Oregon ( 22) species: E/T Medium Taxon

Albatross, Short-tailed (Phoebastria (=Diomedea) albatrus) E Terrestrial, Saltwater Bird

Murrelet, Marbled (Brachyramphus marmoratus) T Terrestrial, Bird

Freshwater, 

Fairy Shrimp, Vernal Pool (Branchinecta lynchi) T Vernal pool

Crustacean

Howellia, Water (Howellia aquatilis) T Freshwater Dicot

Lomatium, Bradshaw's (Lomatium bradshawii) E Terrestrial, Dicot

Freshwater

Lomatium, Cook's (Lomatium cookii) E Vernal pool Dicot

Meadowfoam, Large-flowered (Limnanthes floccosa ssp. Grandiflora) E Vernal pool Dicot

Woolly

Popcornflower, Rough (Plagiobothrys hirtus) E Vernal pool Dicot

Chub, Hutton Tui (Gila bicolor ssp.) T Freshwater Fish

Chub, Oregon (Oregonichthys crameri) E Freshwater Fish

Dace, Foskett Speckled (Rhinichthys osculus ssp.) T Freshwater Fish

Salmon, Chinook (Oncorhynchus (=Salmo) tshawytscha) E/T Freshwater, Fish

Brackish, Saltwater

Salmon, Chum (Oncorhynchus (=Salmo) keta) T Freshwater, Fish

Brackish, Saltwater

Salmon, Coho (Oncorhynchus (=Salmo) kisutch) E Freshwater, Fish

Brackish, Saltwater

Salmon, Sockeye (Oncorhynchus (=Salmo) nerka) E Freshwater, Fish
100

Brackish, Saltwater

Steelhead (Oncorhynchus (=Salmo) mykiss) E Freshwater, Fish

Brackish, Saltwater

Sucker, Lost River (Deltistes luxatus) E Freshwater Fish

Sucker, Modoc (Catostomus microps) E Freshwater Fish

Sucker, Shortnose (Chasmistes brevirostris) E Freshwater Fish

Sucker, Warner (Catostomus warnerensis) T Freshwater Fish

Trout, Bull (Salvelinus confluentus) T Freshwater Fish

Trout, Lahontan Cutthroat (Oncorhynchus clarki henshawi) T Freshwater Fish

Pennsylvania ( 5) species: E/T Medium Taxon

Mussel, Clubshell (Pleurobema clava) E Freshwater Bivalve

Mussel, Dwarf Wedge (Alasmidonta heterodon) E Freshwater Bivalve

Riffleshell, Northern (Epioblasma torulosa rangiana) E Freshwater Bivalve

Bulrush, Northeastern (=Barbed (Scirpus ancistrochaetus) E Terrestrial, 

Monocot

Bristle) Freshwater

Turtle, Bog (Clemmys muhlenbergii) T Terrestrial, Reptile

Freshwater

Puerto Rico ( 8) species: E/T Medium Taxon

Coqui, Golden (Eleutherodactylus jasperi) T Terrestrial, 

Amphibian

Freshwater

Guajon (Eleutherodactylus cooki) T Terrestrial, 

Amphibian

Freshwater

Toad, Puerto Rican Crested (Peltophryne lemur) T Terrestrial, 

Amphibian

Freshwater

Manatee, West Indian (Trichechus manatus) E Saltwater

Mammal

Sea turtle, green (Chelonia mydas) E/T Saltwater Reptile

Sea turtle, hawksbill (Eretmochelys imbricata) E Saltwater, Coastal Reptile

Sea turtle, leatherback (Dermochelys coriacea) E Saltwater, Coastal Reptile

Sea turtle, loggerhead (Caretta caretta) T Saltwater, Coastal Reptile

Rhode Island ( 1) species: E/T Medium Taxon

Sturgeon, Shortnose (Acipenser brevirostrum) E Freshwater, Fish

South Carolina ( 13) species: E/T Medium Taxon

Salamander, Frosted Flatwoods (Ambystoma cingulatum) T Terrestrial, 

Amphibian

Freshwater, Vernal 

pool

Mussel, Heelsplitter Carolina (Lasmigona decorata) E Freshwater Bivalve

Amaranth, Seabeach (Amaranthus pumilus) T Coastal Dicot

Amphianthus, Little (Amphianthus pusillus) T Freshwater Dicot

Dropwort, Canby's (Oxypolis canbyi) E Terrestrial, Dicot

Freshwater

Harperella (Ptilimnium nodosum) E Freshwater Dicot

Pitcher-plant, Mountain Sweet (Sarracenia rubra ssp. jonesii) E Terrestrial, Dicot

Freshwater

Quillwort, Black-spored (Isoetes melanospora) E Vernal pool Ferns

Sturgeon, Shortnose (Acipenser brevirostrum) E Freshwater, Fish

Manatee, West Indian (Trichechus manatus) E Saltwater

Mammal

Arrowhead, Bunched (Sagittaria fasciculata) E Freshwater

Monocot

Pink, Swamp (Helonias bullata) T Terrestrial, 

Monocot

Freshwater
101

Turtle, Bog (Clemmys muhlenbergii) T Terrestrial, Reptile

Freshwater

South Dakota ( 5) species: E/T Medium Taxon

Crane, Whooping (Grus americana) E Terrestrial, Bird

Freshwater

Mussel, Scaleshell (Leptodea leptodon) E Freshwater Bivalve

Pearlymussel, Higgins' Eye (Lampsilis higginsii) E Freshwater Bivalve

Shiner, Topeka (Notropis topeka (=tristis)) E Freshwater Fish

Sturgeon, Pallid (Scaphirhynchus albus) E Freshwater Fish

Tennessee ( 58) species: E/T Medium Taxon

Combshell, Upland (Epioblasma metastriata) E Freshwater Bivalve

Elktoe, Appalachian (Alasmidonta raveneliana) E Freshwater Bivalve

Fanshell (Cyprogenia stegaria) E Freshwater Bivalve

Kidneyshell, Triangular (Ptychobranchus greenii) E Freshwater Bivalve

Mucket, Pink (Pearlymussel) (Lampsilis abrupta) E Freshwater Bivalve

Mussel, Alabama Moccasinshell (Medionidus acutissimus) T Freshwater Bivalve

Mussel, Clubshell (Pleurobema clava) E Freshwater Bivalve

Mussel, Coosa Moccasinshell (Medionidus parvulus) E Freshwater Bivalve

Mussel, Cumberland Combshell (Epioblasma brevidens) E Freshwater Bivalve

Mussel, Cumberland Elktoe (Alasmidonta atropurpurea) E Freshwater Bivalve

Mussel, Cumberland Pigtoe (Pleurobema gibberum) E Freshwater Bivalve

Mussel, Fine-lined Pocketbook (Lampsilis altilis) T Freshwater Bivalve

Mussel, Fine-rayed Pigtoe (Fusconaia cuneolus) E Freshwater Bivalve

Mussel, Ovate Clubshell (Pleurobema perovatum) E Freshwater Bivalve

Mussel, Oyster (Epioblasma capsaeformis) E Freshwater Bivalve

Mussel, Ring Pink (=Golf Stick (Obovaria retusa) E Freshwater Bivalve

Pearly)

Mussel, Rough Pigtoe (Pleurobema plenum) E Freshwater Bivalve

Mussel, Shiny Pigtoe (Fusconaia cor) E Freshwater Bivalve

Mussel, Southern Pigtoe (Pleurobema georgianum) E Freshwater Bivalve

Pearlymussel, Alabama Lamp (Lampsilis virescens) E Freshwater Bivalve

Pearlymussel, Appalachian (Quadrula sparsa) E Freshwater Bivalve

Monkeyface

Pearlymussel, Birdwing (Conradilla caelata) E Freshwater Bivalve

Pearlymussel, Cracking (Hemistena lata) E Freshwater Bivalve

Pearlymussel, Cumberland Bean (Villosa trabalis) E Freshwater Bivalve

Pearlymussel, Cumberland (Quadrula intermedia) E Freshwater Bivalve

Monkeyface

Pearlymussel, Dromedary (Dromus dromas) E Freshwater Bivalve

Pearlymussel, Green-blossom (Epioblasma torulosa gubernaculum) E Freshwater Bivalve

Pearlymussel, Little-wing (Pegias fabula) E Freshwater Bivalve

Pearlymussel, Orange-footed (Plethobasus cooperianus) E Freshwater Bivalve

Pearlymussel, Pale Lilliput (Toxolasma cylindrellus) E Freshwater Bivalve

Pearlymussel, Purple Cat's Paw (Epioblasma obliquata obliquata) E Freshwater Bivalve

Pearlymussel, Tubercled- (Epioblasma torulosa torulosa) E Freshwater Bivalve

Pearlymussel, Turgid-blossom (Epioblasma turgidula) E Freshwater Bivalve

Pearlymussel, White Wartyback (Plethobasus cicatricosus) E Freshwater Bivalve

Pearlymussel, Yellow-blossom (Epioblasma florentina florentina) E Freshwater Bivalve

Purple Bean (Villosa perpurpurea) E Freshwater Bivalve

Rabbitsfoot, Rough (Quadrula cylindrica strigillata) E Freshwater Bivalve

Riffleshell, Tan (Epioblasma florentina walkeri (=E. E Freshwater Bivalve

Crayfish, Nashville (Orconectes shoupi) E Freshwater

Crustacean

Bladderpod, Spring Creek (Lesquerella perforata) E Floodplain Dicot

Pitcher-plant, Green (Sarracenia oreophila) E Terrestrial, Dicot

Freshwater
102

Chub, Slender (Erimystax cahni) T Freshwater Fish

Chub, Spotfin (Erimonax monachus) T Freshwater Fish

Dace, Blackside (Phoxinus cumberlandensis) T Freshwater Fish

Darter, Amber (Percina antesella) E Freshwater Fish

Darter, Bluemask (=jewel) (Etheostoma sp.) E Freshwater Fish

Darter, Boulder (Etheostoma wapiti) E Freshwater Fish

Darter, Duskytail (Etheostoma percnurum) E Freshwater Fish

Darter, Slackwater (Etheostoma boschungi) T Freshwater Fish

Darter, Snail (Percina tanasi) T Freshwater Fish

Logperch, Conasauga (Percina jenkinsi) E Freshwater Fish

Madtom, Pygmy (Noturus stanauli) E Freshwater Fish

Madtom, Smoky (Noturus baileyi) E Freshwater Fish

Madtom, Yellowfin (Noturus flavipinnis) T Freshwater Fish

Shiner, Blue (Cyprinella caerulea) T Freshwater Fish

Shiner, Palezone (Notropis albizonatus) E Freshwater Fish

Sturgeon, Pallid (Scaphirhynchus albus) E Freshwater Fish

Riversnail, Anthony's (Athearnia anthonyi) E Freshwater

Gastropod

Texas ( 22) species: E/T Medium Taxon

Salamander, Barton Springs (Eurycea sosorum) E Terrestrial, 

Amphibian

Freshwater

Salamander, San Marcos (Eurycea nana) T Terrestrial, 

Amphibian

Freshwater

Salamander, Texas Blind (Typhlomolge rathbuni) E Freshwater, 

Amphibian

Subterraneous

Toad, Houston (Bufo houstonensis) E Terrestrial, 

Amphibian

Freshwater

Crane, Mississippi Sandhill (Grus canadensis pulla) E Terrestrial, Bird

Freshwater

Crane, Whooping (Grus americana) E Terrestrial, Bird

Freshwater

Amphipod, Peck's Cave (Stygobromus (=Stygonectes) pecki) E Freshwater, 

Crustacean

Subterraneous

Sunflower, Pecos (Helianthus paradoxus) T Terrestrial, Perm. Dicot

wetland

Darter, Fountain (Etheostoma fonticola) E Freshwater Fish

Gambusia, Big Bend (Gambusia gaigei) E Freshwater Fish

Gambusia, Pecos (Gambusia nobilis) E Freshwater Fish

Gambusia, San Marcos (Gambusia georgei) E Freshwater Fish

Minnow, Devils River (Dionda diaboli) T Freshwater Fish

Pupfish, Comanche Springs (Cyprinodon elegans) E Freshwater Fish

Pupfish, Leon Springs (Cyprinodon bovinus) E Freshwater Fish

Shiner, Arkansas River (Notropis girardi) T Freshwater Fish

Snail, Pecos Assiminea (Assiminea pecos) E Freshwater

Gastropod

Beetle, Comal Springs Dryopid (Stygoparnus comalensis) E Freshwater, Insect

Subterraneous

Beetle, Comal Springs Riffle (Heterelmis comalensis) E Freshwater, Insect

Subterraneous

Manatee, West Indian (Trichechus manatus) E Saltwater

Mammal

Wild-rice, Texas (Zizania texana) E Freshwater

Monocot

Snake, Concho Water (Nerodia paucimaculata) T Terrestrial, Reptile
103

Freshwater

Utah ( 10) species: E/T Medium Taxon

Daisy, Maguire (Erigeron maguirei) T Freshwater Dicot

Chub, Bonytail (Gila elegans) E Freshwater Fish

Chub, Humpback (Gila cypha) E Freshwater Fish

Chub, Virgin River (Gila seminuda (=robusta)) E Freshwater Fish

Squawfish, Colorado (Ptychocheilus lucius) E Freshwater Fish

Sucker, June (Chasmistes liorus) E Freshwater Fish

Sucker, Razorback (Xyrauchen texanus) E Freshwater Fish

Trout, Lahontan Cutthroat (Oncorhynchus clarki henshawi) T Freshwater Fish

Woundfin (Plagopterus argentissimus) E Freshwater Fish

Ambersnail, Kanab (Oxyloma haydeni kanabensis) E Terrestrial, 

Gastropod

Freshwater

Vermont ( 2) species: E/T Medium Taxon

Mussel, Dwarf Wedge (Alasmidonta heterodon) E Freshwater Bivalve

Bulrush, Northeastern (=Barbed (Scirpus ancistrochaetus) E Terrestrial, 

Monocot

Bristle) Freshwater

Virginia ( 40) species: E/T Medium Taxon

Salamander, Shenandoah (Plethodon shenandoah) E Terrestrial, 

Amphibian

Freshwater

Fanshell (Cyprogenia stegaria) E Freshwater Bivalve

Mucket, Pink (Pearlymussel) (Lampsilis abrupta) E Freshwater Bivalve

Mussel, Cumberland Combshell (Epioblasma brevidens) E Freshwater Bivalve

Mussel, Dwarf Wedge (Alasmidonta heterodon) E Freshwater Bivalve

Mussel, Fine-rayed Pigtoe (Fusconaia cuneolus) E Freshwater Bivalve

Mussel, Oyster (Epioblasma capsaeformis) E Freshwater Bivalve

Mussel, Rough Pigtoe (Pleurobema plenum) E Freshwater Bivalve

Mussel, Shiny Pigtoe (Fusconaia cor) E Freshwater Bivalve

Pearlymussel, Appalachian (Quadrula sparsa) E Freshwater Bivalve

Monkeyface

Pearlymussel, Birdwing (Conradilla caelata) E Freshwater Bivalve

Pearlymussel, Cracking (Hemistena lata) E Freshwater Bivalve

Pearlymussel, Cumberland Bean (Villosa trabalis) E Freshwater Bivalve

Pearlymussel, Cumberland (Quadrula intermedia) E Freshwater Bivalve

Monkeyface

Pearlymussel, Dromedary (Dromus dromas) E Freshwater Bivalve

Pearlymussel, Green-blossom (Epioblasma torulosa gubernaculum) E Freshwater Bivalve

Pearlymussel, Little-wing (Pegias fabula) E Freshwater Bivalve

Purple Bean (Villosa perpurpurea) E Freshwater Bivalve

Rabbitsfoot, Rough (Quadrula cylindrica strigillata) E Freshwater Bivalve

Riffleshell, Tan (Epioblasma florentina walkeri (=E. E Freshwater Bivalve

Spinymussel, James River (Pleurobema collina) E Freshwater Bivalve

Isopod, Lee County Cave (Lirceus usdagalun) E Freshwater

Crustacean

Isopod, Madison Cave (Antrolana lira) T Freshwater

Crustacean

Amaranth, Seabeach (Amaranthus pumilus) T Coastal Dicot

Birch, Virginia Round-leaf (Betula uber) T Floodplain Dicot

Harperella (Ptilimnium nodosum) E Freshwater Dicot

Joint-vetch, Sensitive (Aeschynomene virginica) T Terrestrial, Brackish Dicot

Sneezeweed, Virginia (Helenium virginicum) T Vernal pool Dicot

Chub, Slender (Erimystax cahni) T Freshwater Fish

Chub, Spotfin (Erimonax monachus) T Freshwater Fish
104

Dace, Blackside (Phoxinus cumberlandensis) T Freshwater Fish

Darter, Duskytail (Etheostoma percnurum) E Freshwater Fish

Logperch, Conasauga (Percina jenkinsi) E Freshwater Fish

Logperch, Roanoke (Percina rex) E Freshwater Fish

Madtom, Yellowfin (Noturus flavipinnis) T Freshwater Fish

Sturgeon, Shortnose (Acipenser brevirostrum) E Freshwater, Fish

Butterfly, Mitchell's Satyr (Neonympha mitchellii mitchellii) E Terrestrial, Perm. Insect

wetland

Bulrush, Northeastern (=Barbed (Scirpus ancistrochaetus) E Terrestrial, 

Monocot

Bristle) Freshwater

Pink, Swamp (Helonias bullata) T Terrestrial, 

Monocot

Freshwater

Turtle, Bog (Clemmys muhlenbergii) T Terrestrial, Reptile

Freshwater

Washington ( 10) species: E/T Medium Taxon

Albatross, Short-tailed (Phoebastria (=Diomedea) albatrus) E Terrestrial, Saltwater Bird

Murrelet, Marbled (Brachyramphus marmoratus) T Terrestrial, Bird

Freshwater, 

Howellia, Water (Howellia aquatilis) T Freshwater Dicot

Lomatium, Bradshaw's (Lomatium bradshawii) E Terrestrial, Dicot

Freshwater

Sandwort, Marsh (Arenaria paludicola) E Terrestrial, Dicot

Freshwater

Salmon, Chinook (Oncorhynchus (=Salmo) tshawytscha) E/T Freshwater, Fish

Brackish, Saltwater

Salmon, Sockeye (Oncorhynchus (=Salmo) nerka) E Freshwater, Fish

Brackish, Saltwater

Steelhead (Oncorhynchus (=Salmo) mykiss) E Freshwater, Fish

Brackish, Saltwater

Trout, Apache (Oncorhynchus apache) T Freshwater Fish

Trout, Bull (Salvelinus confluentus) T Freshwater Fish

West Virginia ( 10) species: E/T Medium Taxon

Salamander, Cheat Mountain (Plethodon nettingi) T Terrestrial, 

Amphibian

Freshwater

Fanshell (Cyprogenia stegaria) E Freshwater Bivalve

Mucket, Pink (Pearlymussel) (Lampsilis abrupta) E Freshwater Bivalve

Mussel, Clubshell (Pleurobema clava) E Freshwater Bivalve

Pearlymussel, Tubercled- (Epioblasma torulosa torulosa) E Freshwater Bivalve

Riffleshell, Northern (Epioblasma torulosa rangiana) E Freshwater Bivalve

Spinymussel, James River (Pleurobema collina) E Freshwater Bivalve

Isopod, Madison Cave (Antrolana lira) T Freshwater

Crustacean

Harperella (Ptilimnium nodosum) E Freshwater Dicot

Bulrush, Northeastern (=Barbed (Scirpus ancistrochaetus) E Terrestrial, 

Monocot

Bristle) Freshwater

Wisconsin ( 3) species: E/T Medium Taxon

Mussel, Winged Mapleleaf (Quadrula fragosa) E Freshwater Bivalve

Pearlymussel, Higgins' Eye (Lampsilis higginsii) E Freshwater Bivalve

Dragonfly, Hine's Emerald (Somatochlora hineana) E Terrestrial, Insect

Freshwater

Wyoming ( 7) species: E/T Medium Taxon

Toad, Wyoming (Bufo baxteri (=hemiophrys)) E Terrestrial, 

Amphibian
105

Freshwater

Wyoming ( 7) species: E/T Medium Taxon

Crane, Whooping (Grus americana) E Terrestrial, Bird

Freshwater

Chub, Bonytail (Gila elegans) E Freshwater Fish

Chub, Humpback (Gila cypha) E Freshwater Fish

Squawfish, Colorado (Ptychocheilus lucius) E Freshwater Fish

Sturgeon, Pallid (Scaphirhynchus albus) E Freshwater Fish

Sucker, Razorback (Xyrauchen texanus) E Freshwater Fish

 

 No species were selected for exclusion.

Dispersed species included in report.

Aquatic Marine Species

Fish (Actinopterygii)

Common name Scientific name Family Order

Salmon, Atlantic Salmo salar Salmonidae Salmoniformes

Salmon, Chinook Oncorhynchus (=Salmo) tshawytscha Salmonidae Salmoniformes

Salmon, Chum Oncorhynchus (=Salmo) keta Salmonidae Salmoniformes

Salmon, Coho Oncorhynchus (=Salmo) kisutch Salmonidae Salmoniformes

Salmon, Sockeye Oncorhynchus (=Salmo) nerka Salmonidae Salmoniformes

Sawfish, Smalltooth Pristis pectinata Pristidae Pristiformes

Steelhead Oncorhynchus (=Salmo) mykiss Salmonidae Salmoniformes

Sturgeon, Gulf Acipenser oxyrinchus desotoi Acipenseridae Acipenseriformes

Sturgeon, North American green Acipenser medirostris Acipenseridae Acipenseriformes

Sturgeon, Shortnose Acipenser brevirostrum Acipenseridae Acipenseriformes

Sturgeon, White Acipenser transmontanus Acipenseridae Acipenseriformes

Gastropod (Gastropoda)

Common name Scientific name Family Order

Abalone, White Haliotis sorenseni Haliotidae Vetigastropoda

Mammal (Mammalia)

Common name Scientific name Family Order

Bear, polar Ursus maritimus Ursidae Carnivora

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

Seal, spotted Phoca largha Phocidae Carnivora

Sea-lion, Steller Eumetopias jubatus Otariidae Carnivora

Whale, Blue Balaenoptera musculus Balaenopteridae Cetacea

Whale, Bowhead Balaena mysticetus Balaenidae Cetacea

Whale, Finback Balaenoptera physalus Balaenopteridae 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

Monocot (Liliopsida)
106

Common name Scientific name Family Order

Seagrass, Johnson's Halophila johnsonii Hydrocharitaceae Alismatales

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