2 

NEW CHEMICAL REGISTRATION 

ECOLOGICAL RISK ASSESSMENT 

Cyflumetofen 

CAS Number 400882-07-7 

US EPA PC CODE 138831 

Prepared by:

Robin Sternberg, Ph.D., Wildlife Biologist 

Stephen Wente, Ph.D., Biologist 

Environmental Risk Branch I 

Reviewed by: 

Meghan Radtke, Ph.D., Biologist 

Faruque Khan, Ph.D., Senior Fate Scientist 

Environmental Risk Branch I 

Environmental Fate and Effects Division 

U. S. Environmental Protection Agency

Office of Pesticide Programs

Environmental Fate and Effects Division

Environmental Risk Branch I

1200 Pennsylvania Ave., NW

Mail Code 7507P

Washington, DC 20460
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Contents

1 Executive Summary ................................................................................................................ 6

2 Problem Formulation .............................................................................................................. 7

2.1 Stressor: Source and Distribution ................................................................................... 8

2.1.1 Source and Intensity .................................................................................................. 8

2.1.2 Pesticide Type, Class, and Mode of Action .............................................................. 9

2.1.3 Physical/Chemical/Fate and Transport Properties .................................................... 9

2.1.4 Overview of Pesticide Usage .................................................................................. 10

2.2 Receptors: The Biological Entities Exposed to the Stressor ......................................... 10

2.2.1 Effects to Aquatic and Terrestrial Organisms ......................................................... 10

2.2.2 Ecosystems Potentially at Risk ............................................................................... 11

2.3 Assessment Endpoints .................................................................................................. 11

2.4 Conceptual Model ......................................................................................................... 13

2.4.1 Risk Hypothesis ...................................................................................................... 13

2.4.2 Exposure Pathways of Concern .............................................................................. 13

2.5 Analysis Plan ................................................................................................................ 14

2.5.1 Stressors of Concern ............................................................................................... 14

2.5.2 Measures of Exposure ............................................................................................. 15

2.5.3 Measures of Effect .................................................................................................. 17

2.5.4 Integration of Exposure and Effects ....................................................................... 18

2.5.5 Endangered Species Assessments ........................................................................... 19

2.5.6 Endocrine Disruptor Screening Program ................................................................ 19

2.6 Data Gaps ...................................................................................................................... 20

2.6.1 Environmental fate .................................................................................................. 20

2.6.2 Ecological Effects ................................................................................................... 22

3 Fate and Transport Characterization ..................................................................................... 24

3.1 Degradation ................................................................................................................... 26

3.1.1 Hydrolysis ............................................................................................................... 26

3.1.2 Aquatic Photolysis .................................................................................................. 26

3.1.3 Soil photolysis ......................................................................................................... 26

3.1.4 Aerobic Soil Metabolism ........................................................................................ 27

3.1.5 Anaerobic Soil Metabolism .................................................................................... 27

3.1.6 Aerobic Aquatic Metabolism .................................................................................. 28

3.1.7 Anaerobic Aquatic Metabolism .............................................................................. 28
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3.2 Mobility......................................................................................................................... 28

3.2.1 Volatility ................................................................................................................. 28

3.2.2 Adsorption/desorption – Parent .............................................................................. 28

3.2.3 Adsorption/desorption – Degradates....................................................................... 29

3.3 Field Studies.................................................................................................................. 29

3.4 Bioconcentration ........................................................................................................... 30

4 Exposure Assessment............................................................................................................ 30

4.1 Terrestrial Exposure ...................................................................................................... 30

4.1.1 Birds, Mammals, and Terrestrial Invertebrates ....................................................... 30

4.1.2 Terrestrial (Upland and Semi-Aquatic) Plants ........................................................ 31

4.2 Aquatic Exposure .......................................................................................................... 32

4.2.1 Aquatic Bioaccumulation........................................................................................ 37

5 Effects Characterization ........................................................................................................ 38

5.1 Effects to Terrestrial Organisms ................................................................................... 38

5.1.1 Birds ........................................................................................................................ 38

5.1.2 Mammals................................................................................................................. 43

5.1.3 Terrestrial Invertebrates .......................................................................................... 44

5.1.4 Terrestrial (Upland and Semi-Aquatic) Plants ........................................................ 44

5.2 Effects to Aquatic Organisms ....................................................................................... 46

5.2.1 Parent Cyflumetofen ............................................................................................... 46

5.2.2 Degradates of Cyflumetofen ................................................................................... 52

5.3 Review of Incident Data ............................................................................................... 53

6 Risk Characterization ............................................................................................................ 54

6.1 Risk Estimation ............................................................................................................. 54

6.1.1 Direct Effects to Terrestrial Organisms .................................................................. 54

6.1.2 Direct Effects to Aquatic Organisms ...................................................................... 56

6.2 Risk Description............................................................................................................ 60

6.2.1 Direct Effects to Birds, Reptiles, and Terrestrial-Phase Amphibians ..................... 61

6.2.2 Direct Effects to Mammals ..................................................................................... 61

6.2.3 Direct Effects to Terrestrial Invertebrates ............................................................... 62

6.2.4 Direct Effects to Terrestrial (Upland and Semi-Aquatic) Plants ............................ 63

6.2.5 Direct Effects to Fish, Aquatic-Phase Amphibians, and Aquatic Invertebrates ..... 64

6.2.6 Direct Effects to Sediment-Dwelling (Benthic) Invertebrates ................................ 65

6.2.7 Direct Effects to Aquatic Plants .............................................................................. 65
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6.3 Summary of Direct Effects ........................................................................................... 66

6.4 Indirect Effects .............................................................................................................. 66

6.5 Federally Threatened and Endangered (Listed) Species Concerns ............................... 67

6.5.1 Action Area ............................................................................................................. 67

6.5.2 Taxonomic Groups Potentially at Risk ................................................................... 67

7 Uncertainties ......................................................................................................................... 70

7.1 Data Gaps ...................................................................................................................... 70

7.1.1 Environmental Fate ................................................................................................. 70

7.1.2 Ecological Effects ................................................................................................... 71

8 References ............................................................................................................................. 71

9 Bibliography of Cited MRIDs .............................................................................................. 72

Appendix A: Input and Results of Screening Imbibition Program (SIP v. 1.0) ........................... 80

Appendix B: Input and Output of Screening Tool for Inhalation Risk (STIR v. 1.0) .................. 82

Appendix C: Cyflumetofen and Its Environmental Transformation Products and Degradation 

Pathways ....................................................................................................................................... 85

Appendix D: Parent and Total Toxic Residue (TTR) PestDF Degradation Half-life Estimation 

Output and Available Degradate Study Half-life Estimation Output ........................................... 98

Appendix E: Example PRZM/EXAMS Modeling Output and AgDRIFT® Input Data Summary

..................................................................................................................................................... 114

Appendix F: Listed Species That Overlap at the County Level with Areas Where Cyflumetofen 

Is Proposed To Be Used as Identified by LOCATES (v. 2.2.5) ................................................. 120

 
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1 Executive Summary 

The purpose of this screening-level ecological risk assessment is to evaluate potential risks to 

non-target species, both non-listed and federally-listed endangered and threatened species 

(hereafter referred to as non-listed and listed species, respectively), from proposed uses of the 

new insecticide, cyflumetofen. 

Cyflumetofen (2-methoxyethyl (RS)-2-(4-tert-butylphenyl)-2-cyano-3-oxo-3-(α,α,α-trifluoro-otolyl)propionate) is a non-systemic, contact miticide that provides knockdown and residual 

control of tetranychid mites. Cyflumetofen acts as a mitochondria complex II electron transport 

inhibitor and is classified as a Group 25 acaricide by the Insecticide Resistance Action 

Committee (IRAC). 

Proposed uses of cyflumetofen include citrus, pome fruits, grapes, strawberries, tomatoes, tree 

nuts, and ornamentals. The proposed maximum single application rate and maximum 

application rate per crop cycle or year are 0.2 lb a.i./A and 0.4 lb a.i./A, respectively, 

corresponding to a maximum of 2 applications per crop cycle or year. The proposed minimum 

application interval is 14 days. Cyflumetofen is formulated as a suspension concentrate and is 

proposed to be applied via ground equipment. Aerial application is proposed only for tomatoes. 

The parent chemical, cyflumetofen, is expected to degrade rapidly in the environment, but 

undergoes a complex series of transformations that result in the production of many degradates 

of concern. Some of the degradates of concern are much more persistent than the parent. 

A summary of direct and indirect effects to non-listed and listed taxa from the proposed uses of 

cyflumetofen is provided in Table 1-1. Direct or indirect effects to specific listed species have 

not been definitively determined; further investigation into temporal, geographical, and 

biological associations between the proposed uses and affected taxa is needed before definitive 

effects determinations can be made. 

Based on Agency Level of Concern (LOC) exceedances, results of this screening-level 

ecological risk assessment indicate that the proposed uses of cyflumetofen have the potential for 

direct adverse effects to listed and non-listed mammals and listed dicots. Risk quotients (RQs) 

could not be calculated for monocots due to the lack of appropriate endpoints for seedling 

emergence. However, direct adverse effects to listed monocots are expected based on a 

comparison of terrestrial plant EECs and available seedling emergence data. In addition, given 

the inability to determine a seedling emergence EC25 for monocots, risk to non-listed monocots 

cannot be precluded. A Tier II seedling emergence continuation study is necessary to reduce 

uncertainty in the characterization of risk to listed and non-listed monocots. 

 

Table 1-1. Summary of Direct and Indirect Effects Associated with Proposed Uses of 

Cyflumetofen 

Taxon 

Risk Concern for 

Direct Effects?* 

Risk Concern for 

Indirect Effects to 

Non-Listed Listed** Listed Species?** 

Birds No No Yesa,b

Reptiles No No Yesa,b
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Taxon 

Risk Concern for 

Direct Effects?* 

Risk Concern for 

Indirect Effects to 

Non-Listed Listed** Listed Species?** 

Terrestrial-phase amphibians No No Yesa,b

Mammals Yes (chronic 

exposurec) 

Yes (chronic 

exposurec) 

Yesb

Terrestrial invertebrates Nod Nod Yesa,b

Terrestrial (upland and semi-aquatic) plants : monocots Yese Yesf Yesa

Terrestrial (upland and semi-aquatic) plants: dicots No Yes Yesa

Freshwater fish No No Yesb

Aquatic-phase amphibians No No Yesb

Freshwater invertebrates No No Yesb

Estuarine/marine fish No No Yesb

Estuarine/marine invertebrates No No Yesb

Sediment-dwelling (benthic) invertebrates No No Yesb

Aquatic vascular plants No No Yesb

Aquatic non-vascular plants No NA Yesb

NA = not applicable because there are no listed aquatic non-vascular plants 

* Unless otherwise specified, the Agency Level of Concern (LOC) was exceeded. 

** Direct or indirect effects to specific species have not been definitively determined; further investigation into 

temporal, geographical, and biological associations between the proposed uses and affected taxa is needed before 

definitive effects determinations can be made. a

 due to direct effects to non-listed mammals 

b

 due to direct effects to non-listed monocots which cannot be precluded given the inability to determine a seedling 

emergence EC25 for monocots c

 small and medium mammals consuming short grass, tall grass, broadleaf plants, or arthropods and large mammals 

consuming short grass or tall grass 

d Given the insecticidal mode of action of cyflumetofen, the potential for risk to sensitive, non-target terrestrial 

invertebrates exists. e

 Given the inability to determine a seedling emergence EC25 for monocots, risk to non-listed monocots cannot be 

precluded. f

 Although RQs could not be calculated for listed monocots due to the lack of a NOAEC for seedling emergence, 

adverse direct effects to listed monocots are expected based on a comparison of terrestrial plant EECs and the 

available seedling emergence data. 

2 Problem Formulation 

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

registration of the new chemical, cyflumetofen. As a new insecticide being proposed for use in 

the United States, EPA is required under the Federal Insecticide, Fungicide, and Rodenticide Act 

(FIFRA) to ensure that cyflumetofen does not have the potential to cause unreasonable adverse 

effects to the environment. A “preliminary assessment” to determine the potential for direct and 

indirect effects to federally-listed endangered and threatened species (hereafter referred to listed 

species) is also conducted. Further investigation into temporal, geographical, and biological 

associations between the proposed uses of cyflumetofen and affected listed taxa is needed before 

definitive effects determinations can be made. To these ends, this assessment follows EPA 

guidance on conducting ecological risk assessments (USEPA, 1998) and the Office of Pesticide 

Program’s policies for assessing risk to non-target and listed organisms (USEPA, 2004).

Among the end products of the EPA pesticide registration process is a determination of whether 

a product is eligible for registration and, if so, a description of how the product may be used. A 
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label represents the legal document that 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. This assessment is in support of the new chemical registration of cyflumetofen. 

2.1 Stressor: Source and Distribution 

2.1.1 Source and Intensity 

Cyflumetofen, a non-systemic, contact miticide, is a new chemical that is undergoing registration 

by BASF. In addition to the technical, two end-use products are being proposed for registration 

in the United States (Table 2-1). According to the proposed labels, the products would provide 

knockdown and residual control of tetranychid mites (Table 2-2) in citrus, grapes, pome fruits, 

strawberries, tomatoes, tree nuts, and ornamentals (Table 2-3). 

Table 2-1. Proposed End-Use Products of Cyflumetofen 

End-Use Product Use % Active 

Ingredient 

Type of Formulation Registration 

Number 

NealtaTM miticide Citrus, grapes, pome fruits, 

strawberries, tree nuts, tomatoes 18.7 Suspension concentrate 7969-GGA 

SultanTM miticide Ornamentals 18.7 Suspension concentrate 7969-GGT 

Table 2-2. Tetranychid Mites Controlled by Proposed End-Use Products of Cyflumetofen 

Common Name Scientific name 

Carmine Tetranychus cinnabarinus

Citrus red Panonychus citri

Banks grass Oligonychus pratensis

Brown almond Bryobia rubrioculus

Brown wheat Petrobia lateens

European red Panonychus ulmi

Texas citrus Eutetranychus banks

Spider mites 

McDaniel Tetranychus mcdaniel

Pacific spider Tetranychus pacificus

Spruce spider Oligonychus ununguis

Strawberry spider Tetranychus turkestan

Two spotted Tetranychus urticae

Willamette Eotetranychus willamettei

Yuma Eotetranychus yumensis

Table 2-3. Proposed Uses of Cyflumetofen 

Citrus Fruit Group 

Calamondin Citrus citron Citrus hybrids Chironja 

Grapefruit Kumquat Lemon Lime 

Mandarin orange 

(sweet and sour) 

Pummelo 

Tangerine 

Satsuma 

Tangor 

Tangelo 

Grapes 

Pome Fruit Group 

Apple Crabapple Loquat Mayhaw 

Oriental Pear Pear Quince 
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Strawberry 

Tomato 

Tree Nuts Group 

Almonds Beech nut Brazil nut Butternut 

Cashew Chestnut Chinquapin Filbert 

Hickory nut Macadamia nut Pecan Walnuts 

(black and English) 

Ornamentals 

annual and perennial herbaceous plants woody trees and shrubs 

2.1.2 Pesticide Type, Class, and Mode of Action 

Cyflumetofen is a non-systemic, contact miticide that belongs to the benzoylacetonitrile class of 

compounds. It is classified as a Group 25 acaricide by the Insecticide Resistance Action 

Committee (IRAC); the only other active ingredient in this group – cyenopyrafen – is not 

registered in the United States. Cyflumetofen acts as a mitochondria complex II electron 

transport inhibitor resulting in knockdown and residual control of the egg, nymph, and adult 

stages of tetranychid mites. 

2.1.3 Physical/Chemical/Fate and Transport Properties 

Cyflumetofen is non-volatile, has limited solubility in water, and is quite lipophilic and therefore 

would be expected to absorb to foliage surfaces and soil (Koc of 1.3 x 105

 ml/g) at the site of 

application. Selected physical and chemical properties are summarized in Table 2-4. Once 

deposited, either at the site of application or farther afield through runoff and/or spray drift, the 

parent molecule is expected to degrade quickly through multiple fate processes (half-lives of 

hours to several days) under environmental conditions. 

Table 2-4. Selected Physical and Chemical Properties for Cyflumetofen 

Property Value 

Common Name Cyflumetofen 

Chemical Name 2-methoxyethyl (RS)-2-(4-tert-butylphenyl)-2-cyano-3-oxo-3-(α,α,α-trifluoro-otolyl)propionate 

CAS Number 400882-07-7 

Pesticide Class Mitochondria complex II electron transport inhibitor (IRAC Group 25) – Acaricide 

Molecular Formula C24H24F3NO4

Molecular Weight 447.45g/mol 

Physical State Milky white, odorless suspension concentrated liquid, with density of 1.0682 g/cm3 

@ 20oC 

Vapor Pressure < 4.43 × 10-8 torr at 25oC 

Water Solubility 28 μg/L 

Henry’s Law Constant < 9.3 × 10-7 Pa*m3/mol at 20oC 

Log Kow 4.3 at 25°C 

IRAC = Insecticide Resistance Action Committee 

Cyflumetofen forms many degradates with a wide range of fate properties (e.g., from highly 

soluble to less soluble than the parent). Many of these degradates were considered degradates of 

concern by EFED due to the presence of a cyano group (C≡N). However, the reason for 

developing a very broad and inclusive set of degradates of concern is more out of a concern for 

efficiency in the Ecological Risk Assessment, rather than the toxicological properties of the 
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individual degradates. Attempts to quantify exposure and effects for each of the many individual 

degradates of cyflumetofen would produce considerable uncertainty in the risk assessment. 

Instead, a strategy was devised to estimate a maximum exposure to total cyflumetofen degradates 

and show that even in the most conservative case with all of the potential degradates of concern 

assumed to be the most toxic degradate that the degradates would not pose a risk individually or 

as a group. Note that this strategy is applied to the aquatic portions of the risk assessment. Other 

arguments are provided for the terrestrial portions of this assessment. This definition of the 

degradates of concern for the Ecological Risk Assessment differs from the degradates of concern 

in the drinking water assessment conducted for human health concerns by the Agency’s Health 

Effects Division, which included only the parent and “AB” degradates (described in Section 3; 

Negrón-Encarnación, 2013). 

2.1.4 Overview of Pesticide Usage 

Proposed uses of cyflumetofen include citrus, pome fruits, grapes, strawberries, tomatoes, tree 

nuts, and ornamentals. Cyflumetofen is formulated as a suspension concentrate and is proposed 

to be applied via ground equipment. Aerial application is proposed only for tomatoes. 

Application information is provided in Table 2-5. Since this a new chemical, the Agency does 

not have any usage information for cyflumetofen. The assessment assumes one crop cycle per 

year. 

Table 2-5. Application Information for Proposed Uses of Cyflumetofen 

Use Form. App. Method Max. 

Single 

App. 

Rate 

(lb a.i./A) 

Max. 

Number of 

App.

Max. App. 

Rate Per 

Crop Cycle 

or Year 

(lb a.i./A) 

Min. 

App. 

Interval 

(Days)

PHI 

(Days) 

Citrus 

NealtaTM

miticide 

Ground 

0.2 2/crop cycle 0.4 14 7 

Grapes 0.2 2/crop cycle 0.4 14 14 

Pome fruits 0.2 2/crop cycle 0.4 14 7 

Strawberries 0.2 2/crop cycle 0.4 14 1 

Tree nuts 0.2 2/crop cycle 0.4 14 7 

Tomatoes Aerial, ground 0.2 2/crop cycle 0.4 14 3 

Ornamentalsa SultanTM

miticide Ground 0.2 2/yr 0.4 14 NA 

App. = application; Form. = formulation; Max. = maximum; Min. = minimum; NA = not applicable; PHI = 

Preharvest interval 

a

 annual and perennial herbaceous plants and woody trees and shrubs 

2.2 Receptors: The Biological Entities Exposed to the Stressor 

2.2.1 Effects to Aquatic and Terrestrial Organisms 

Table 2-6 provides examples of taxonomic groups and species that are tested to help understand 

potential ecological effects of pesticides to non-target organisms. Within each of these very 

broad taxonomic groups, a measure of effect from acute and/or chronic exposure is selected from 

the available data. 

Table 2-6. Taxonomic Groups and Test Species Evaluated for Ecological Effects in 

Screening-Level Risk Assessments
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Taxonomic Group Example(s) of Representative Species 

Birds1 Mallard duck (Anas platyrhynchos) 

Bobwhite quail (Colinus virginianus)

Mammals Laboratory rat (Rattus norvegicus) 

Terrestrial invertebrates Honeybee (Apis mellifera) 

Freshwater fish2 Bluegill sunfish (Lepomis macrochirus) 

Rainbow trout (Oncorhynchus mykiss) 

Freshwater invertebrates Water flea (Daphnia magna) 

Estuarine/marine fish Sheepshead minnow (Cyprinodon variegatus) 

Estuarine/marine invertebrates Mysid (Americamysis bahia)

Eastern oyster (Crassostrea virginica) 

Terrestrial plants3 Monocots – corn (Zea mays) 

Dicots – soybean (Glycine max) 

Aquatic vascular plants Duckweed (Lemna gibba) 

Aquatic non-vascular plants 

Green algae (Pseudokirchneriella subcapitata) 

Freshwater diatom (Navicula pelliculosa) 

Marine diatom (Skeletonema costatum) 

Cyanobacterium (Anabaena flos-aquae) 1

 Birds serve as surrogates for terrestrial-phase amphibians and reptiles. 

2

 Freshwater fish serve as surrogates for aquatic-phase amphibians. 3

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

one is soybeans.

2.2.2 Ecosystems Potentially at Risk 

The ecosystems potentially at risk include aquatic and terrestrial areas adjacent to or downstream 

from the application site. In addition, organisms that use the application site as part of their 

habitat (e.g., birds foraging for insects within application areas) are also considered to be part of 

the ecosystems potentially at risk. 

2.3 Assessment Endpoints 

FIFRA Part 158 guideline toxicity tests (CFR 40 §158.630, 2009) are intended to determine 

pesticide effects on a variety of organisms, including birds, mammals, fish, terrestrial and aquatic 

invertebrates, and plants. These tests include both short-term and long-term exposure periods 

and evaluate the survival, reproduction, and/or growth of laboratory species. The studies, when 

available, are used to evaluate the potential of a pesticide to cause adverse effects, to determine 

whether further testing is required, and to determine the need for precautionary label statements 

to minimize the potential adverse effects to non-target animals and plants (CFR 40 §158.630, 

2009). 

Assessment endpoints are intended to represent valued attributes of the environment that, if 

detrimentally altered, could pose a risk to the environment. The assessment endpoints of this 

ecological risk assessment include terrestrial and aquatic animal and plant mortality following 

acute exposure to cyflumetofen and terrestrial and aquatic animal reproduction, growth and 

survival effects from chronic exposure to cyflumetofen. Surrogate species are used to represent 

all freshwater fish (2000+) and bird (680+) species in the United States. For mammals, acute 

studies are usually limited to the Norway rat (Rattus norvegicus) or the house mouse (Mus 

musculus). Usually data from estuarine/marine testing are limited to a crustacean, a mollusk, and 

a fish. The assessment of risk or hazard makes the assumption that avian toxicity is similar to 
12 

terrestrial-phase amphibians and reptiles, unless more appropriate data are available. The same 

assumption is made for fish and aquatic-phase amphibians. The most sensitive toxicity 

endpoints are used from surrogate test species to estimate treatment-related direct effects on 

mortality and reproductive and growth assessment endpoints. 

For terrestrial and semi-aquatic plants, the screening assessment endpoints for non-target species 

(crops and non-crop plant species) are based on the emergence and growth of seedlings and 

vegetative vigor of annuals. Measures of effect for this assessment focus on alterations to plant 

emergence and/or to active growth. 

For aquatic plants, the assessment endpoint is the maintenance and growth of standing crop or 

biomass. Measures of effect for this assessment focus on non-vascular, e.g., algae, and vascular 

plant, e.g., duckweed (Lemna gibba), growth rates and biomass measurements. 

The Agency acknowledges that pesticides have the potential to exert indirect effects upon listed 

organisms by, for example, perturbing forage or prey availability, altering the extent of nesting 

habitat, and creating gaps in the food chain. In conducting a screen for indirect effects, the 

endpoints for each taxonomic group are used to make inferences concerning the potential for 

indirect effects upon listed species that rely upon non-listed organisms as resources critical to 

their life cycle. 

The endpoints are typically derived from registrant-submitted studies which have undergone 

review and were classified as “acceptable” (conducted under guideline conditions and considered 

to be scientifically valid) or “supplemental” (conditions deviated from guidelines but the results 

are considered to be scientifically valid). Additional details on EFED’s study classification 

system and study guidelines can be found in the Agency’s Overview Document (USEPA, 2004). 

Assessment endpoints can also be derived from the open literature. Toxicity data from the open 

literature are identified via the ECOTOX1 search engine which is maintained by the U.S. EPA 

Office of Research and Development (ORD). To be included in the ECOTOX database, papers 

must meet several criteria. Data that pass the ECOTOX screen are evaluated relative to the data 

provided by the registrant and may be incorporated qualitatively or quantitatively into the risk 

assessment after a formal review conducted in accordance with current guidelines for evaluating 

ecological toxicity data in the open literature.2

 Specific studies may warrant inclusion in the 

ecological risk assessment when: 

 tested endpoints are more sensitive than those in registrant data; 

 the test data are based on under-represented taxa; and/or 

 the data include ecologically relevant endpoints not normally evaluated in registrant 

studies 

Although all endpoints are measured at the individual level, they can provide some insight about 

the potential for adverse effects at higher levels of biological organization (e.g. populations and 

 

1

 USEPA 2011. Ecotoxicity database http://cfpub.epa.gov/ecotox/ 2

http://www.epa.gov/pesticides/science/efed/policy_guidance/team_authors/endangered_species_reregistration_work

group/esa_evaluation_open_literature.htm
13 

communities). For example, pesticide effects on individual survivorship have important 

implications for both population rates and habitat carrying capacity. 

No cyflumetofen studies from the open literature were identified using the public version of 

ECOTOX3

. 

2.4 Conceptual Model 

2.4.1 Risk Hypothesis 

The Agency presumes the following risk hypothesis for this screening-level ecological risk 

assessment: 

Based on mode of action, the proposed use patterns, and the sensitivity of non-target aquatic and 

terrestrial species, the proposed uses of cyflumetofen have the potential to reduce survival, 

reproduction, and/or growth in non-target terrestrial and aquatic animals and plants through 

direct application, spray drift and/or runoff. These non-target organisms include Federally-listed 

threatened and endangered species as well as non-listed species. 

To pose an ecological risk, a chemical must reach non-target organisms at concentrations found 

to cause adverse effects. The analysis of ecological exposure pathways in this assessment 

includes an examination of the source and potential migration pathways of cyflumetofen 

exposure and the determination of potential adverse effects to non-target species. 

2.4.2 Exposure Pathways of Concern 

This screening-level ecological risk assessment considers potential exposure to cyflumetofen as a 

result of direct application, spray drift, and runoff. 

For terrestrial vertebrates, the major route of exposure to cyflumetofen is considered to be via 

dietary ingestion of food items such as seeds, plants, and/or animals that have cyflumetofen 

residues as a result of direct application, spray drift, and runoff. Exposure to parent 

cyflumetofen through the consumption of drinking water alone is not considered a potential 

concern for birds or mammals based on the results of EFED’s Screening Imbibition Program 

(SIP v. 1.0)4

 using parent cyflumetofen’s solubility (0.0281 mg/L) and non-definitive endpoints 

for mammalian and avian acute oral toxicity (rat and bobwhite quail LD50 > 2000 mg/kg-bw, 

MRIDs 48542669 and 48542772, respectively) and endpoints for mammalian and avian chronic 

toxicity (rat NOAEC = 9.21 mg/kg-bw/day, MRID 48542702; mallard NOAEC = 930 mg/kgdiet, MRID 48542778; bobwhite quail NOAEC = 154 mg/kg-diet, MRID 48542777; Appendix 

A). Exposure to terrestrial vertebrates through inhalation is considered unlikely given 

cyflumetofen’s low vapor pressure and the results of EFED’s Screening Tool for Inhalation Risk 

(STIR v. 1.0)5

 using conservative non-definitive endpoints for mammalian and avian acute oral 

toxicity (LD50 > 2000 mg/kg-bw) and a conservative non-definitive endpoint for mammalian 

acute inhalation toxicity (LC50 > 2.65 mg/L, MRID 48542672) (Appendix B). 

 

3

 Quick Database Query conducted on CAS number 400882-07-7 at http://cfpub.epa.gov/ecotox/ 4 http://www.epa.gov/oppefed1/models/terrestrial/index.htm#sip

5 http://www.epa.gov/oppefed1/models/terrestrial/index.htm#stir
14 

For terrestrial invertebrates, the major routes of exposure to cyflumetofen are considered to be 

direct contact as a result of direct application and spray drift and dietary ingestion of 

plants/pollen/nectar, animals, and/or soil that have cyflumetofen residues as a result of direct 

application, spray drift, and runoff. 

For terrestrial (upland and semi-aquatic) non-target plants, the major routes of exposure to 

cyflumetofen are considered to be direct contact as a result of direct application and spray drift 

and root uptake via soil contaminated via spray drift and runoff. 

For aquatic animals, the major route of exposure to cyflumetofen is considered to be uptake via 

the respiratory surface (gills) or the integument from surface water/sediment that has 

cyflumetofen residues as a result of spray drift, runoff, and leaching to groundwater from soil. 

For aquatic plants, the major routes of exposure to cyflumetofen are considered to be uptake 

from surface water/sediment containing cyflumetofen residues as a result of spray drift, runoff, 

and leaching to groundwater from soil. 

2.5 Analysis Plan 

As with any pesticide, there is concern regarding the potential effects cyflumetofen use may pose 

to non-target animals and plants. This document characterizes the environmental fate of 

cyflumetofen to assess whether its use as proposed on the label provides a means of exposure to 

non-target species. Additionally, the toxicity of cyflumetofen is characterized. Then both 

potential exposure and effects are integrated to estimate the likelihood of adverse effects (risk) to 

non-target listed and non-listed animals and plants that could potentially affect the registration 

decision of cyflumetofen under FIFRA, the Food Quality Protection Act (FQPA), and the 

Endangered Species Act (ESA). 

2.5.1 Stressors of Concern 

Cyflumetofen forms many degradates. Eleven of these degradates are considered degradates of 

concern by EFED due to the presence of a cyano group (C≡N) and for some degradates, 

similarity in structure to the parent molecule. Ten of the 11 degradates of concern are considered 

to be major degradates (occurring as >10% of the applied radioactivity) in the registrantsubmitted fate studies. Only AB-12 was a minor degradate (<10% of the applied radioactivity). 

Again as stated in Section 2.1.3, the purpose of identifying a large and inclusive list of 

degradates of concern is to make the risk assessment more efficient by addressing the maximum 

possible exposure to degradates of potential concern, comparing this exposure to the most toxic 

degradate endpoints, and showing that the degradates individually and as a group do not pose 

risks to the environment. 

2.5.1.1 Aquatic Assessment 

For the aquatic exposure assessment, both cyflumetofen and its degradates of concern were 

included in the risk assessment. Calculating exposure to the parent was accomplished using 

standard EFED methods. However, estimating exposure to the degradates is more challenging 
15 

and was accomplished by making conservative assumptions of the estimated environmental 

concentrations (EECs) using a modified total toxic residue (TTR) approach. Typically in the 

TTR approach, all of the degradates of concern are assumed as toxic as the parent. This 

assumption is considered conservative (protective of the environment) for most chemicals 

because structural changes in molecules as pesticides degrade tend to result in chemicals that are 

less toxic. Additionally, degradates are typically smaller and often more water soluble than the 

parent molecule, which typically results in a molecule that is easier to excrete from target and 

non-target organisms resulting in more limited exposure durations. 

In the case of cyflumetofen and its degradates, the available toxicity data indicates that 

cyflumetofen is more toxic than its degradates. However, toxicity data is only available for 

selected degradates (Section 5). In the modified TTR approach used in this assessment, all of 

the degradates of concern are assumed to be as toxic as the most toxic degradate for which data 

is available rather than as toxic as the parent. The modified TTR approach essentially treats the 

parent and degradates of concern as a single chemical that 1) persists as long as any of the parent 

and degradates of concern persist in fate studies; and 2) occurs at concentrations over time 

commensurate with the sum of the concentrations of the parent and all degradates of concern at 

each sampling date in the fate studies. The chemicals included in the TTR approach include: 

cyflumetofen, A-1, A-2, A-18, AB-1, AB-7, AB-11, AB-12, AB-15, AB-1 dimer (which is dimer 

of two AB-1 molecules joined together), AU16 (which is dimer of two A-1 molecules joined 

together), and AU17 (which is dimer of an A-1 and AB-1 molecules joined together). The TTR 

half-lives are discussed in Section 3. Structures of cyflumetofen and its degradates are presented 

in Appendix Table C-1. 

This modified TTR approach is considered conservative (protective of environmental concerns) 

because the EECs of the most toxic degradate is likely to be less than the TTR EECs (i.e., not all 

of the TTR exposure is to that most toxic degradate). Further, the potential of the degradates of 

concern for which toxicity data is unavailable is discussed in terms of how much more toxic 

would that degradate have to be than the most toxic degradate for there to be an effect to aquatic 

ecological listed and non-listed species. 

2.5.1.2 Terrestrial Assessment 

For the terrestrial exposure assessment, exposure is based on the parent cyflumetofen alone since 

there is no defined process for including specific degradates in terrestrial exposure estimates 

using the current model (i.e., T-REX). Additionally, while consideration of degradates in the 

terrestrial assessment would lengthen the window of exposure, it would not affect the resulting 

RQs. 

2.5.2 Measures of Exposure 

To estimate risks to aquatic and terrestrial organisms from exposure to cyflumetofen, all 

exposure modeling and resulting risk conclusions are made based on maximum application rates, 

application methods, and any mitigation measures specifically indicated on the label. Models 

used to predict estimated environmental concentrations (EECs) of cyflumetofen are discussed on 
16 

OPP’s model website6

 and include: PRZM (Pesticide Root Zone Model) and EXAMS (EXposure 

Analysis Modeling System), T-REX, and TerrPlant. 

2.5.2.1 PRZM and EXAMS 

PRZM and EXAMS are simulation models coupled with the linkage program shell, PE5, which 

incorporates the standard scenarios developed by EFED. The models generate daily exposures 

and calculate 1-in-10 year EECs that may occur in surface water bodies adjacent to application 

sites. PRZM simulates pesticide fate and transport as a result of leaching, direct spray drift, 

runoff and erosion from an agricultural field, and EXAMS estimates environmental fate and 

transport of pesticides in a surface water body for a 30-year period. The standard scenarios used 

for ecological pesticide assessments assume application to a 10-hectare agricultural field that 

drains into an adjacent 1-hectare water body that is 2 meters deep (20,000 m3 volume) with no 

outlet. The combined models (i.e., PRZM/EXAMS) are designed to estimate pesticide 

concentrations found in the water body (standard pond) at the edge of the treated field. As such, 

they provide high-end values of the pesticide concentrations that might be found in ecologically 

sensitive environments following pesticide application. The location of the field is specific to 

the crop being simulated using site-specific information on the soils, weather, cropping, and 

management factors associated with the scenario. The crop/location scenario is intended to 

represent a high-end exposure site on which the crop is normally grown. Based on historical 

rainfall patterns, the receiving water body receives multiple runoff events during the years 

simulated. Weather and agricultural practices are simulated for 30 years so that the 10-year 

exceedance probability at the site can be estimated. The simulation is generated using 30 years 

of meteorological data, typically, encompassing the years from 1961 to 1990. Additional 

information on these models can be found at OPP’s model website7

. 

2.5.2.2 T-REX 

The T-REX model (v1.5.1; August 20, 2012), a Tier 1 model for screening-level assessments of 

pesticides, is used to estimate terrestrial animal exposure values resulting from possible dietary 

ingestion of cyflumetofen residues on vegetative matter and insects present on non-food and 

food items from exposure to cyflumetofen. This model incorporates the Kenaga nomograph, as 

modified by Fletcher et al. (1994), which is based on a large set of actual field residue data. The 

upper limit values from the nomograph represent the 95th percentile of residue values from actual 

field measurements (Hoerger and Kenaga, 1972). In all screening-level assessments, the 

organisms are assumed to consume 100% of their diet as one food type. The T-REX model 

determines (1) EECs for different food items of birds and mammals, (2) risk to birds and 

mammals via calculation of risk quotients (RQs), and (3) EECs (i.e., for tall grass) to evaluate 

risk to terrestrial invertebrates from dietary exposure. 

2.5.2.3 TerrPlant 

TerrPlant (v1.2.2; October 29, 2009), a Tier 1 model for screening-level assessments of 

pesticides, is used to estimate exposure to terrestrial plants from single pesticide applications; the 

model does not consider exposures to plants from multiple pesticide applications. TerrPlant 

 

6 http://www.epa.gov/oppefed1/models/terrestrial/index.htm

7 http://www.epa.gov/oppefed1/models/water/index.htm
17 

determines (1) EECs in runoff and in spray drift and (2) risk to non-listed and listed species of 

monocots and dicots inhabiting dry (upland) and semi-aquatic areas via calculation of RQs. 

2.5.2.4 AgDRIFT 

The AgDRIFT (v 2.1.1) model8 is used to estimate spray drift from aerial and ground spray 

applications. In addition, AgDRIFT is used to estimate buffer distances, i.e., the distance offsite 

where effects to non-target organisms are no longer expected, in cases where a proposed use of 

cyflumetofen results in a LOC exceedance. The AgDRIFT spray drift model has undergone 

thorough peer review and can be used to provide estimates of off-target spray drift deposition 

from aerial and ground boom application methods (USEPA 1997, 1999). Tier 1 AgDRIFT 

conditions are used to estimate spray drift deposition from pesticide applications as allowed by 

product labels. 

2.5.2.5 KABAM 

KABAM (KOW (based) Aquatic BioAccumulation Model; v. 1.0; April 9, 2009) is used to 

estimate potential bioaccumulation of hydrophobic organic pesticides in freshwater aquatic food 

webs and subsequent risks to mammals and birds via consumption of contaminated aquatic prey. 

KABAM is composed of two parts: 1) a bioaccumulation model estimating pesticide 

concentrations in aquatic organisms and 2) a risk component translating exposure and 

toxicological effects of a pesticide into risk estimates for mammals and birds consuming 

contaminated aquatic prey. The bioaccumulation portion of KABAM is based on an aquatic 

food web bioaccumulation model published by Arnot and Gobas (2004). The bioaccumulation 

portion of KABAM relies on a pesticide’s octanol-water partition coefficient (KOW) to estimate 

uptake and elimination constants through respiration and diet of aquatic organisms in different 

trophic levels. Pesticide tissue concentrations in aquatic organisms are calculated for different 

trophic levels of a food web through diet and respiration. In the risk component of KABAM, 

pesticide concentrations in aquatic organisms are used to estimate dose- and dietary-based 

exposures and associated risk quotients for mammals and birds consuming aquatic organisms. 

2.5.3 Measures of Effect 

Measures of effect are obtained from a suite of registrant-submitted guideline studies conducted 

with a limited number of surrogate species or studies found in the open literature. The test 

species are not intended to be representative of the most sensitive species but rather are selected 

based on their ability to thrive under laboratory conditions. The acute measures of effect 

routinely used for listed and non-listed animals in screening level assessments are the LD50, LC50

or EC50, depending on taxon (Table 2-6). LD stands for "Lethal Dose", and LD50 is the amount 

of a material (e.g., mg/kg-bw), given all at once, that is estimated to cause the death of 50% of a 

group of test organisms. LC stands for “Lethal Concentration”, and LC50 is the concentration of 

a chemical (e.g., mg/kg-diet; mg/L) that is estimated to kill 50% of a sample population. EC 

stands for “Effective Concentration”, and the EC50 is the concentration of a chemical that is 

estimated to produce some measured effect (e.g., mortality; reduced growth and/or reproduction) 

in 50% of the test population. Endpoints for chronic measures of exposure for listed and non-

 

8 http://www.agdrift.com
18 

listed organisms are the NOAEL or NOAEC. NOAEL stands for “No Observed-Adverse-EffectLevel” and refers to the highest tested dose (e.g., mg/kg-bw) of a substance that has been 

reported to have no harmful (adverse) effects on a test population. The NOAEC (i.e., “NoObserved-Adverse-Effect-Concentration”) is the highest test concentration (e.g., mg/kg-diet; 

mg/L) at which none of the observed results were statistically different from the control. For 

non-listed plants, the Agency uses EC25(IC25) for terrestrial plants and EC50 (IC50) for aquatic 

plants; for listed plants, the Agency uses the EC05 (IC05) or NOAEC (Table 2-7). 

Table 2-7. Acute and Chronic Measures of Effect 

Taxon Assessment Measure of Effect

Birds Acute/sub-acute Lowest LD50 (single oral dose)/LC50 (sub-acute dietary) 

Chronic Lowest NOAEC (21-week reproduction) 

Mammals Acute Lowest LD50 (single oral dose) 

Chronic Lowest NOAEC (two-generation reproduction) 

Terrestrial invertebrates Acute Lowest LD50 (acute contact) 

Terrestrial plants: 

monocots and dicots Acute/chronic 

Non-listed: Lowest EC25 (IC25) (seedling emergence and 

vegetative vigor) 

Listed: EC05 (IC05) or NOAEC associated with the lowest EC25

(IC25) (seedling emergence and vegetative vigor) 

Fish and aquatic 

invertebrates 

Acute Lowest EC50 or LC50 (acute toxicity tests) 

Chronic Lowest NOAEC (early life-stage or full life-cycle tests) 

Aquatic plants: 

vascular and non-vascular Acute/chronic Non-listed: Lowest EC50 (IC50) Listed: EC05 (IC05) or NOAEC associated with the lowest EC50

Where available, sublethal effects observed in both registrant-submitted and open literature 

studies will be evaluated qualitatively. Such effects may include behavioral changes (e.g., 

lethargy and changes in coloration). However, quantitative assessments of risks are limited to 

those endpoints that can be directly linked to the Agency’s assessment endpoints of impaired 

survival, growth, and reproduction. 

Information on the potential effects of cyflumetofen to non-target organisms is also collected 

from reviews of incidents associated with the use of cyflumetofen. 

The assessment of risk for direct effects to non-target organisms makes the assumption that the 

toxicity of cyflumetofen to birds is similar to terrestrial-phase amphibians and reptiles. The 

same assumption is made for the relationship between fish and aquatic-phase amphibians. 

2.5.4 Integration of Exposure and Effects 

Risk characterization is the integration of exposure and ecological effect characterizations to 

determine the potential ecological risk from the use of cyflumetofen and the likelihood of direct 

and indirect effects to non-target organisms in aquatic and terrestrial habitats. The exposure and 

effects data are integrated to evaluate potential adverse ecological effects on non-target species. 

The risk quotient (RQ) method will be used to compare estimated exposure and measured 

toxicity values. Acute and chronic EECs will be divided by acute and chronic toxicity values. 

The resulting, unitless RQs will then be compared to the Agency’s Levels of Concern (LOC) 

(USEPA, 2004). As outlined in the Overview Document (USEPA, 2004), the likelihood of 

effects to individual organisms from particular uses of a chemical may also be estimated using 

the probit dose-response slope and either the LOC or the actual calculated risk quotient value. 
19 

Collectively, these methods are used to indicate when cyflumetofen’s use, as directed on the 

labels, has the potential to cause adverse direct or indirect effects to non-target organisms. 

2.5.5 Endangered Species Assessments 

Consistent with the Agency’s responsibility under the Endangered Species Act (ESA), the 

Agency evaluates risks to Federally-listed threatened and/or endangered (listed) species from 

registered uses of cyflumetofen. This assessment is conducted in accordance with the Overview 

Document (USEPA, 2004), provisions of the Endangered Species Act (ESA), and the Services’ 

Endangered Species Consultation Handbook (USFWS/NMFS, 1998). 

The assessment of effects associated with the registration of cyflumetofen is based on an action 

area. The action area is considered to be the area directly or indirectly affected by the federal 

action, as indicated by the exceedance of Agency LOCs used to evaluate direct or indirect 

effects. The Agency’s approach to defining the action area under the provisions of the Overview 

Document (USEPA, 2004) considers the results of the risk assessment process to establish 

boundaries for that action area with the understanding that exposures below the Agency’s 

defined LOCs constitute a no-effect threshold. For the purposes of this assessment, attention is 

focused on the footprint of the action (i.e., the area where cyflumetofen application occurs) and 

all areas where offsite transport (i.e., spray drift, runoff, etc.) may result in potential exposure 

that exceeds the Agency’s LOCs. Specific measures of ecological effect that define the action 

area for listed species include any direct and indirect effects and/or potential modification of its 

critical habitat, including reduction in survival, growth, and reproduction as well as the full suite 

of sublethal effects available in the effects literature. Therefore, the action area extends to a 

point where environmental exposures are below any measured lethal or sublethal effect threshold 

for any biological entity at the whole organism, organ, tissue, and cellular level of organization. 

In situations where it is not possible to determine the threshold for an observed effect, the action 

area is assumed to encompass the entire United States. 

2.5.6 Endocrine Disruptor Screening Program 

As required by FIFRA and the Federal Food, Drug, and Cosmetic Act (FFDCA), EPA reviews 

numerous studies to assess potential adverse outcomes from exposure to chemicals. 

Collectively, these studies include acute, subchronic and chronic toxicity, including assessments 

of carcinogenicity, neurotoxicity, developmental, reproductive, and general or systemic toxicity. 

These studies include endpoints which may be susceptible to endocrine influence, including 

effects on endocrine target organ histopathology, organ weights, estrus cyclicity, sexual 

maturation, fertility, pregnancy rates, reproductive loss, and sex ratios in offspring. For 

ecological hazard assessments, EPA evaluates acute tests and chronic studies that assess growth, 

developmental and reproductive effects in different taxonomic groups and reviews these data and 

selects the most sensitive endpoints for relevant risk assessment scenarios from the existing 

hazard database. However, as required by FFDCA section 408(p), cyflumetofen is subject to the 

endocrine screening part of the Endocrine Disruptor Screening Program (EDSP). 

EPA has developed the EDSP to determine whether certain substances (including pesticide 

active and other ingredients) may have an effect in humans or wildlife similar to an effect 

produced by a “naturally occurring estrogen, or other such endocrine effects as the Administrator 
20 

may designate.” The EDSP employs a two-tiered approach to making the statutorily required 

determinations. Tier 1 consists of a battery of 11 screening assays to identify the potential of a 

chemical substance to interact with the estrogen, androgen, or thyroid (E, A, or T) hormonal 

systems. Chemicals that go through Tier 1 screening and are found to have the potential to 

interact with E, A, or T hormonal systems will proceed to the next stage of the EDSP where EPA 

will determine which, if any, of the Tier 2 tests are necessary based on the available data. Tier 2 

testing is designed to identify any adverse endocrine-related effects caused by the substance, and 

establish a dose-response relationship between the dose and the E, A, or T effect. 

Under FFDCA section 408(p), the Agency must screen all pesticide chemicals for endocrine 

effects. Between October 2009 and February 2010, EPA issued test orders/data call-ins for the 

first group of 67 chemicals, which contains 58 pesticide active ingredients and 9 inert 

ingredients. For additional information on the EDSP program, visit http://www.epa.gov/endo/. 

2.6 Data Gaps 

Submission of data to eliminate data gaps would reduce uncertainties in the ecological risk 

assessment. Data gaps have been assigned either a low or high potential to add value to the 

ecological risk assessment. While still considered data gaps according to 40 CFR Part 158, data 

from low potential studies are unlikely to change risk conclusions, and alternate methods and 

weight of evidence can be used in the absence of data. In contrast, data from high potential 

studies are likely to impact risk conclusions and allow the Agency to be better able to 

characterize potential risks by eliminating uncertainties for both non-listed and listed species that 

cannot be accounted for using alternate methods or weight of evidence. 

2.6.1 Environmental fate 

Table 2-8 provides environmental fate studies by MRID that offer data for each guideline 

requirement as well as study classifications and whether or not further data are needed to support 

the ecological risk assessment (i.e., whether there is a data gap). 

Table 2-8. Environmental Fate Data for Cyflumetofen and Remaining Data Gaps

Guideline Description MRID (parent unless 

otherwise specified) 

Classification Data 

Gap? 

Comments 

835.2120 

161-1 Hydrolysis 48542624 

48542625 

Supplemental 

Acceptable No 

MRID 48542624 did 

not identify/quantify 

degradates. 

835.2240 

161-2 Photodegradation in Water 48542627 Acceptable No 

835.2410 

161-3 Photodegradation in Soil 48542750 (A-label) 

48542751 (B-label) 

Acceptable 

Acceptable No 

835.4100 

162-1 

Aerobic 

Soil Metabolism - parent 

48542745 

48542748 

48542752 

Acceptable 

Acceptable 

Acceptable 

No 

Of the 8 soils 

studied, only 2 used 

an A-label. 

Aerobic 

Soil Metabolism - 

degradate 

48542754 (B-1) 

48542755 (AB-1) 

48542756 (B-3) 

Supplemental 

Supplemental 

Supplemental 

No 

Did not identify/ 

quantify degradates. 

Not radio-labeled. 
21 

Guideline Description MRID (parent unless 

otherwise specified) 

Classification Data 

Gap? 

Comments 

835.4200 

162-2 

Anaerobic 

Soil Metabolism 48542749 Acceptable No

835.4300 

162-4 

Aerobic Aquatic 

Metabolism 

48542768 

48542770 

48542771 

Acceptable 

Acceptable 

Acceptable 

No

835.4400 

162-3 

Anaerobic Aquatic 

Metabolism 48542769 Acceptable No

835.1230 

163-1 

Sediment and soil 

Adsorption/ Desorption 

48542759 (parent) 

48542760 (B-1) 

48542761 (AB-1) 

48542762 (B-3) 

48542763 (B-1, B-3, and A-2)

48542786 (AB-1 dimer) 

Supplemental 

Supplemental 

Supplemental 

Supplemental 

Supplemental 

Supplemental 

No Did not use Agency 

approved methods. 

835.1240 

163-1 Soil column leaching 48542764 (B-1) 48542765 (B-1) 

Supplemental 

Supplemental No Not required 

835.6100 

164-1 

Terrestrial Field 

Dissipation 

48542757 Not classified 

yet 

In 

review 

Storage stability 

study is not finished. 

Preliminary results 

show parent not 

stable for as long as 

samples stored 

before analysis. 

850.6100 Analytical Method - Soil 

48542828 (parent, A-2, B-3, 

B-1, and AB-1 dimer) 

48542647 (parent, A-2, B-3, 

B-1, and AB-1 dimer) 

Acceptable 

Acceptable No 

850.6100 

Analytical Method - Water 

48542650 (parent) 

48542651 (B-1) 

48542652 (B-3) 

Acceptable 

Acceptable 

Acceptable 

No 

850.6100 Analytical MethodSediment 48542657 (AB-1) Acceptable No 

850.1730 

165-4 Accumulation in fish 48542785 Acceptable No Did not identify/ quantify degradates. 

Because there were no aquatic risks identified in this assessment, there are no fate related studies 

that would have a high potential to affect the ecological risk assessment for cyflumetofen. 

Data from the following fate guideline studies are considered to have low potential to add value 

to the ecological risk assessment for cyflumetofen: 

Guideline 835.1240 – Soil Column Leaching of Parent: Cyflumetofen has hydrophobic 

characteristics and is unlikely to persist long in wet aerobic/anaerobic environments. Therefore, 

it is unlikely that the parent will leach in substantial quantities. 

Guideline 835.6100 – Terrestrial Field Dissipation: The 2-year storage stability is incomplete 

but interim reports appear to show that cyflumetofen cannot be stored for long in frozen soil 
22 

samples without degradation. Therefore, it is likely that the study will need to be repeated, but a 

non-radiolabeled field study cannot address the unextracted residue issue using the current 

analytical methods. If an analytical method using harsher extraction methods was shown to 

greatly reduce unextracted residues, it would be more useful to repeat the terrestrial field 

dissipation study with the harsher extraction methods. 

2.6.2 Ecological Effects 

Table 2-9 provides ecological effects studies by MRID that offer data for each guideline 

requirement as well as study classifications and whether or not further data are needed to support 

the ecological risk assessment (i.e., whether there is a data gap). 

Table 2-9. Ecological Effects Data for Cyflumetofen and Remaining Data Gaps

Guideline Description MRID (parent unless 

otherwise specified) 

Classification Data 

Gap? 

Potential for 

Additional Data 

to Add Value 

850.1010 Acute toxicity 

freshwater invertebrates 

48542789 

48542790 (A-2) 

48542787 (B-1) 

48542788 (B-2) 

48542921 (form.) 

Acceptable 

Acceptable 

Acceptable 

Supplemental 

Supplemental 

No NA 

850.1025 

850.1055 

Acute toxicity 

estuarine/marine mollusk 48542810 Acceptable No NA 

850.1035 

850.1045 

Acute toxicity 

estuarine/marine invertebrate 48542711 Acceptable No NA 

850.1075 

Acute toxicity freshwater fish

(cold water species) 

48542779 

48542780 (form.) 

Acceptable 

Supplemental No NA 

Acute toxicity freshwater fish 

(warm water species) 

48542780 

48542782 (A-2) 

48542781 (B-1) 

Acceptable 

Acceptable 

Acceptable 

No NA 

Acute toxicity 

estuarine/marine fish 48542812 Acceptable No NA 

850.1300 Aquatic invertebrate life 

cycle (freshwater) 48542791 Acceptable No NA 

850.1350 Aquatic invertebrate life 

cycle (saltwater) -- -- Yes Low 

850.1400 

Fish early life stage 

(freshwater) 48542783 Supplemental Yes Low 

Fish early life stage 

(saltwater) -- -- Yes Low 

850.1740 Whole sediment: acute 

marine invertebrates 48542798 Acceptable No NA 

Whole sediment: chronic 

freshwater invertebrates 

48542802 

48542801 (AB-1) 

48542803 (AB-1 dimer) 

Acceptable 

Acceptable 

Acceptable 

No NA 

850.2100 Avian oral toxicity (upland 

game or waterfowl species) 

48542772 

48542773 Acceptable No NA 
23 

Guideline Description MRID (parent unless 

otherwise specified) 

Classification Data 

Gap? 

Potential for 

Additional Data 

to Add Value 

Avian oral toxicity 

(passerine species) 48542774 Acceptable No NA 

850.2200 

Avian dietary toxicity 

(upland game species) 48542775 Acceptable No NA 

Avian dietary toxicity 

(waterfowl species) 48542776 Acceptable No NA 

850.2300 

Avian reproduction 

(upland game species) 48542777 Acceptable No NA 

Avian reproduction 

(waterfowl species) 48542778 Acceptable No NA 

850.3020 Honeybee acute contact 

toxicity 48542805 Acceptable No NA 

850.4100 Seedling emergence 

(terrestrial plants) 48542933 Supplemental Yes High 

850.4150 Vegetative vigor 

(terrestrial plants) 48542932 Acceptable No NA 

850.4400 

Aquatic plant growth 

(aquatic vascular plant 

toxicity) 

48542804 Acceptable No NA 

850.4500 

Aquatic plant growth 

(aquatic non-vascular plant: 

algal toxicity) 

48542792 

48542793 

48542795 

48542796 (AB-11) 

48542797 (B-1) 

48542922 (form.) 

Acceptable 

Acceptable 

Acceptable 

Acceptable 

Supplemental 

Supplemental 

No NA 

850.4550 

Aquatic plant growth 

(aquatic non-vascular plant: 

cyanobacteria toxicity) 

48542794 Acceptable No NA 

form. = formulation; NA = not applicable; FW = freshwater; SW = saltwater 

Data from the following guideline studies are considered to have high potential to add value to 

the ecological risk assessment for cyflumetofen: 

Guideline 850.4100 – Seedling Emergence and Seedling Growth: Acceptable seedling 

emergence data are not available. The submitted seedling emergence study (MRID 48542933) 

was classified as Supplemental because for the most sensitive monocot – oat, dry weight and 

shoot length of the lowest treatment group (i.e., 0.000706 lb a.i./A) were significantly reduced 

(i.e., 33.2 and 27.3 %, respectively) when compared to the control group resulting in the lack of a 

NOAEC for monocots. In addition, an EC25 for monocots could not be determined because the 

oat endpoints of dry weight and shoot length displayed an atypical concentration-response 

relationship leading to issues with model convergence (see Figure 5-1). A continuation, Tier II 

test with oat is necessary to reduce uncertainty in characterizing risk to listed and non-listed 

monocots and is considered to have a high potential to add value to the ecological risk 

assessment. 
24 

Data from the following guideline studies are considered to have low potential to add value to 

the ecological risk assessment for cyflumetofen: 

Guideline 850.1350 – Mysid Chronic Toxicity Test: Aquatic invertebrate life cycle toxicity 

data for an estuarine/marine invertebrate are required under 40 CFR Part 158 if the product is 

expected to enter the environment in significant concentrations because of its expected use or 

mobility patterns. No studies have been submitted for this data requirement. Given that there is 

no evidence to indicate that estuarine/marine animals are substantially more sensitive to 

cyflumetofen than freshwater animals, fulfilling this data requirement has a low potential to add 

value to the ecological risk assessment. In the absence of these data, toxicity to estuarine/marine 

invertebrates from chronic exposure to cyflumetofen will be characterized using toxicity data for 

freshwater invertebrates (e.g., Daphnia). 

Guideline 850.1400 – Fish Early Life Stage Toxicity Test, freshwater: Acceptable early life 

stage toxicity data are not available for a freshwater fish. The submitted freshwater fish early 

life stage study was classified as supplemental because the high:low ratio and percent coefficient 

of variation for measured test concentrations were 2.1 and 27%, respectively, exceeding the 1.5 

and 20% maxima for acceptable variability in aquatic studies (MRID 48542783). Since 

repeating this study is likely to yield the same variability with respect to exposure concentrations 

due to the rapid hydrolysis of cyflumetofen in aqueous environments, fulfilling this data 

requirement has a low potential to add value to the ecological risk assessment. In the absence of 

these data, toxicity to freshwater fish from chronic exposure to cyflumetofen will be 

characterized using the NOAEC (= 31.6 μg/L) from the submitted study (MRID 48542783) and 

acknowledging the associated uncertainty. 

Guideline 850.1400 – Fish Early Life Stage Toxicity Test, estuarine/marine: Early life stage 

toxicity data for an estuarine/marine fish are required under 40 CFR Part 158 if the product is 

expected to enter the environment in significant concentrations because of its expected use or 

mobility patterns. No studies have been submitted for this data requirement. Given that there is 

no evidence to indicate that estuarine/marine animals are substantially more sensitive to 

cyflumetofen than freshwater animals, fulfilling this data requirement has a low potential to add 

value to the ecological risk assessment. In the absence of these data, toxicity to estuarine/marine 

fish from chronic exposure to cyflumetofen will be characterized using toxicity data for 

freshwater fish. 

3 Fate and Transport Characterization 

Cyflumetofen is not persistent in the environment and rapidly converts to degradates via abiotic 

hydrolysis reactions (DT50 = 9.75 hours at pH 7) and biotic reactions with (DT50 of less than 22 

days). Many of the degradates (e.g., A-2, A-18, AB-1, and B-1) are much more persistent than 

the parent. Maximum formation fractions and limited chemical property and mobility data for 

the degradates identified in cyflumetofen fate studies appear in Appendix Table C-1, and 

transformation pathways are depicted in Appendix Figures C-1 through C-5 for abiotic 

hydrolysis, aquatic photolysis, aerobic soil metabolism, aerobic aquatic metabolism, and 

anaerobic aquatic metabolism, respectively. 
25 

Cyflumetofen has two rings, both of which were radio-labeled in fate studies. The phenyl ring 

label (see cyflumetofen structure in Figure 3-1 for location) is referred to as the A label, and the 

tolyl ring label is referred to as the B label. These label designations were used in naming the 

cyflumetofen degradates. Degradates that retain only the A label (phenyl ring) typically are 

named with the prefix “A”, whereas degradates that retain only the B label (tolyl ring) typically 

are named with the prefix “B”. Degradates that retain both rings are named with the prefix 

“AB”. 

Figure 3-1. Cyflumetofen chemical structure with A and B rings denoted and bonds 

identified that are important in the initial degradation of the molecule through most fate 

pathways.

There are two bonds that readily break (denoted in Figure 3-1) in all of the fate studies involving 

water other than photolysis (i.e., hydrolysis, aerobic and anaerobic soil and aquatic metabolism, 

and terrestrial field dissipation studies). If the bond denoted 1 in Figure 3-1 breaks, the A and B 

degradates are formed. If the bond denoted 2 in Figure 3-1 breaks (or less typically, some other 

bond on the same unlabeled side chain), the AB degradates are formed. 

“B” degradates (i.e., tolyl ring degradates; B-1 and B-3) are water soluble (range: 363.3 – 13,000 

mg/L), have low estimated Koc’s (range: 79 – 121.5 L/kg-organic carbon), and lack the cyano 

group (C≡N) of the parent. “A” degradates (i.e., phenyl ring degradates; A-1, A-2, A-12, and A18) are also water soluble (range: 28.94 – 201.8 mg/L) and have low estimated Koc’s (range: 

113.7 – 1200 L/kg-organic carbon), but most (A-1, A-2, and A-18) retain the cyano group of the 

parent. The “AB” degradates (AB-1, AB-7, AB-11, AB-15, and AB-12) have low water 

solubility (range: 0.01 – 0.142 mg/L), high estimated Koc’s (range: 10,400 – 85,630 L/kgorganic carbon), and retain the cyano group of the parent. 

Some of the degradates that have a cyano group (A-1 and AB-1) formed dimers in the fate 

studies (AB-1 Dimer, AU16, and AU17). The dimers are formed by two molecules with cyano 

groups bonding together (2 only) at the carbon to which the cyano group is attached in each 

molecule (the carbon atom located between the 1 and 2 bonds in Figure 3-1). It is not clear 

whether these dimers would actually form in the environment or simply form during the sample 

extraction process. These dimers are predicted (EpiSuite v4.10) to have extremely low water 

solubility (range: 4×10-10 – 7×10-3 mg/L) and high Koc’s (range: 50,600 – 1.6×108 L/kg-organic 

carbon). 

CF3 O

NC

O

O

O

A

B

1 2
26 

For comparison, cyflumetofen has a comparatively low water solubility of 0.0277 mg/L at 20oC 

(MRID 48542621) and Koc of 131,826 L/kg-organic carbon. Only degradates AB-11, AB-12, 

AB-1 dimer, AU16 (dimer), and AU17 (dimer) are predicted to have lower water solubilities 

than the parent. Similarly, only degradates AB-12, AB-1 dimer, and AU17 (dimer) are predicted 

to have higher Kocs than the parent. Therefore, the vast majority of the degradates are expected 

to be more mobile than the parent. (All degradate data on solubility and Koc data were estimated 

using EpiSuite v4.10 and are included in Appendix Table C-1. For purposes of consistency 

with the estimated degradate data provided, the water solubility and Koc values reported in this 

paragraph and Appendix Table C-1 are also EpiSuite estimates. The text following this point in 

the document is based on registrant-submitted cyflumetofen fate studies.) 

3.1 Degradation 

3.1.1 Hydrolysis 

Cyflumetofen’s hydrolytic degradation appears to be pH dependent, with degradation rate 

increasing (half-life time [DT50] decreasing) and with increasing pH. The DT50 values decrease 

from 7.42 days at pH 4, to 6.16 days at pH 5, to 0.406 days (~9.7 hours) at pH 7, to 0.00518 days 

(~7.5 minutes) at pH 9 (T = 25oC; average of both labels, MRID 48542625). Hydrolytic 

degradation in the A-labeled studies yielded: A-1, A-18, A-2, and AB-1 (Appendix Figure C-1). 

All of the A-labeled hydrolysis degradates retain a cyano-group and therefore, are of concern. 

Therefore in terms of TTR half-life calculation, cyflumetofen is stable to hydrolysis since it only 

produces degradates of concern (Appendix Table D-1). Hydrolytic degradation in the B-labeled 

studies yielded: AB-1 and B-1. (Notice, the production of B-1 which does not have a cyanogroup in the B-label study does not indicate that the TTR half-life should not be considered 

stable since it results in the production of A-1. A-1 just does not show up in the B-label studies.) 

A second study (MRID 48542624), measured hydrolysis rates at 3 temperatures (20, 25, and 

40oC) and three pHs (4, 7, and 9). (No degradates were identified or quantified in this study.) At 

25oC, the results were similar (9.25 days at pH 4, 5 hours at pH 7, and 12 minutes at pH 9). 

3.1.2 Aquatic Photolysis 

The aqueous photolysis study shows a photo transformation half-life in distilled water of about 

1.2 hours or 0.0511 days (T = 25oC; average of both labels, MRID 48542627). This same study 

provides a similar estimate of 0.04 days natural water at 25oC (average of both labels). 

Degradates produced included degradates of concern (A-1, A-18, A-2, AB-1, AB-6, AB-7, and 

AB-15) and degradates not of concern (A-14, A-12, and B-1) (Appendix Figure C-2). The TTR 

half-life in distilled water is 17.6 days (Appendix Table D-1). 

3.1.3 Soil photolysis 

Soil photolysis studies were conducted for the parent, cyflumetofen, with a DT50 value of 4.9 

days (A-label, MRID 48542750) and 5.9 days (B-label, MRID 48542751). Degradates produced 

included degradates of concern (AB-8, AB-11, and AB-12) and degradates not of concern (AB13 and B-1). Maximum occurrence of unextracted residues ranged from 25.5 to 47.7% of 

applied radioactivity. The highest unextracted residue value came from the A-labeled soil, 
27 

possibly indicating some contribution from an A-labeled chemical that would not show up in the 

B-labeled studies (~22% more in A- than B-labels from the same soil). The TTR half-life from 

the A-label study is 68.5 days (Appendix Table D-1). 

3.1.4 Aerobic Soil Metabolism 

Aerobic soil metabolism DT50 values from eight soils were available from registrant-submitted 

studies for the parent, cyflumetofen, with half-lives ranging from 2.24 to 13.3 days (MRIDs 

48542745, 48542748, and 48542752). However, only two of these soils were studied with an Alabel radio-tracer. Degradates produced included degradates of concern (A-1, A-2, AB-1, AU17, 

and AB-1 dimer) and degradates not of concern (B-1, B-3, and A-12) (Appendix Figure C-3). 

Maximum occurrence of unextracted residues ranged from 21.6 to 43.4% of applied 

radioactivity. The highest unextracted residue value came from the A-labeled soil, possibly 

indicating some contribution from an A-labeled chemical that would not show up in the Blabeled studies (~8-10% more in A- than B-labels from the same soil). The TTR half-lives from 

the A-label studies are 64.1 and 846 days (Appendix Table D-1). 

Aerobic soil metabolism studies using non-radiolabeled material were conducted for three of the 

degradates of cyflumetofen. Because non-radiolabeled material was used, no estimate of 

unextractable residues can be made. Additionally, no degradates were identified in these studies. 

The degradate B-1 was studied in three European soils yielding degradation curves that roughly 

approximated first-order degradation kinetics with half-lives of 4.98, 16.8, and 36.3 days 

(Appendix Table D-2 – separate from the parent degradation graphs in Appendix Table D-1). 

Similarly, B-3 yielded degradation curves that roughly approximated first-order degradation 

kinetics with half-lives of 6.32, 9.56, and 8.46 days. Both of these chemicals (B-1 and B-3) have 

relatively similar structures, are expected to be hydrophilic (see EpiSuite estimated water 

solubilities and Kocs in Appendix Table C-1), and seem to behave very similarly in terms of 

aerobic soil degradation (similar half-lives and shape of the degradation curve). 

Degradate AB-1 (non-radiolabeled) was also studied in three European soils, yielded radically 

different degradation curves from those of B-1 and B-3. The AB-1 degradation curves initially 

dropped steeply to 14%, 13%, and 11% of applied radioactivity at their 24 hour sampling. These 

degradation curves then flattened-out to yield an almost linear decline for the remaining 119 days 

of the studies for final measurements at 120 days of 8%, 6%, and 3% of applied radioactivity. 

AB-1 is expected to be hydrophobic. 

The Agency’s interpretation of these AB-1 studies is the initial decline is likely due to the 

formation of unextractable residues and potentially, formation of dimers, rather than rapid 

degradation to simpler molecules. In the radio-labeled aerobic soil metabolism studies, AB-1 was 

a major degradate that persisted to the end of the studies. Potentially, AB-1 may persist in soil 

and sediment in some form of equilibrium with soil water or overlying and pore water in aquatic 

systems. Additional data from longer-term (at least 1 year duration) radio-labeled studies using 

more rigorous extraction methods (optimized to extract AB-1 and its degradates) would be 

beneficial in understanding the fate of this degradate. 

3.1.5 Anaerobic Soil Metabolism 
28 

Anaerobic soil metabolism DT50 values from four soils were available from registrant-submitted 

studies for the parent, cyflumetofen, with half-lives ranging from 1.78 to 10.4 days (MRID 

48542749). However, only one of these soils was studied with an A-label radio-tracer. 

Degradates produced included degradates of concern (A-1, A-2, AB-1, and AB-1 dimer) and 

degradates not of concern (B-1, B-3, and A-12). Maximum occurrence of unextracted residues 

ranged from 16.3 to 32.4% of applied radioactivity. The highest unextracted residue value came 

from the A-labeled soil, possibly indicating some contribution from an A-labeled chemical that 

would not show up in the B-labeled studies (~10% more in A- than B-labels from the same soil). 

The TTR half-life from the A-label study is 264 days (Appendix Table D-1). 

3.1.6 Aerobic Aquatic Metabolism 

Aerobic aquatic metabolism DT50 values from four systems were available from registrantsubmitted studies for the parent, cyflumetofen, with half-lives ranging from 0.3 to 21.4 days 

(MRIDs 48542768, 48542770, and 48542771). All of these systems were studied with both Aand B-label radio-tracers. Degradates produced included degradates of concern (A-1, A-2, AB1, and AB-1 dimer) and degradates not of concern (B-1, B-3, and A-12) (Appendix Figure C-4). 

Maximum occurrence of unextracted residues ranged from 14 to 44.2% of applied radioactivity. 

The highest unextracted residue values came from A-labeled soils, probably indicating some 

contribution from an A-labeled chemical that would not show up in the B-labeled studies (~2.7 - 

20% more in A- than B-labels from the same soil). The TTR half-lives from the A-label studies 

range from 16.4 to 149 days (Appendix Table D-1). 

3.1.7 Anaerobic Aquatic Metabolism 

Anaerobic aquatic metabolism DT50 values from two systems were available from registrantsubmitted studies for the parent, cyflumetofen, with half-lives ranging from 4.76 to 21.5 days 

(MRID 48542769). All of these systems were studied with both A- and B-label radio-tracers. 

Degradates produced included degradates of concern (A-2 and AB-1) and degradates not of 

concern (B-1 and A-12) (Appendix Figure C-5). Maximum occurrence in each system of 

unextracted residues ranged from 4.1 to 12.1% of applied radioactivity. However, unlike the 

other metabolism studies, there was no difference in unextracted residues in terms of percent 

applied radioactivity in one system (Pennsylvania), whereas the other system (Florida) had the 

highest unextracted residue values in the B-labeled samples (~8% more in B- than A-labeled 

samples from the Florida soil). The TTR half-lives from the A-label studies range from 3780 

(Pennsylvania) to 31,300 (Florida) days (Appendix Table D-1). 

3.2 Mobility 

3.2.1 Volatility 

Cyflumetofen appears to be non-volatile. This is supported by its water solubility (0.0277 mg/L 

at 20oC; MRID 48542621) and low vapor pressure (< 4.43 × 10-8 torr at 25oC; MRID 48542611) 

and Henry’s Law constant (< 9.3 × 10-7 Pa*m3

/mol at 20oC; MRID 48542612). 

3.2.2 Adsorption/desorption – Parent 
29 

The organic carbon normalized soil adsorption coefficient (Koc) of OK-5101 pure was 

determined by an HPLC method. Phenol, 4-methylbenzamide, methylbenzoate, naphthalene, 

1,2,3-trichlorobenzene, fenthion, phenanthrene and p,p-DDT were used for the calibration 

standards. The organic carbon normalized soil adsorption coefficient (Koc) of OK-5101 pure 

was calculated to be 131,826 L/kgoc (MRID 48542759). 

3.2.3 Adsorption/desorption – Degradates 

The adsorption behavior of B-1 to soil was studied in three soils using the batch equilibrium 

method: Speyer 2.2 soil (2.29% organic carbon (OC), loamy sand), Speyer 2.3 soil (1.02% OC, 

sandy loam) and Speyer 6S soil (1.9% OC, sandy clay). Adsorption isotherms were determined 

over a concentration range of 0.1-5 mg/L. Based on the kinetics experiment, B-1 hardly adsorbs 

to the soil. Therefore, the equilibrium time could not be determined accurately. B-1 adsorbs 

only very weakly to soil and can be considered highly mobile (MRID 48542760). 

AB-1 in soils was studied in the same three soils. At a soil:solution ratio of only 1:200 the 

percentage adsorption was ≥87% in Speyer 2.2 and Speyer 2 3 soils and ≥30% in Speyer 6S soil. 

Given the strong adsorption of AB-1 to soil even at a very low soil:solution ratio and the low 

water solubility (0.0277 mg/L) in combination with the limit of quantification of 0.005 mg/L, 

isotherms could not be determined. Instead, the adsorption coefficient was determined in 

duplicate for each soil at soil solution ratios of 1:100 and 1:200. Based on the resulting Kom 

values (≥2.6 x 103

 ml/g) AB-1 should be considered immobile (MRID 48542761). 

B-3 in soils was studied in the same three soils. Adsorption of B-3 on soil could be described by 

Freundlich adsorption isotherms. Kfoc values were 11.726 (Speyer 2.2), 12.202 (Speyer 6S), and 

16.863 L/kg (Speyer 2.3) for a mean of 13.597 and 1/n values were 0.874, 0.959 and 1.039, 

respectively (mean 0.957) (MRID 48542762). 

The adsorption/desorption behavior of the radiolabeled metabolites of cyflumetofen B-1, B-3 and 

A-2 was investigated on different US and European soils. The six soils covered a range of pH 

from 5.8 to 8.1, a range of organic carbon content from 0.28% to 3.84% and four different 

USDA textural classes: Silty Clay Loam, Loam, Loamy sand and Sandy Loam. The average 

adsorption Koc was 4.4, 22.8, and 865 for B-1, B-3 and A-2, respectively (MRID 48542763). 

The adsorption/desorption potential of the AB-1 dimer was investigated in four US soils, which 

included sandy loam, clay loam, sand, and loam and one German sandy loam soil. The soils 

covered a range of pH from 6.1 to 8.1 and a range of organic carbon content from 0.08 to 2.26. 

The adsorption coefficients Kd and Koc were estimated using 1 concentration level (0.28 

ng/mL). The estimated Kd values for all the test soils ranged from 237.47 to 4341.91 L/kg. The 

adsorption coefficient, Koc, derived from the Kd values for the test soils was > 103,000 L/kg, 

indicating that the test substance AB-1 dimer is immobile in the test soils. The Koc value was 

also estimated by the HPLC method to be 8,315,788 L/kg. 

3.3 Field Studies 

The interpretation of the terrestrial field dissipation studies (MRID 48542757) awaits the 

completion of the storage stability study (interim report is MRID 48542829). Some of the 
30 

terrestrial field dissipation samples were held under frozen conditions for 2 years. The interim 

report indicates that the parent cyflumetofen does not appear to be stable under the frozen 

storage conditions used in the study. This lack of stability of the parent would likely reduce the 

concentrations of the parent chemical measured at each time point and potentially enhance the 

concentration of degradates at each time point. It appears likely that the terrestrial field 

dissipation study may need to be repeated. 

3.4 Bioconcentration 

The measured BCF is approximately 200× in whole fish (other tissues were not measured 

separately) based on TRR (total radioactive residues). The BCF study is somewhat problematic 

in that the TRR was still increasing at the end of the accumulation phase. The identity of 

radioactivity measured in the BCF study was not determined in the fish BCF study. Therefore, it 

is unknown whether it is parent, degradate(s), or some combination of parent and degradate(s) 

that is accumulating in the fish. However, the rate of accumulation appears to slow over the 21 

day accumulation phase with concentrations only doubling from day 1 (approximately 100×) to 

day 21 (approximately 200×) (MRID 48542785). 

4 Exposure Assessment 

4.1 Terrestrial Exposure 

4.1.1 Birds, Mammals, and Terrestrial Invertebrates 

Input parameters for T-REX9 (Table 4-1) include a maximum application rate, number of 

applications, application interval, a default EFED foliar dissipation half-life of 35 days, and 

definitive toxicity endpoints for birds and mammals. 

Table 4-1. Input Parameters for T-REX Modeling Scenarios 

Use Maximum 

Single 

Application 

Rate 

(lb a.i./A) 

Maximum 

Number of 

Applications

 (Minimum 

Application 

Interval, Days) 

Other Parameters1

Citrus 

Grapes 

Pome fruits 

Strawberries 

Tree nuts 

Tomatoes 

Ornamentals 

0.2 2 (14) 

Foliar dissipation half-life = 35 days (default) 

Avian NOAEC = 154 mg a.i./kg-diet 

(bobwhite quail; MRID 48542777) 

Mammalian NOAEC = 150 mg/kg-diet (9.21 mg/kg-bw) 

(rat; MRID 48542702) 1

 Avian acute oral, avian sub-acute dietary, and mammalian acute oral endpoints are non-definitive (i.e., >) and are 

thus not included in this table because they cannot be used to calculate RQs. 

 

9 http://www.epa.gov/oppefed1/models/terrestrial/index.htm#trex
31 

Results of T-REX modeling of cyflumetofen residue levels on dietary food items of mammals 

and birds are provided in Tables 4-2, 4-3, and 4-4. Results include dietary-based values (i.e., 

mg/kg-food item) and dose-based values (i.e., mg/kg-bw). 

Table 4-2. Avian Dose-Based (mg/kg-bw) Estimated Exposure Concentrations (EECs)a

Use Feeding Category 

Dose-Based EECs (mg/kg-bw)b

Small 

(20 g) 

Medium 

(100 g) 

Large 

(1000 g) 

Citrus 

Grapes 

Pome fruits 

Strawberries 

Tree nuts 

Tomatoes 

Ornamentals

Short grass 96.10 54.80 24.53 

Tall grass 44.04 25.12 11.24 

Broadleaf plants 54.05 30.82 13.80 

Fruits/pods 6.01 3.42 1.53 

Arthropods 37.64 21.46 9.61 

Seeds 1.33 0.76 0.34 

a

 upper bound Kenaga values 

b

 Minimum and maximum EECs are in BOLD. 

Table 4-3. Mammalian Dose-Based (mg/kg-bw) Estimated Exposure Concentrations 

(EECs)a

Use Feeding Category 

Dose-Based EECs (mg/kg-bw)b

Small 

(15 g) 

Medium 

(35 g) 

Large 

(1000 g) 

Citrus 

Grapes 

Pome fruits 

Strawberries 

Tree nuts 

Tomatoes 

Ornamentals

Short grass 80.45 55.60 12.89 

Tall grass 36.87 25.48 5.91 

Broadleaf plants 45.25 31.27 7.25 

Fruits/pods 5.03 3.47 0.81 

Arthropods 31.51 21.78 5.05 

Seeds 1.12 0.77 0.18 

a

 upper bound Kenaga values 

b

 Minimum and maximum EECs are in BOLD. 

Table 4-4. Avian and Mammalian Dietary-Based (mg/kg-diet) Estimated Exposure 

Concentrations (EECs)a

Use Feeding Category Dietary-Based EECsb

(mg/kg-diet) 

Citrus 

Grapes 

Pome fruits 

Strawberries 

Tree nuts 

Tomatoes 

Ornamentals

Short grass 84.38 

Tall grass 38.67 

Broadleaf plants 47.46 

Fruits/pods/seeds 5.27 

Arthropods 33.05 

a

 upper bound Kenaga values 

b

 Minimum and maximum EECs are in BOLD. 

4.1.2 Terrestrial (Upland and Semi-Aquatic) Plants 
32 

Input parameters for TerrPlant10 (Table 4-5) include a maximum application rate, incorporation 

depth (1 inch; default), water solubility (0.0281 mg/L) to inform the run-off fraction (1%), spray 

drift fraction (1% for ground application; 5% for aerial application), and definitive toxicity 

endpoints from seedling emergence (SE) and vegetative vigor (VV) studies. 

EECs used to evaluate potential risk to terrestrial plants are provided in Table 4-6. 

Table 4-5. Input Parameters for TerrPlant Modeling Scenarios 

Use 

(Application Method) 

Maximum Single 

Application Rate 

(lb a.i./A) 

Spray Drift 

Fractiona 

(%) 

Other Parameters 

Citrus 

Grapes 

Pome fruits 

Strawberries 

Tree nuts 

Tomatoes 

Ornamentals 

(Ground) 

0.2 1 

Incorporation depth = ≤ 1 inch 

Runoff fraction = 1% 

SE endpoints (MRID 48542933)b

Dicot (Tomato) 

EC25 = 0.0393 lb a.i./A 

NOAEC = 0.000706 lb a.i./A 

VV endpoints (MRID 48542932)c

Monocot & Dicot 

NOAEC = 0.273 lb a.i./A 

Tomatoes 

(aerial) 0.2 5 

SE = seedling emergence; VV = vegetative vigor 

a

 1% for ground application; 5% for aerial application 

b

 monocot SE endpoints are not available (i.e., definitive) or could not be determined c monocot and dicot VV EC25 endpoints are non-definitive (i.e., >) 

Table 4-6. Terrestrial (Upland and Semi-aquatic) Plant Estimated Exposure 

Concentrations (EECs) 

Use 

(Application 

Method) 

Runoff EEC 

(lb a.i./A) 

Spray Drift EEC 

(lb a.i./A) 

Total Loading EEC 

(Runoff + Spray Drift) 

(lb a.i./A) 

Dry (Upland) 

Areas 

Semi-Aquatic 

Areas 

All Areas Dry (Upland) 

Areas 

Semi-Aquatic 

Areas 

Citrus 

Grapes 

Pome fruits 

Strawberries 

Tree nuts 

Tomatoes 

Ornamentals 

(ground)

0.002 0.02 0.002 0.004 0.022 

Tomatoes 

(aerial) 0.002 0.02 0.01 0.012 0.03 

4.2 Aquatic Exposure 

 

10 http://www.epa.gov/oppefed1/models/terrestrial/index.htm#terrplant
33 

The environmental fate properties used for modeling parent only and the total toxic residues 

(TTR) for cyflumetofen are summarized in Table 4-7 and Table 4-8. 

Table 4-7. PRZM/EXAMS Input Parameter Values for Parent Only Modeling 

Parameter (Units) Input Value and Unit Source/Comments 

Maximum Application Rate See Table 4-10 Labels 

Minimum Reapplication Interval See Table 4-10 Labels 

Modeling Scenarios See Table 4-10 Professional Judgment 

Initial Application Dates (dd-mm) See Table 4-10 Professional Judgment 

Application Method Cam = 2 Foliar spray 

Application Efficiency Fraction Aerial – 0.95 or ground – 0.99 Default

Spray Drift Loading Fraction Aerial – 0.305 

Ground – 0.027 

AgDRIFT – 15mph, boom height = 15ft 

(aerial) / 2 ft (ground), droplet size = fine

Incorporation depth (cm) 0 Default 

Molecular Weight (g/mole) 447.45 MRID 48542621 

Water Solubility (mg/L) 0.028 MRID 48542621 

Vapor Pressure (torr) 4.43 × 10-8 MRID 48542611 

KOC (L/kgoc) 72,000 Professional Judgment – a Koc value was 

chosen to represent a low-end value for 

the parent and be consistent with the 

degradates of concern that are considered 

likely to be more persistent. 

Hydrolysis t1⁄2 (days) 0.406 TTR – MRID 48542625 

Aqueous Photolysis t1⁄2 (days) 0.0511 TTR – MRID 48542627 

Aerobic Soil Metabolism t1⁄2 (days) 27.512 TTR – MRIDs 48542745, 48542748, and 

48542752 

Aerobic Aquatic Metabolism t1⁄2 (days) 38.893 TTR – MRIDs 48542769, 48542770, and 

48542771 

Anaerobic Aquatic Metabolism t1⁄2

(days) 

6.594 TTR – MRID 48542769 

1

 Input Parameter Guidance Manual, Pesticides (Version 2.1; Oct. 22, 2009) 2

 Aerobic soil metabolism TTR half-lives of 2.24, 4.98, 2.27, 2.36, 3.4, 4.37, 13.3, and 2.53 days. 

3

 Aerobic aquatic metabolism TTR half-lives of 21.4, 18.3, 11.3, and 0.297 days. 

4

 Anaerobic aquatic metabolism TTR half-lives of 21.5 and 4.76 days. 

Table 4-8. PRZM/EXAMS Input Parameter Values for Total Toxic Residues Modeling 

Parameter (Units) Input Value and Unit Source/Comments 

Maximum Application Rate See Table 4-10 Labels 

Minimum Reapplication Interval See Table 4-10 Labels 

Modeling Scenarios See Table 4-10 Professional Judgment 

Initial Application Dates (dd-mm) See Table 4-10 Professional Judgment 

Application Method Cam = 2 Foliar spray 

Application Efficiency Fraction Aerial – 0.95 or ground – 0.99 Default

Spray Drift Loading Fraction Aerial – 0.305 

Ground – 0.027 

AgDRIFT – 15mph, boom height = 15ft 

(aerial) / 2 ft (ground), droplet size = fine

Incorporation depth (cm) 0 Default 

Molecular Weight (g/mole) 447.45 MRID 48542621 

Water Solubility (mg/L) 0.028 MRID 48542621 

Vapor Pressure (torr) 4.43 × 10-8 MRID 48542611 

KOC (L/kgoc) 72,000 Professional Judgment – a Koc value was 

chosen to represent a low-end value for 
34 

Parameter (Units) Input Value and Unit Source/Comments 

the degradates of concern that are 

considered likely to be more persistent. 

Hydrolysis t1⁄2 (days) Stable TTR – MRID 48542625 

Aqueous Photolysis t1⁄2 (days) 17.6 TTR – MRID 48542627 

Aerobic Soil Metabolism t1⁄2 (days) 10962 TTR – MRIDs 48542745 and 48542748 

Aerobic Aquatic Metabolism t1⁄2 (days) 1733 TTR – MRIDs 48542769, 48542770, and 

48542771 

Anaerobic Aquatic Metabolism t1⁄2

(days) 

60,0004 TTR – MRID 48542769 

1

 Input Parameter Guidance Manual, Pesticides (Version 2.1; Oct. 22, 2009) 2

 Aerobic soil metabolism TTR half-lives of 61.4 and 846 days. 

3

 Aerobic aquatic metabolism TTR half-lives of 149, 99.2, 16.4, and 40.3 days. 

4

 Anaerobic aquatic metabolism TTR half-lives of 31,300 and 3780 days. 

The label-required spray application conditions (release height greater than 15 feet above crop 

canopy and droplet size category of fine) are likely to transport cyflumetofen through spray drift 

in excess of EFED’s default spray drift assumptions. Additionally, the label specifies 15 mph as 

the maximum wind speed during application. Non-default AgDRIFT modeling inputs are 

summarized in Table 4-9. AgDRIFT output is provided in Appendix E. 

Table 4-9. Summary of Non-Default AgDRIFT Modeling Inputs 

Parameter Aerial Application Ground Application 

Droplet Size Fine (DV05 = 179.6 μm) ASAE Very fine to fine (DV05 = 175 μm) 

Boom Height 15 ft. above ground 24” on label (20” modeled) 

Data Percentile NA 90th percentile 

Wind Speed 15 mph NA 

Spray Volume NA 

NA = Not Applicable 

The aquatic parent only and TTR EECs for the various scenarios and application practices are 

listed in Table 4-10. (See Appendix E for representative output from PRZM/EXAMS.) Surface 

water Parent only EECs for the proposed uses of cyflumetofen ranged from 0.26 to 3.2 μg/L for 

peak EECs, 0.016 to 0.20 μg/L for 1-in-10 year 21-day average EECs, and 0.006 to 0.078 μg/L 

for 1-in-10 year 60-day average EECs. Surface water TTR EECs for the proposed uses of 

cyflumetofen ranged from 0.48 to 7.8 μg/L for peak EECs, 0.25 to 5.1 μg/L for 1-in-10 year 21-

day average EECs, and 0.23 to 4.9 μg/L for 1-in-10 year 60-day average EECs. 

Pore water TTR EECs change slowly over time, displaying little inter-annual variation and 

ranging from 0.14 to 3.0 μg/L for peak EECs, 1-in-10 year 21-day average EECs, and 1-in-10 

year 60-day average EECs across all scenarios (Table 4-10). Over multi-year time scales 

though, both surface water (Figure 4-1c) and pore water (Figure 4-1d) TTR EECs increase with 

time. (Notice that because inter-annual variation is small for pore water TTR EECs in Figure 4-

1d, the peak, 21-day, and 60-day plot on top of each other for the same year.) 
35 

Figure 4-1. Temporal variation in cyflumetofen parent only surface (a) and benthic pore 

(b) water and total toxic residue (TTR) surface (c) and benthic pore (d) water estimated 

environmental concentrations (EECs). 

0

0.5

1

1.5

2

2.5

3

3.5

4

1950 1960 1970 1980 1990 2000

Parent Concentration (μg/L)

Time

Peak

21 Day

60 Day

a

0

0.005

0.01

0.015

0.02

0.025

0.03

0.035

0.04

0.045

0.05

1950 1960 1970 1980 1990 2000

Parent Concentration (μg/L)

Time

Peak

21 Day

60 Day

b

0

1

2

3

4

5

6

7

8

9

10

1950 1960 1970 1980 1990 2000

TTR Concentration (μg/L)

Time

Peak

21 Day

60 Day

c

0

0.5

1

1.5

2

2.5

3

3.5

1950 1960 1970 1980 1990 2000

TTR Concentration (μg/L)

Time

Peak

21 Day

60 Day

d
36 

1 Table 4-9. Parent Only and Total Toxic Residue (TTR) Estimated Environmental Concentrations (EECs) in Surface and Benth2 Cyflumetofen

Use/ 

Scenario 

Aerial (A) or 

Ground (G) / 

Initial App. 

Dates (d-m) 

Max. 

Single 

App. Rate 

(lb a.i./A) 

Max. 

Number 

of App.

Max. App. 

Rate Per Crop 

Cycle/Season 

(lb a.i./A) 

Min. 

App. 

Interval 

(Days)

Parent Only EECs (μg/L) Total Toxic R

Surface Water 

Benthic 

Pore Water Surface W

Peak 21-day 60-day 21-day Peak 21-day 

Citrus 

CA G / 1-1 0.2 2/CC 0.4 14 0.258 0.016 0.006 0.002 0.478 0.253 FL G / 1-1 0.2 2/CC 0.4 14 0.272 0.019 0.007 0.003 2.583 1.859 

Grapes 

CA Grapes G / 1-1 0.2 2/CC 0.4 14 0.258 0.017 0.007 0.002 0.553 0.328 CA Wine Grapes G / 1-1 0.2 2/CC 0.4 14 0.445 0.037 0.016 0.010 2.458 1.503 NY Grapes G / 1-6 0.2 2/CC 0.4 14 0.869 0.053 0.023 0.015 5.271 3.404 

Pome Fruit

NC G / 1-6 0.2 2/CC 0.4 14 0.447 0.035 0.015 0.008 2.801 1.595 OR G / 1-6 0.2 2/CC 0.4 14 0.258 0.016 0.006 0.002 1.322 1.064 PA G / 1-6 0.2 2/CC 0.4 14 0.508 0.025 0.011 0.006 2.920 1.927 

Strawberry CA G / 1-1 0.2 2/CC 0.4 14 0.262 0.018 0.007 0.002 0.897 0.629 FL G / 1-1 0.2 2/CC 0.4 14 0.259 0.016 0.006 0.002 2.495 1.897 Tree Nuts 

CA Almond G / 1-1 0.2 2/CC 0.4 14 0.260 0.018 0.007 0.002 0.772 0.523 OR Filberts G / 1-6 0.2 2/CC 0.4 14 0.258 0.016 0.006 0.002 1.289 1.035 GA Pecans G / 1-6 0.2 2/CC 0.4 14 0.886 0.041 0.017 0.011 3.488 2.126 

Tomatoes 

CA A / 1-6 0.2 2/CC 0.4 14 2.914 0.176 0.065 0.015 5.012 2.501 

G / 1-6 0.2 2/CC 0.4 14 0.258 0.016 0.006 0.001 0.575 0.352 

FL A / 1-6 0.2 2/CC 0.4 14 2.980 0.185 0.069 0.016 6.058 3.566 

G / 1-6 0.2 2/CC 0.4 14 0.329 0.025 0.010 0.004 2.439 1.699 

PA A / 1-6 0.2 2/CC 0.4 14 3.216 0.202 0.078 0.025 7.833 5.108 

G / 1-6 0.2 2/CC 0.4 14 0.961 0.042 0.019 0.012 3.947 2.974 

Nursery/Ornamental 

CA G / 1-1 0.2 2/yr 0.4 14 0.413 0.032 0.014 0.008 3.115 1.510 FL G / 1-1 0.2 2/yr 0.4 14 0.259 0.016 0.006 0.002 2.262 1.594 MI G / 1-4 0.2 2/yr 0.4 14 0.264 0.018 0.007 0.002 2.572 1.903 NJ G / 1-4 0.2 2/yr 0.4 14 0.279 0.022 0.009 0.004 2.624 1.732 OR G / 1-4 0.2 2/yr 0.4 14 0.258 0.016 0.006 0.002 0.807 0.589 TN G / 1-4 0.2 2/yr 0.4 14 0.259 0.019 0.008 0.003 2.311 1.739 
37 

1 Although the TTR EECs are increasing over time, it is important to note that in reality the 

2 accumulating mass of TTRs is changing in chemical composition over time (see the complex 

3 degradation pathways in Appendix Figures C-1 to C-5). The TTR EECs include all of the 

4 degradates that retain the cyano group expressed as the equivalent concentration of parent if all 

5 of those degradates were transformed back into the parent. 

6 

7 Typically, the degradation process proceeds from more complex (higher molecular weight) and 

less water soluble chemicals to simpler and more water soluble chemicals. 14 8 Carbon dioxide was 

9 produced in quantities greater than 5% of applied radioactivity in the A-labeled studies of the 

10 aerobic soil and aerobic aquatic metabolism studies (Appendix Table C-1). (The simpler 

11 chemicals that retain the cyano-group occur in the A-label studies.) Additionally, A-12 (which 

12 does not have a cyano-group but degrades from intermediate degradates that do possess a cyano13 group) was detected in anaerobic soil and anaerobic aquatic metabolism studies. Therefore over 

14 time, it might be expected that the accumulated TTR mass represents mostly degradates slowly 

15 undergoing complete mineralization in aerobic environments or converting to degradates that are 

16 not of concern (e.g., A-12) in anaerobic environments. This is probably a good assumption for 

17 the fraction of cyflumetofen that degrades through the pathway involving an initial break of the 

18 bond denoted #1 in Figure 3-1, since this break results in the production of mostly simple 

19 molecules. However, the pathway involving an initial break of the bond #2 in Figure 3-1 results 

20 in the “AB” chemicals, which appear to be much more persistent. 

21 

22 Finally, the fate data also show the formation of dimers, which are complex (higher molecular 

23 weight) chemicals with very low water solubilities in the hydrolysis, aerobic and anaerobic soil 

24 metabolism, aerobic aquatic metabolism, and terrestrial field dissipation studies (Appendix 

25 Table C-1). If these dimers are actually forming in the environment (not a laboratory artifact), it 

26 is difficult to predict their environmental fate from the registrant-submitted fate data. Often 

27 these dimers were at their highest concentrations at, or near, the end of the fate studies 

28 (Appendix Table C-1). Additionally, the aerobic and anaerobic soil metabolism and aerobic 

29 and anaerobic aquatic metabolism studies had high proportions of the total applied radioactivity 

30 as unextractable, and therefore unidentified, residues. 

31 4.2.1 Aquatic Bioaccumulation 

32 

33 The KABAM model (v. 1.0) was used to model a single high-end scenario based on the highest 

34 TTR EECs that result from any of the assessed uses of cyflumetofen (aerial application to 

35 Pennsylvania tomatoes). This scenario was chosen to represent the highest potential for 

36 bioaccumulation from the currently proposed cyflumetofen uses (Table 4-11). 

37 

38 Table 4-11. Bioaccumulation Model Input Values for Cyflumetofen 

Parameter Input Value Source 

Pesticide Name Cyflumetofen 

Log KOW 4.3 MRID 48542623 

KOC 72,000 

Professional Judgment – a Koc value was chosen to 

represent a low-end value for the degradates of concern 

that are considered likely to be more persistent. 

Concentration in sediment pore water (ppb) 2.9998 highest TTR EECs: aerial application to Pennsylvania 

Concentration in water column(ppb) 5.1084 tomatoes 

39 
38 

5 Effects Characterization 

Data from registrant-submitted studies used to characterize the effects of parent cyflumetofen 

and degradates to non-target organisms are described in this section. 

No cyflumetofen studies from the open literature were identified using the public version of 

ECOTOX11. 

5.1 Effects to Terrestrial Organisms 

Summaries of data used to characterize the effects of parent cyflumetofen and degradates to 

terrestrial organisms are provided in Tables 5-1 (parent) and 5-2 (degradates). The most 

sensitive definitive toxicity endpoints used in RQ calculations are bolded. 

5.1.1 Birds 

Based on studies with mallard duck, bobwhite quail, and zebra finch, cyflumetofen is practically 

non-toxic to birds on an acute oral basis. No mortality or sublethal effects were noted in the 

acute oral studies with zebra finch and mallard duck (MRIDs 48542774 and 48542773, 

respectively). There was no mortality in the study with bobwhite quail (MRID 48542772). 

However, hunched posture was observed in males from the 222 mg a.i./kg-bw treatment group 

and in males and females from the 667 and 2000 mg a.i./kg-bw treatment groups resulting in a 

NOAEL of 74 mg a.i./kg-bw based on clinical signs of toxicity. With the exception of one 

female from the 2000 mg/kg-bw treatment group showing abnormal posture of the head from 

Day 4 onwards, all animals recovered between days 1 and 3. 

 

Based on studies with mallard duck and bobwhite quail, cyflumetofen is practically non-toxic to 

birds on a sub-acute dietary basis. No mortality or sublethal effects were noted in the acute oral 

study with mallard duck (MRIDs 48542776). In the study with bobwhite quail (MRID 

485427775), there was 10% mortality (1 out of 10) in the second highest treatment group (i.e., 

2333 mg a.i./kg-diet). This death was considered incidental since no mortality occurred in the 

highest treatment group (i.e., 5033 mg a.i./kg-diet). In addition, reduced weight gain was 

observed in the 2333 and 5033 mg a.i./kg-diet treatment groups resulting in a NOAEC of 1133 

mg a.i./kg-diet based on sublethal effects. 

In the reproduction study with mallard duck (MRID 48542778), one mortality was reported with 

the cause of death unknown. A statistically-significant decrease in eggshell thickness was 

detected in the lowest treatment group (i.e., 160 mg a.i./kg-diet) but not the intermediate and 

highest treatment groups. Since the reduction in eggshell thickness was not concentrationdependent, and there were no treatment-related effects detected for any adult, offspring, or other 

reproductive parameter at any treatment level, the NOAEC for this study was set at the highest 

treatment level (i.e., 930 mg a.i./kg-diet). 

 

11 Quick Database Query conducted on CAS number 400882-07-7 at http://cfpub.epa.gov/ecotox/ 
39 

Table 5-1. Endpoints Used to Characterize the Effects of Cyflumetofen to Terrestrial Organisms Assessment Endpoint 

Measurement Endpoint 

TGAI / Form. (%) 

Species Toxicity Values1,2 (Effects) & Acute Toxicity Classif

(if applicable) 

Survival, growth, and reproduction of birds (surrogate for reptiles and terrestrial-phase amphibians) 

Most sensitive avian acute oral LD50

TGAI (98.4) 

Bobwhite quail (Colinus virginianus) 

14-day LD50 > 2000 mg a.i./kg-bw (nom) 

14-day NOAEL = 74 mg a.i./kg-bw (nom) (no mortality; NOAEL based on clinical signs of toxiciincluding hunched posture) Practically non-toxic 

TGAI (98.4) 

Zebra finch (Taeniopygia guttata) 

14-day LD50 > 2000 mg a.i./kg-bw (nom) 

14-day NOAEL = 2000 mg a.i./kg-bw (nom) (no mortality or sublethal effects) Practically non-toxic 

TGAI (98.0) 

Mallard duck (Anas platyrhynchos) 

14-day LD50 > 2250 mg a.i./kg-bw (nom) 

14-day NOAEL = 2250 mg a.i./kg-bw (nom) (no mortality or sublethal effects) Practically non-toxic 

Most sensitive avian sub-acute dietary LC50

TGAI (98.0) 

Bobwhite quail (Colinus virginianus) 

8-day LC50 > 5033 mg a.i./kg-bw (m) 

8-day NOAEC = 1133 mg a.i./kg-bw (m) (10% [1 out of 10] mortality at 2333 mg a.i./kg-diet; Nbased on reduced body weight gain) Practically non-toxic 

TGAI (98.4) 

Mallard duck (Anas platyrhynchos) 

8-day LC50 > 5760 mg a.i./kg-bw (m) 

8-day NOAEC = 5760 mg a.i./kg-bw (m) (no mortality or sublethal effects) Practically non-toxic 

Most sensitive avian chronic NOAEC 

TGAI (98.4) 

Bobwhite quail (Colinus virginianus) 

22-week NOAEC = 154 mg a.i./kg-diet (m) 

22-week LOAEC = 389 mg a.i./kg-diet (m) (NOAEC based on eggs cracked per pen and eggs not cracked/eggs laid) 

TGAI (98.4) 

Mallard duck (Anas platyrhynchos) 

22-week NOAEC = 930 mg a.i./kg-diet (m) 22-week LOAEC > 930 mg a.i./kg-diet (m) (no effects) 

Survival, growth, and reproduction of mammals 

Most sensitive mammalian acute LD50

TGAI (98.0) 

Han Wistar rat (Rattus norvegicus) 

14-day (females) LD50 ≥ 2000 mg/kg-bw 

(no mortality; 1 out of 5 females with loose feces on studay 1 only) Practically non-toxic 

Most sensitive mammalian chronic NOAEC 

TGAI (97.67) 

Wistar Hannover (Rattus norvegicus) 

Two-generation reproduction Parental

NOAEL = 150 mg/kg-diet (9.21/13.8 mg/kg-bw/day in males/females) 
40 

Assessment Endpoint 

Measurement Endpoint 

TGAI / Form. (%) 

Species Toxicity Values1,2 (Effects) & Acute Toxicity Classif

(if applicable) LOAEL = 500 mg/kg-diet (30.6/46.6 mg/kg-bw/day in males/females) (based on effects to adrenals: increased organ weights ahistopathology) Reproductive

Male NOAEL ≥ 1500 mg/kg-diet (89.4 mg/kg-bw/day) Female NOAEL = 500 mg/kg-diet (46.6 mg/kg-bw/dayFemale LOAEL = 1500 mg/kg-diet (141.1 mg/kg-bw-d(based on hormone changes and increased estrous cycle length) Offspring

NOAEL = 150 mg/kg-diet (9.21/13.8 mg/kg-bw/day in males/females) LOAEL = 500 mg/kg-diet (30.6/46.6 mg/kg-bw/day in males/females) (based on effects to adrenals: increased organ weights ahistopathology) 

Survival, growth, and reproduction of terrestrial invertebrates 

Most sensitive terrestrial invertebrate (honeybee) acute LD50

TGAI (98.0) 

Honey bee (Apis mellifera) 

Acute contact 96-hr LD50 > 100 μg a.i./bee (nom) 

96-hr NOAEL = 20.7 μg a.i./bee (nom) (NOAEL based on statistically-significant mortality; 1020, and 13% in the 4.3, 9.4, 20.7, 45.5, and 100 μg a.i./treatment groups) Practically non-toxic 

Form. (20.4) 

Honey bee (Apis mellifera) 

Acute contact 48-hr LD50 > 100 μg a.i./bee (nom) 

48-hr NOAEL = 4.6 μg a.i./bee (nom) (no statistically-significant mortality; NOAEL based on lethargy) Practically non-toxic 

Form. (20.3) 

Honey bee (Apis mellifera) 

Acute oral 96-hr LD50 > 116 μg a.i./bee (nom) 

96-hr NOAEL = 116 μg a.i./bee (nom) (no statistically-significant mortality) Practically non-toxic 

Form. (20.3) 

Parasitic wasp (Aphidius rhopalosiphi) 

Limit test 48-hr LR50 > 1.2 lb a.i./A (nom) 

48-hr NOAEC = 1.2 lb a.i./A (nom) 
41 

Assessment Endpoint 

Measurement Endpoint 

TGAI / Form. (%) 

Species Toxicity Values1,2 (Effects) & Acute Toxicity Classif

(if applicable) (no mortality or sublethal effects) 

Form. (20.3) 

Predatory mite (Typhlodromus pyri) 

Limit test 7-day LR50 > 1.2 lb a.i./A (nom) 

7-day NOAEC = 1.2 lb a.i./A (nom) (5 and 11% mortality in the control and 1.2 lb a.i./A tregroup, respectively; no sublethal effects) 

TGAI (98.0) 

Earthworm (Eisenia fetida fetida) 

14-day LC50 > 1000 mg a.i./kg-dw (soil; nom) 

14-day NOAEC = 100 mg a.i./kg-dw (soil; nom) (no mortality; NOAEC based on reduced weight gain) 

Form. (20.4) 

Earthworm (Eisenia fetida fetida) 

14-day LC50 > 1050 mg a.i./kg-dw (soil; nom) 

14-day NOAEC = 106 mg a.i./kg-dw (soil; nom) (10% mortality at 1.1 mg a.i./kg-dw; NOAEC based on reduced weight gain) 

TGAI (98.4) 

Earthworm (Eisenia fetida fetida) 

28- & 56-day NOAEC = 1000 mg a.i./kg-dw (soil; nom28- & 56-day LOAEC > 1000 mg a.i./kg-dw (soil; nom(based on mortality, growth, and reproduction) 

Survival, growth and reproduction of terrestrial plants 

Seedling emergence: Most sensitive monocot EC25 and 

NOAEC 

Form. (19.64) 

Oat (Avena sativa) 

21/22-day EC25: Could not be determined 

21/22-day EC05: Could not be determined 21/22-day NOAEC < 0.000706 lb a.i./A (m) (based on dry weight & shoot length) 

Seedling emergence: Most sensitive dicot EC25 and NOAEC 

Tomato (Lycopersicon esculentum) 

21-day EC25 (95% C.I.) = 0.0393 (0.0174-0.0889) lb a.

21-day NOAEC = 0.000706 lb a.i./A (m) (based on dry weight) 

Vegetative vigor: Most sensitive monocot EC25 and 

NOAEC 

Form. (19.64) 

Could not be determined 

21-day EC25 > 0.250/0.268/0.273 lb a.i./A (m) 

21-day NOAEC = 0.250/0.268/0.273 lb a.i./A (m) (endpoint depends on species tested) 

Vegetative vigor: Most sensitive dicot EC25 and NOAEC 

Could not be determined 

21-day EC25 > 0.250/0.268/0.273 lb a.i./A (m) 

21-day NOAEC = 0.250/0.268/0.273 lb a.i./A (m) (endpoint depends on species tested) 

Form = formulation; NS = not specified; TGAI = technical grade active ingredient 1 BOLD values used in RQ calculations 2 m = measured; mm = mean-measured; nom = nominal 
42 

Table 5-2. Endpoints Used to Characterize the Effects of Degradates of Cyflumetofen to Terrestrial Organ

Assessment Endpoint 

Degradate (%) 

Species Toxicity Values1 (Effects) Source & 

Classification 

Survival, growth, and reproduction of terrestrial invertebrates (earthworms) 

AB-1 (99.8) 

Earthworm (Eisenia fetida fetida) 

14-day LC50 > 1000 mg/kg-dw (soil; nom) 

14-day NOAEC = 100 mg/kg-dw (soil; nom) (2.5, 0, 0, 2.5, 12.5, and 20% mortality in the control, 100, 180, 320, 560, and 1000 mg a.i./kg-dw treatment groups; NOAEC based on reduced weight gain) 

MRID 48542Acceptable (non-guidelin

B-1 (99.1) 

Earthworm (Eisenia fetida fetida) 

14-day LC50 > 1000 mg/kg-dw (soil; nom) 

14-day NOAEC = 1000 mg/kg-dw (soil; nom) (no mortality; NOAEC based on mortality and weight gain) 

MRID 48542Acceptable (non-guidelin

1 nom = nominal
43 

In the reproduction study with bobwhite quail (MRID 48542777), eight incidental mortalities 

were reported; the mortalities were mostly attributed to head and/or neck lesions. In addition, 

there was a statistically-significant increase in eggs cracked per pen and a statistically-significant 

decrease in eggs not cracked per eggs laid resulting in a NOAEC of 154 mg a.i./kg-diet. 

5.1.2 Mammals 

Based on a study with female rats, cyflumetofen is practically non-toxic to mammals on an acute 

oral basis. In this limit study (MRID 48542669), no mortality, treatment-related necropsy 

findings, or changes in weight were reported; however, one out of the 5 tested females exhibited 

loose feces on study day 1 only. 

In the 2-generation study with rats (MRID 48542702), adrenal weights were increased in P and 

F1 parental females at ≥ 500 mg/kg-diet. In parental males at 1500 mg/kg-diet, adrenal weights 

were increased in the P and F1 generations. In addition, ovary weights were increased in P 

generation females at 1500 mg/kg-diet only. Histopathological examination of the adrenals 

revealed an increased incidence of hypertrophy of the zona glomerulosa at ≥ 500 mg/kg-diet in P 

generation females and F1 generation males and females and in P males at 1500 mg/kg-diet. 

Additionally in the adrenals, an increased incidence of vacuolation of the zona fasciculata cells 

was observed at 1500 mg/kg-diet in P generation females and in both sexes of the F1 generation. 

An increased incidence of vacuolation of the interstitial cells of the ovary was also noted at 1500 

mg/kg-diet in F1 females. These findings resulted in a parental NOAEL of 150 mg/kg-diet 

(9.21/13.8 mg/kg-bw/day in males/females) based on effects on the adrenals (increased organ 

weights and histopathology). 

An increase in estrous cycle length was noted at 1500 mg/kg-diet. In addition, decreased FSH 

levels were noted at 500 mg/kg-diet and above and decreased progesterone was noted at 150 

mg/kg-diet and above in F1 females. As for the decreases in progesterone at 150 and 500 ppm, 

and in FSH at 500 mg/kg-diet in females, there were no corresponding changes in estrous cycle 

length or reproductive performance after sexual maturation at these dose levels. In females at 

1500 mg/kg-diet, increased estrous cycle length was accompanied by decreases in FSH, 

progesterone and 17β-estradiol. These findings resulted in a reproductive NOAEL in females of 

500 mg/kg-diet (46.6 mg/kg-bw/day) based on hormone changes and increased estrous cycle 

length; the reproductive NOAEL in males is ≥1500 mg/kg-diet (89.4 mg/kg-bw/day). 

Adrenal weights were increased at 500 mg/kg-diet and above in both sexes of both generations 

of offspring. Microscopic examination of the adrenals revealed an increased incidence of 

hypertrophy of the zona glomerulosa cells in both generations of males at ≥ 500 mg/kg-diet and 

in both generations of females at 1500 mg/kg-diet. Additionally in the adrenals, an increased 

incidence of hypertrophy of the zona fasciculata cells was noted at ≥ 500 mg/kg-diet in F1 males 

and females and F2 males and at 1500 mg/kg-diet in F2 females. Delayed sexual maturation was 

observed in females (increased time to vaginal opening) at ≥ 500 mg/kg-diet, and in males 

(increased time to preputial separation) at 1500 mg/kg-diet. These findings resulted in an 

offspring NOAEL is 150 mg/kg-diet (9.21/13.8 mg/kg-bw/day in males/females) based on 

effects on the adrenals (increased organ weights and histopathology) in both sexes and a delay in 

sexual maturation of females. 
44 

5.1.3 Terrestrial Invertebrates 

Based on two honey bee contact toxicity studies, one with technical grade active ingredient 

(TGAI; MRID 48542805) and one with a 20.4% formulation (MRID 48542914), and a honey 

bee acute oral toxicity study with a 20.4% formulation, cyflumetofen is practically non-toxic to 

terrestrial invertebrates. In the acute contact toxicity study with technical grade cyflumetofen, 

mortality after 96 hours in the 4.3, 9.4, 20.7, 45.5, and 100 μg a.i./bee treatment groups was 10, 

0, 7, 20, and 13%, respectively, resulting in a NOAEC of 20.7 μg a.i./bee based on statisticallysignificant mortality in the 45.5 μg a.i./bee treatment group. In the acute contact and oral 

toxicity studies with a 20.4% formulation of cyflumetofen, there was no statistically-significant 

mortality after 48 and 96 hours, respectively. However, observed lethargy in the acute contact 

study with a formulation resulted in a NOAEL of 4.6 μg a.i./bee based on sublethal effects. 

Toxicity data from non-guideline studies are also available for arthropods and earthworms 

(Tables 5-1 and 5-2). Acute limit tests with two beneficial terrestrial arthropods – the parasitic 

wasp (Aphidius rhopalosiphi) and the predatory mite (Typhlodromus pyri) – using a 20.3% 

formulation of cyflumetofen both yielded a LR50 of >1.2 lb a.i./A and a NOAEC and 1.2 lb 

a.i./A. No mortality or sublethal effects were noted in the test with A. rhopalosiphi, and no 

sublethal effects or statistically-significant mortality were noted in the test with T. pyri (MRIDs 

48542924 and 48542725, respectively). 

A series of sub-chronic and/or chronic toxicity tests were conducted with earthworms (Eisenia 

fetida fetida) using technical grade cyflumetofen, a 20.4% formulation of cyflumetofen, and 

degradates AB-1 and B-1 at concentrations up to 1000 mg/kg-dw soil. For the sub-chronic, 14-

day toxicity studies, NOAECs of 100-106 mg/kg-dw soil for technical grade and formulated 

cyflumetofen and degradate AB-1 were based on reduced weight gain (MRIDs 48542824, 

48542916, 48542806) whereas the NOAEC for degradate B-1 was set at the highest treatment 

level (1000 mg/kg-dw soil; MRID 48542807). For the chronic, 56-day toxicity study, the 

NOAEC was set at the highest treatment level (1000 mg/kg-dw soil; MRID 48542808). 

5.1.4 Terrestrial (Upland and Semi-Aquatic) Plants 

In the vegetative vigor study (MRID 48542932), the most sensitive monocot and dicot species 

could not be determined because the NOAEC was the highest treatment level (i.e., 

0.250/0.268/0.273 lb a.i./A) for all tested species. 

Species-specific endpoints for the seedling emergence study (MRID 48542933) are provided in 

Table 5-3. The most sensitive dicot was tomato, and the most sensitive monocot was oat. For 

oat, an EC25 could not be determined because the concentration-response relationship for dry 

wieght and shoot length was atypical leading to issues with model convergence (See Figure 5-

1). In addition, oat dry weight and shoot length of the lowest treatment group (i.e., 0.000706 lb 

a.i./A) were significantly reduced (i.e., 33.2 and 27.3%, respectively) when compared to the 

control group resulting in the lack of a NOAEC for monocots and a Supplemental classification 

for the study. 
45 

Table 5-3. Species-Specific Endpoints for Seedling Emergence 

Species Most Sensitive 

Endpoint 

NOAEC/LOAEC 

(lb a.i./A) 

% reductiona at 

NOAEC/LOAEC 

EC25 

(lb a.i./A) 

Monocots 

Oat(Avena sativa) Dry weight 

Shoot length 

<0.000706/0.000706 

<0.000706/0.000706 

--/33.2 

--/27.3 

CBDa

Onion (Allium sepa) Survival 0.0235/0.045 13.9/15.6 >0.267 

Corn (Zea mays) None 0.260/>0.260 NA >0.260 

Ryegrass (Lolium perenne) None 0.260/>0.260 NA >0.260 

Dicots 

Tomato (Lycopersicon esculentum) Dry weight 0.000706/0.00145 2.1/29.3 0.0393 

Cucumber (Cucumis sativa) Dry weight 0.0222/0.0413 14.3/15.5 >0.260 

Sugarbeet (Beta vulgaris) Emergence 0.139/0.260 7.7/10.3 >0.260 

Radish (Raphanus sativus) None 0.260/>0.260 NA >0.260 

Lettuce (Lactuca sativa) None 0.260/>0.260 NA >0.260 

Soybean (Glycine max) None 0.260/>0.260 NA >0.260 

CBD = could not be determined; NA = not applicable 

a

 if NOAEC < highest treatment concentration 

b

 While statistically-significant reductions were detected, there were issues with model convergence. Therefore, an 

EC25 could not be determined. 

Figure 5-1. Seedling emergence length and weight data for oat graphed in terms of 

exposure concentration (lb a.i./A) using SAS (v. 8.2), Sprouts (v. 1.0) 
46 

5.2 Effects to Aquatic Organisms 

Summaries of data used to characterize the effects of cyflumetofen and degradates to aquatic 

organisms are provided in Tables 5-3 (parent) and 5-4 (degradates). The most sensitive 

definitive toxicity endpoints used in RQ calculations are bolded. 

5.2.1 Parent Cyflumetofen 

5.2.1.1 Fish 

Fish acute and early life stage toxicity studies with technical grade cyflumetofen were conducted 

as limit tests because of the low solubility of cyflumetofen (i.e., 28.1 μg/L at 20°C). Meanmeasured concentrations of 17.5 μg a.i./L for rainbow trout (MRID 48542779), 29.2 and 31.6 

μg a.i./L for fathead minnow (MRIDs 48542780 and 48542783; acute and early life stage tests, 

respectively), and 7.59 μg a.i./L for sheepshead minnow (MRID 48542783) were achieved using 

a saturator column and flow-through exposure. An acute toxicity study with rainbow trout was 

also conducted with a 20.4% formulation of cyflumetofen which resulted in a mean-measured 

concentration of 837 μg a.i./L (MRID 48542920). A non-guideline juvenile growth study with 

carp that achieved mean-measured concentrations of 7.2, 16, 34, 72 and 179 μg a.i./L was 

conducted using a flow through exposure and a solvent consisting of 1:1 mixture of 

dimethylformamide (DMF) and cremophor. 

 

Based on studies with rainbow trout, fathead minnow, and sheepshead minnow, technical grade 

cyflumetofen is practically non-toxic to fish up to the tested solubility limit on an acute basis. 

No mortality or sublethal effects were noted in any of the acute studies (MRIDs 48542779, 

48542780, and 48542783), including the study with a 20.4% formulation of cyflumetofen 

(MRID 48542920). 

In the early life stage study with fathead minnow (MRID 48542783), there were no effects on 

hatching success, survival, or growth (length and dry weight). The study was classified as 

Supplemental because the high:low ratio and percent coefficient of variation for measured test 

concentrations were 2.1 and 27%, respectively, exceeding the 1.5 and 20% maxima for 

acceptable variability in aquatic studies. 

5.2.1.1 Aquatic Invertebrates 

Similar to fish, aquatic invertebrate acute and chronic toxicity studies with technical grade 

cyflumetofen were conducted as limit tests because of the low solubility of cyflumetofen (i.e., 

28.1 μg/L at 20°C). Mean-measured concentrations of 17.2 and 16.2 μg a.i./L for Daphnia 

magna (MRIDs 48542789 and 48542791; acute and chronic tests, respectively), 6.30 μg a.i./L 

for Eastern oyster (MRID 48542810) and 22.7 μg a.i./L for mysid shrimp (MRID 48542811) 

were achieved using a saturator column and flow-through exposure. An acute toxicity study 

with Daphnia magna was also conducted with a 20.4% formulation of cyflumetofen which 

resulted a mean-measured concentration of 744 μg a.i./L (MRID 48542921). 

Based on studies with daphnids, Eastern oyster, and mysid shrimp, technical grade cyflumetofen 

is practically non-toxic to aquatic invertebrates up to the tested solubility limit on an acute basis. 
47 

Table 5-3. Endpoints Used to Characterize the Effects of Cyflumetofen to Aquatic Organisms

Assessment Endpoint Measurement 

Endpoint 

TGAI (%) Species Toxicity Values1,2 (Effects) & Acute 

Toxicity Classification (if applicable) 

Survival, growth, and reproduction of freshwater fish (surrogate for aquaticphase amphibians) 

Most sensitive freshwater fish acute LC50

TGAI (97.08) 

Rainbow trout (Oncorhynchus mykiss) 

Limit test 96-hr LC50 > 17.5 μg a.i./L (mm) 

96-hr NOAEC = 17.5 μg a.i./L (mm) (no mortality or sublethal effects) Practically non-toxic up to solubility lim

TGAI (97.08)

Fathead minnow (Pimephales promelas) 

Limit test 96-hr LC50 > 29.2 μg a.i./L (mm) 

96-hr NOAEC = 29.2 μg a.i./L (mm) (no mortality or sublethal effects) Practically non-toxic up to solubility lim

Form. (20.4) 

Rainbow trout (Oncorhynchus mykiss) 

Limit test 96-hr LC50 > 837 μg a.i./L (mm) 

96-hr NOAEC = 837 μg a.i./L (mm) (no mortality or sublethal effects) 

Most sensitive freshwater fish chronic NOAEC 

TGAI (97.08) 

Fathead minnow (Pimephales promelas) 

Limit test Early life-stage 34-day NOAEC = 31.6 μg a.i./L (TWA) 34-day LOAEC > 31.6 μg a.i./L (TWA) (no effects) 

TGAI (98.4) 

Carp (Cyprinus carpio) 

Juvenile growth 28-day EC50 = 180.65 μg a.i./L (mm) 

28-day NOAEC = 72 μg a.i./L (mm) (based on growth rate) 

Survival, growth, and reproduction of estuarine/marine fish 

Most sensitive estuarine/marine fish acute LC50

TGAI (97.08) 

Sheepshead minnow (Cyprinodon variegatus) 

Limit test 96-hr LC50 > 7.59 μg a.i./L (mm) 

96-hr NOAEC = 7.59 μg a.i./L (mm) (no mortality or sublethal effects) Practically non-toxic up to solubility lim

Survival, growth, and reproduction of freshwater invertebrates 

Most sensitive freshwater invertebrate acute EC50

TGAI (97.08) 

Water flea (Daphnia magna) 

Limit test 48-hr EC50 > 17.2 μg a.i./L (mm) 

48-hr NOAEC = 17.2 μg a.i./L (mm) (no effects) Practically non-toxic up to solubility lim

 Form. 

(20.4) 

Water flea (Daphnia magna) 

Limit test 48-hr EC50 > 744 μg a.i./L (mm) 

48-hr NOAEC = 744 μg a.i./L (mm) (no effects) 
48 

Assessment Endpoint Measurement 

Endpoint 

TGAI (%) Species Toxicity Values1,2 (Effects) & Acute 

Toxicity Classification (if applicable) 

Most sensitive freshwater invertebrate chronic NOAEC 

TGAI (97.08) 

Water flea (Daphnia magna) 

Limit test 21-day NOAEC = 16.2 μg a.i./L (mm) 21-day LOAEC > 16.2 μg a.i./L (mm) (no effects) 

Survival, growth, and reproduction of estuarine/marine invertebrates 

Most sensitive estuarine/marine invertebrate acute EC50

or LC50

TGAI (97.08) 

Eastern oyster (Crassostrea virginica) 

Limit test 96-hr EC50 > 6.30 μg a.i./L (mm) 

96-hr NOAEC = 6.30 μg a.i./L (mm) (no effects) Practically non-toxic up to solubility lim

TGAI (97.08) 

Mysid shrimp (Mysidopsis bahia) 

Limit test 96-hr LC50 > 22.7 μg a.i./L (TWA) 

96-hr NOAEC = 22.7 μg a.i./L (TWA) (no mortality or sublethal effects) Practically non-toxic up to solubility lim

Survival, growth, and reproduction of sediment-dwelling invertebrates 

Most sensitive sediment invertebrate acute LC50

TGAI (97.08 nonradio; 96.0 radio) 

Amphipod (Leptocheirus plumulosus)

Spiked sediment exposure Sediment concentrations

10-day LC50 >787 mg TRR/kg-dw (mm) 

10-day NOAEC = 787 mg TRR/kg-dw (mm) Pore water concentrations

10-day LC50 > 19.7 mg TRR/L 

10-day NOAEC = 19.7 mg TRR/L Overlying water concentrations

10-day LC50 > 5.2 mg TRR/L 

10-day NOAEC = 5.2 mg TRR/L (no statistically-significant mortality) 

Most sensitive sediment invertebrate chronic NOAEC 

TGAI (98.4 nonradio; ≥ 96.4 radio) 

Non-biting midge (Chironomus riparius) 

Spiked water exposure Overlying water concentrations

28-day EC50 > 65.9 μg a.i./L (TWA) 

28-day NOAEC = 65.9 g a.i./L (TWA) 

(no statistically-significant effects on rateof emergence and development) 

TGAI (97.08) 

Non-biting midge (Chironomus riparius) 

Spiked sediment exposure Sediment concentrations

28-day EC50 > 419 mg a.i./kg-dw (mm) 

28-day NOAEC = 26.5 mg a.i./kg-dw (mm) Pore water concentrations

28-day EC50 > 10.4 μg a.i./L (mm) 
49 

Assessment Endpoint Measurement 

Endpoint 

TGAI (%) Species Toxicity Values1,2 (Effects) & Acute 

Toxicity Classification (if applicable) 28-day NOAEC = 0.12 μg a.i./L (mm) Overlying water concentrations

28-day EC50 > 0.11 μg a.i./L (mm) 

28-day NOAEC = 0.03 μg a.i./L (mm) (based on emergence rate) 

Survival, growth and reproduction of aquatic plants 

Aquatic non-vascular species: Most sensitive EC50

TGAI (97.08) 

Green alga (Pseudokirchneriella subcapitata) 

Tier II 96-hr EC50 > 23.8 μg a.i./L (im) 

96-hr NOAEC = 23.8 μg a.i./L (im) 

(no effects) 

TGAI (97.08) 

Cyanobacterium (Anabaena flos-aqua) 

Tier II 96-hr EC50 > 31.5 μg a.i./L (im) 

96-hr NOAEC = 31.5 μg a.i./L (im) (no effects) 

TGAI (97.08) 

Marine diatom (Skeletonema costatum) 

Tier II 96-hr EC50 > 33.6 μg a.i./L (im) 

96-hr NOAEC = 33.6 μg a.i./L (im) (no effects) 

TGAI (97.08) 

Freshwater diatom (Navicula pelliculosa) 

Tier II 96-hr EC50 > 34.3 μg a.i./L (im) 

96-hr NOAEC = 34.3 μg a.i./L (im) (no effects) 

Form. (20.4) 

Green alga (Pseudokirchneriella subcapitata) 

Tier I 72-hr EC50 > 340 μg a.i./L (TWA) 

72-hr NOAEC = 340 μg a.i./L (TWA) (no effects) 

Aquatic vascular species: Most sensitive EC50

TGAI (97.08) 

Duckweed (Lemna gibba) 

Tier II 7-dayEC50 > 38.3 μg a.i./L (im) 

7-day NOAEC = 38.3 μg a.i./L (im) 

(no effects) 

Form = formulation; C.I. = confidence interval; TGAI = technical grade active ingredient; TRR = total radioactive residues 1 BOLD values used in RQ calculations 2 im = initial-measured; mm = mean-measured; nom = nominal; TWA = time-weighted average, measured 
50 

Table 5-4. Endpoints Used to Characterize the Effects of Degradates of Cyflumetofen to Aquatic Organism

Assessment Endpoint 

Measurement Endpoint 

Degradate (%) 

Species Toxicity Values1,2 (Effects) & Acute Toxicity 

Classification (if applicable) 

Survival, growth, and reproduction of freshwater fish (surrogate for aquatic-phase amphibians) 

Most sensitive freshwater fish acute LC50

A-2 (98.3) 

Rainbow trout (Oncorhynchus mykiss) 

96-hr LC50 (95% C.I.) = 7.09 (5.04-9.96) mg a.i./L (mm) 

96-hr NOAEC < 5.04 mg a.i./L (mm) (NOAEC based on sublethal effects including loss of equilibrium, unbalanced swimming, faulty respiratory function, and non-typical pigmentation) Moderately toxic 

B-1 (99.9) 

Rainbow trout (Oncorhynchus mykiss) 

96-hr LC50 > 97.9 mg a.i./L (mm) 

96-hr NOAEC = 97.9 mg a.i./L (mm) (no mortality or sublethal effects) At most slightly toxic 

Survival, growth, and reproduction of freshwater invertebrates 

Most sensitive freshwater invertebrate acute EC50

A-2 (98.3) 

Water flea (Daphnia magna) 

48-hr EC50 (95% C.I.) = 10.52 (8.50-13.10) mg a.i./L (m

Probit Slope (95% C.I.) = 4.20 (2.77-5.62) 48-hr NOAEC = 3.83 mg a.i./L (mm) (NOAEC based on immobility) Slightly toxic 

B-1 (99.99) 

Water flea (Daphnia magna) 

Limit test 48-hr EC50 > 177.5 mg a.i./L (mm) 

48-hr NOAEC = 177.5 mg a.i./L (mm) (no statistically-significant effects; 5% [1 out of 20] immobility at 177.5 mg a.i./L) Practically non-toxic 

B-2 (99.9) 

Water flea (Daphnia magna) 

Limit test 48-hr EC50 > 0.020 mg a.i./L (mm) 

48-hr NOAEC = 0.020 mg a.i./L (mm) (no statistically-significant effects; 5% [1 out of 20] immobility at 0.020 mg a.i./L) Practically non-toxic up to the limit concentration 

Survival, growth, and reproduction of sedimentdwelling invertebrates 

Most sensitive sediment invertebrate chronic NOAEC 

AB-1 (99.8) 

Non-biting midge (Chironomus riparius) 

Spiked sediment exposure Sediment concentrations

28-day EC50 (95% C.I.) = 120 (100-130) mg a.i./kg-dw (

28-day NOAEC = 36.1 mg a.i./kg-dw (mm) Probit Slope = 16.8 ± 4.14 Pore water concentrations

28-day EC50 (95% C.I.) = 68 (48-95) mg a.i./L (mm) 

28-day NOAEC = 34.2 mg a.i./L (mm) Probit Slope = 4.53 ± 2.88 Overlying water concentrations

28-day EC50 (95% C.I.) = 23 (21-25) mg a.i./L (mm) 
51 

Assessment Endpoint 

Measurement Endpoint 

Degradate (%) 

Species Toxicity Values1,2 (Effects) & Acute Toxicity 

Classification (if applicable) 28-day NOAEC = 9.06 mg a.i./L (mm) Probit Slope = 11.3 ± 1.96 (based on emergence rate) 

AB-1 dimer (92.9) 

Non-biting midge (Chironomus riparius) 

Spiked sediment exposure Sediment concentrations

28-day EC50 > 75.3 mg a.i./kg-dw (mm) 

28-day NOAEC = 75.3 mg a.i./kg-dw (mm) Pore water concentrations

28-day EC50 > 5.61 μg a.i./L (mm) 

28-day NOAEC = 5.61 μg a.i./L (mm) Overlying water concentrations

28-day EC50 > 27.4 μg a.i./L (mm) 

28-day NOAEC = 27.4 μg a.i./L (mm) (no statistically-significant effects on rates of emergence development) 

Survival, growth and reproduction of aquatic plants 

Aquatic nonvascular species: Most sensitive EC50

AB-11 (99.6) 

Green alga (Pseudokirchneriella subcapitata) 

Tier I 96-hr EC50 > 0.483 mg a.i./L (im) 

96-hr NOAEC = 0.483 mg a.i./L (im) 

(no effects) 

B-1 (99.99) 

Green alga (Pseudokirchneriella subcapitata) 

Tier II 96-hr EC50 > 102.7 mg a.i./L (mm) 

96-hr NOAEC < 0.10 mg a.i./L (nom) (NOAEC based on cell density, growth rate, and yield) 

Form = formulation; C.I. = confidence interval 1 BOLD values used in RQ calculations 2 im = initial-measured; mm = mean-measured; nom = nominal; TWA = time-weighted average, measured 
52 

No mortality or sublethal effects were noted in any of the acute studies (MRIDs 48542789, 

48542810, and 48542811), including the study with a 20.4% formulation of cyflumetofen 

(MRID 48542921). 

In the chronic study with daphnids (MRID 48542791), there were no effects on parental survival, 

number of offspring per surviving parent, or growth (length and dry weight) (MRID 48542791). 

5.2.1.2 Sediment-Dwelling (Benthic) Invertebrates 

In an acute spiked sediment test conducted with the marine amphipod Leptocheirus plumulosus

(MRID 48542798) and cyflumetofen, there was no statistically-significant mortality resulting in 

a non-definitive LC50 endpoint (i.e., >) and the NOAEC being set at the highest treatment 

concentration: 787 mg TRR/kg-dw, 19.7 mg TRR/L, and 5.2 mg TRR/L for sediment, pore 

water, and overlying water. It should be noted that these endpoints are expressed in terms of 

total radioactive residue and thus may represent parent cyflumetofen as well as degradates. 

 

Chronic spiked water and spiked sediment tests with the freshwater midge Chironomus riparius

were conducted with cyflumetofen. In the test with spiked water, there were no statisticallysignificant effects on rates of emergence or development with the NOAEC being 65.9 μg a.i./L 

for overlying water (MRID 48542799). In the test with spiked sediment, the NOAECs of 26.5 

mg a.i./kg-dw, 0.12 μg a.i./L, and 0.03 μg a.i./L for sediment, pore water, and overlying water 

were based on reduced rates of emergence (MRID 48542802). 

5.2.1.3 Aquatic Plants 

Aquatic plant Tier II studies were conducted with technical grade cyflumetofen (MRIDs 

48542792-5, 48542804). In addition, a Tier I green algal study was conducted with a 20.4% 

formulation of cyflumetofen (MRID 48542922). Toxicity endpoints for studies testing technical 

grade cyflumetofen are based on initial-measured concentrations because the rapid hydrolysis of 

cyflumetofen typically resulted in concentrations that were below the level of detection or 

quantification at study termination. No effects were noted in any of the aquatic plant studies. 

5.2.2 Degradates of Cyflumetofen 

5.2.2.1 Freshwater Fish 

Rainbow trout toxicity tests were conducted with cyflumetofen degradates A-2 and B-1. A-2 is 

moderately toxic to freshwater fish with a 96-hour LC50 of 7.09 mg a.i./L (MRID 48542782) 

whereas B-1 is at most slightly toxic to freshwater fish with a 96-hour LC50 of >97.9 mg a.i./L 

(MRID 48542781). No mortality or sublethal effects were reported in the study with B-1. 

In the study with A-1, 100% mortality was observed in the four highest treatment groups (i.e., 

9.96, 19.24, 38.91, and 81.37 mg a.i./L). In the lowest treatment group of 5.04 mg a.i./L which 

had 0% mortality, reported sublethal effects included unbalanced swimming, faulty respiratory 

function, loss of equilibrium, and non-typical pigmentation. The former two sublethal effects 

were observed at 3-6 hours post-exposure, and loss of equilibrium was observed at 3-6 and 24 

hours post-exposure; only non-typical pigmentation persisted until study termination at 96 hours. 

Therefore, a non-definitive NOAEC of <5.04 mg a.i./L was set for A-2 based on sublethal 

effects. 
53 

5.2.2.2 Freshwater Invertebrates 

Daphnia toxicity tests were conducted with cyflumetofen degradates A-2, B-1, and B-2; tests 

with the latter two degradates were limit tests. A-2 is slightly toxic to freshwater invertebrates 

with an EC50 of 10.52 mg a.i./L (MRID 48542790); B-1 is practically non-toxic to freshwater 

invertebrates with an EC50 of >177 mg a.i./L (MRID 48542787); and B-2 is practically non-toxic 

up to the limit concentration (i.e., 0.020 mg a.i./L; MRID 48542788). The NOAEC for the study 

with A-2 was set at 3.83 mg a.i./L based on immobility observed at higher concentrations. In the 

studies with B-1 and B-2, since there was no statistically-significant immobility, the NOAEC 

was set at the highest treatment concentration (i.e., 177.5 mg a.i./L and 0.020 mg a.i./L, 

respectively). 

5.2.2.3 Sediment-Dwelling (Benthic) Invertebrates 

Chronic spiked sediment tests with Chironomus riparius were conducted with degradates AB-1 

and AB-1 dimer. Endpoints in the test with AB-1 were based on reduced emergence rates with 

NOAECs of 36.1 mg a.i./kg-dw, 34.2 mg a.i./L, and 9.06 mg a.i./L for sediment, pore water, and 

overlying water (MRID 48542801). There were no statistically-significant effects on rates of 

emergence or development in the test with AB-1 resulting in the NOAEC being set at the highest 

treatment concentration: 75.3 mg a.i./kg-dw, 5.61 μg a.i./L, and 27.4 μg a.i./L for sediment, pore 

water, and overlying water (MRID 48542803). 

5.2.2.4 Aquatic Plants 

Toxicity tests with the green alga Pseudokirchneriella subcapitata were conducted with the 

cyflumetofen degradates AB-11 and B-1. There were no effects in the limit test with AB-11 

(MRID 48542796). In the test with B-1, the EC50 was non-definitive (i.e., >102.7 mg a.i./L), and 

there was no NOAEC (i.e., <0.10 mg a.i./L) due to statistically-significant effects at the lowest 

treatment concentration (MRID 48542797). However, there is uncertainty associated with the 

latter study because of the lack of a clear concentration-response relationship. 

5.3 Review of Incident Data 

Reviews of the Ecological Incident Information System (EIIS, version 2.1) and the Avian 

Incident Monitoring System (AIMS) were conducted on March 21, 2013. There are no reported 

incidents for cyflumetofen in the EIIS or AIMS databases. In addition to the incidents recorded 

in EIIS and AIMS, additional pesticide incidents are reported to the Agency in aggregated 

incident reports. Ecological incidents reported in aggregate reports include those categorized as 

‘minor fish and wildlife’ (W-B), ‘minor plant’ (P-B), and ‘other non-target’ (ONT) incidents. 

‘Other non-target’ incidents include reports of adverse effects to insects and other terrestrial 

invertebrates. As of April 3, 2013, there have been no aggregate cyflumetofen ecological 

incidents reported to the Agency. Given that this is a new chemical that has not been registered 

for use in the United States, the existence of ecological incident reports would be unlikely. 
54 

6 Risk Characterization 

6.1 Risk Estimation 

Estimates of exposure to and toxicity of cyflumetofen are integrated using standard risk quotient 

(RQ) methods to evaluate the potential for adverse ecological effects to mammalian, avian, 

aquatic, and other non-target species. RQ results for non-target terrestrial and aquatic animals 

and plants are described in this section and represent expected direct effects to organisms (i.e. 

effects from direct toxicity to cyflumetofen exposure) in contrast to indirect effects to organisms 

resulting from a modification of a resource such as loss of their prey or habitat. 

6.1.1 Direct Effects to Terrestrial Organisms 

6.1.1.1 Birds, Reptiles, and Terrestrial-Phase Amphibians 

Avian chronic, dietary-based RQs were calculated for the maximum application rate for each 

proposed use of cyflumetofen using the NOAEC from the bobwhite quail reproduction study 

(154 mg a.i./kg-diet; MRID 48542777). Avian chronic, dietary-based RQs range from 0.03 to 

0.55 across all uses and feeding categories (Table 6-1). Therefore, the avian chronic LOC of 1 is 

not exceeded for birds of any feeding categories regardless of the proposed use. 

No avian acute RQs were calculated because avian acute oral and sub-acute dietary toxicity 

studies for cyflumetofen have non-definitive endpoints (i.e., >). Risk to birds from acute 

exposure to cyflumetofen as a result of the proposed uses is discussed in the Risk Description 

section of this document. 

Table 6-1. Avian Chronic Dietary-Based Risk Quotients (RQs) 

Use Feeding Category Dietary-Based RQs 

Citrus 

Grapes 

Pome fruits 

Strawberries 

Tree nuts 

Tomatoes 

Ornamentals

Short grass 0.55 

Tall grass 0.25 

Broadleaf plants 0.31 

Fruits/pods 0.03 

Arthropods 0.21 

6.1.1.2 Mammals 

Mammalian chronic dose- and dietary-based RQs were calculated for the maximum application 

rate for each proposed use of cyflumetofen using the NOAEC from a rat 2-generation 

reproduction study (150 mg/kg-diet, 9.21 mg/kg-bw/day; MRID 48542702). Mammalian 

chronic dose- and dietary-based RQs range from 0.03 to 3.97 and 0.22 to 0.56, respectively, 

across all uses and feeding categories (Tables 6-2 and 6-3). The mammalian chronic LOC of 1 

is exceeded small and medium mammals consuming short grass, tall grass, broadleaf plants, or 

arthropods and large mammals consuming short grass or tall grass. 

No mammalian acute dose-based RQs were calculated because the mammalian acute oral 

toxicity study for cyflumetofen has a non-definitive endpoint (i.e., >). No mammalian acute 
55 

dietary-based RQs were calculated because a mammalian acute dietary-based endpoint (i.e., 

LC50, mg/kg-diet) is not available. Risk to mammals from acute exposure to cyflumetofen as a 

result of the proposed uses is discussed in the Risk Description section of this document. 

Table 6-2. Mammalian Chronic Dose-Based Risk Quotients (RQs) 

Use Feeding Category 

Chronic Dose-Based RQs 

Small 

(15 g) 

Medium 

(35 g) 

Large 

(1000 g) 

Citrus 

Grapes 

Pome fruits 

Strawberries 

Tree nuts 

Tomatoes 

Ornamentals

Short grass 3.97* 3.39* 1.82* 

Tall grass 1.82* 1.56* 0.83 

Broadleaf plants 2.24* 1.91* 1.02* 

Fruits/pods 0.25 0.21 0.11 

Arthropods 1.56* 1.33* 0.71 

Seeds 0.06 0.05 0.03 

* exceeds mammalian chronic LOC (=1) 

Table 6-3. Mammalian Chronic Dietary-Based Risk Quotients (RQs) 

Use Feeding Category Chronic Dietary-Based RQs 

Citrus 

Grapes 

Pome fruits 

Strawberries 

Tree nuts 

Tomatoes 

Ornamentals

Short grass 0.56 

Tall grass 0.26 

Broadleaf plants 0.32 

Fruits/pods/seeds 0.04 

Arthropods 0.22 

6.1.1.3 Terrestrial Invertebrates 

RQs for terrestrial invertebrates were not calculated because only non-definitive toxicity 

endpoints (i.e., >) are available for honeybees. Risk to terrestrial invertebrates from exposure to 

cyflumetofen as a result of the proposed uses is discussed in the Risk Description section of this 

document. 

6.1.1.4 Terrestrial (Upland and Semi-Aquatic) Plants 

RQs for dicots were calculated for the maximum application rate and application method 

(ground, aerial) for each proposed use using the EC25 and NOAEC for the most sensitive dicot 

from the seedling emergence study (tomato, EC25/NOAEC = 0.0393/0.000706 lb a.i./A, MRID 

48542933) and dicot NOAEC from the vegetative vigor study (NOAEC = 0.273 lb a.i./A, MRID 

48542932). RQs for monocots were not calculated due to the lack of definitive endpoints for 

monocots (i.e., seedling emergence EC25: could not be determined because the concentrationresponse relationship for dry weight and shoot length was atypical leading to issues with model 

convergence; seedling emergence NOAEC < 0.000706 lb a.i./A; vegetative vigor EC25 > 0.250 

lb a.i./A). Risk to listed monocots from exposure to cyflumetofen as a result of the proposed 

uses will be discussed in the Risk Description section of this document. 
56 

RQs for terrestrial (upland and semi-aquatic) plants are provided in Table 6-4. For dicots 

inhabiting dry (upland) areas, RQs from exposure via total loading range from 0.10 to 17. For 

dicots inhabiting semi-aquatic areas, RQs from exposure via total loading range from 0.56 to 42. 

RQs from exposure via spray drift alone range from <0.1 to 14 for dicots. The terrestrial plant 

LOC of 1 is exceeded for listed dicots from exposure via total loading (runoff and spray drift) 

and spray drift alone for all proposed uses. 

 

Table 6-4. Terrestrial (Upland and Semi-Aquatic) Plant Risk Quotients (RQs) 

Use 

(Application Method) 

Plant Type RQs for Exposure via 

Total Loading (Runoff + Spray Drift) 

RQs for Exposure via

Spray Drift Alone 

Dry (Upland) 

Areas 

Semi-Aquatic 

Areas 

All Areas 

Citrus 

Grapes 

Pome fruits 

Strawberries 

Tree nuts 

Tomatoes 

Ornamentals 

(ground)

Non-listed monocot Not calculateda

 Not calculatedb

Listed monocot Not calculatedc Not calculatedc

Non-listed dicot 0.10 0.56 <0.1 

Listed dicot 5.67* 31.16* 2.83* 

Tomatoes 

(aerial)

Non-listed monocot Not calculateda

 Not calculatedb

Listed monocot Not calculatedc Not calculatedc

Non-listed dicot 0.31 0.76 0.25 

Listed dicot 17.00* 42.49* 14.16* 

App. = application; SE = seedling emergence; VV = vegetative vigor 

*exceeds terrestrial plant LOC (=1) 

a

 due to lack of a SE EC25 for monocots 

b

 due to due to the non-definitive VV EC25 for monocots and lack of a SE EC25 for monocots c

 due to the lack of a SE NOAEC for monocots 

6.1.2 Direct Effects to Aquatic Organisms 

6.1.2.1 Fish, Aquatic-Phase Amphibians, and Aquatic 

Invertebrates 

Fish acute toxicity endpoints are available for parent cyflumetofen (freshwater, estuarine/marine) 

and degradates A-2 (freshwater) and B-1 (freshwater). Aquatic invertebrate acute toxicity 

endpoints are available for parent cyflumetofen (freshwater, Daphnia; estuarine/marine, oyster 

and mysid shrimp) and degradates A-2 (freshwater, Daphnia), B-1 (freshwater, Daphnia), and B2 (freshwater, Daphnia). All of the acute toxicity studies with parent cyflumetofen were 

conducted as limit tests due to its low solubility and have non-definitive endpoints (i.e., >). Of 

the acute studies with degradates, only those with A-2 have definitive endpoints. Collectively, 

the data from these acute studies indicate that degradate A-2 is more toxic than parent 

cyflumetofen, B-1, and B-2. 

Freshwater fish and invertebrate acute RQs were calculated for the maximum application rate for 

each proposed use using definitive toxicity endpoints for degradate A-2 (rainbow trout LC50 = 

7.09 mg/L, MRID 48542782; daphnid EC50 = 10.52 mg/L, MRID 48542790) and surface water 

TTR residue EECs. These RQs represent risk based on the conservative assumption that the 
57 

collective toxicity of the parent and all of its degradates is equivalent to the toxicity of the most 

toxic chemical among the parent and degradates for which data is available. 

Freshwater fish and invertebrate chronic RQs were calculated for the maximum application rate 

for each proposed use using NOAECs from the early life-stage study with fathead minnow (31.6 

μg a.i./L; MRID 48542783) and the life cycle study with Daphnia (16.2 μg a.i./L; MRID 

48542791), respectively, and surface water parent only EECs because the chronic toxicity studies 

were conducted with technical grade cyflumetofen, and the level of exposure to degradates in 

these studies is unknown. 

Freshwater fish and invertebrate acute RQs are all <0.01; freshwater fish and invertebrate 

chronic RQs for parent cyflumetofen are all <0.01. Therefore the aquatic animal acute and 

chronic LOCs of >0.05 and 1, respectively, are not exceeded for freshwater fish and 

invertebrates regardless of the proposed use. 

No acute RQs were calculated for estuarine/marine fish and invertebrates due to the lack of 

definitive acute toxicity endpoints. No chronic RQs were calculated for estuarine/marine fish 

and invertebrates because there are no chronic toxicity endpoints, and application of an acute to 

chronic ratio (ACR) from data for the freshwater counterparts to existing acute toxicity endpoints 

for estuarine/marine taxa is not possible (i.e., the freshwater fish and invertebrate and 

estuarine/marine fish and invertebrate acute toxicity endpoints are non-definitive). Risk to 

estuarine/marine fish as a result of the proposed uses of cyflumetofen is discussed in the Risk 

Description section of this document. 

6.1.2.2 Sediment-Dwelling (Benthic) Invertebrates 

Sub-chronic RQs for estuarine/marine sediment-dwelling invertebrates were calculated for the 

maximum application rate for each proposed use using the NOAEC of 19.7 mg TRR/L from a 

spiked sediment toxicity study with L. plumulosus (MRID 48542798) and both 21-day parent 

only benthic pore water EECs and 21-day TTR benthic pore water EECs. RQs were calculated 

for both types of EECs (i.e., parent only, and TTR) because the degree to which “Total 

Radioactive Residue” represents parent only versus total toxic residues (i.e., parent and 

degradates) is unknown. 

For parent cyflumetofen, chronic RQs for freshwater sediment-dwelling invertebrates were 

calculated for the maximum application rate for each proposed use using NOAECs from spiked 

water and sediment toxicity studies with C. riparius (spiked water NOAEC = 65.9 μg a.i./L, 

MRID 48542799; spiked sediment NOAEC = 0.12 μg a.i./L, MRID 48542802) and 21-day 

parent only surface water EECs and 21-day parent only benthic pore water EECs, respectively. 

For degradates AB-1 and AB-1 dimer, chronic RQs for freshwater sediment-dwelling 

invertebrates were calculated for the maximum application rate for each proposed use using 

NOAECs from spiked sediment toxicity studies with C. riparius (AB-1 NOAEC = 34.2 mg 

a.i./L, MRID 48542801; AB-1 dimer NOAEC = 5.61 μg a.i./L, MRID 48542803) and 21-day 

TTR benthic pore water EECs. The RQs calculated with degradate toxicity endpoints represent 

risk based on the conservative, underlying assumption that the collective toxicity of the parent 

and all of its degradates is equivalent to the toxicity of the tested degradate. 
58 

Sub-chronic RQs for L. plumulosus exposed to sediment spiked with parent cyflumetofen are all 

<0.01; chronic RQs for C. riparius exposed to sediment spiked with parent cyflumetofen range 

from 0.02 to 0.21; chronic RQs for C. riparius exposed to sediment spiked with degradate AB-1 

are all <0.01; RQs for C. riparius exposed to sediment spiked with degradate AB-1 dimer range 

from 0.02 to 0.53; and RQs for C. riparius exposed to water spiked with parent cyflumetofen 

range are all <0.01 (Table 6-5). Therefore, the aquatic animal acute and chronic LOCs of >0.05 

and 1 are not exceeded for sediment-dwelling invertebrates regardless of the proposed use. 

Table 6-5. Sediment-Dwelling (Benthic) Invertebrates Risk Quotients (RQs)

PRZM/EXAMS 

Use/Scenario 

Method of 

App. 

Spiked Sediment Spiked Water

Estuarine/marine Freshwater Freshwater 

L. plumulosus 

Cyflumetofen 

Endpoint 

C. riparius 

Cyflumetofen

Endpoint 

C. riparius 

Degradate 

AB-1 

Endpoint 

C. riparius 

Degradate 

AB-1 Dimer 

Endpoint

C. riparius 

Cyflumetofen

Endpoint 

21-Day 

Parent 

Only 

Benthic 

Pore Water 

EEC

21-Day 

TTR 

Benthic 

Pore Water 

EEC

21-Day 

Parent Only 

Benthic Pore 

Water EEC

21-Day 

TTR 

Benthic 

Pore Water 

EEC

21-Day 

TTR 

Benthic 

Pore Water 

EEC

21-Day 

Parent Only 

Surface Water 

EEC

Citrus 

CA Ground <0.01 <0.01 0.02 <0.01 0.02 <0.01 

FL Ground <0.01 <0.01 0.03 <0.01 0.20 <0.01 

Grapes 

CA Grapes Ground <0.01 <0.01 0.02 <0.01 0.03 <0.01 

CA Wine Grapes Ground <0.01 <0.01 0.08 <0.01 0.16 <0.01 

NY Grapes Ground <0.01 <0.01 0.13 <0.01 0.37 <0.01 

Pome fruits 

NC Ground <0.01 <0.01 0.07 <0.01 0.17 <0.01 

OR Ground <0.01 <0.01 0.02 <0.01 0.11 <0.01 

PA Ground <0.01 <0.01 0.05 <0.01 0.21 <0.01 

Strawberries 

CA Ground <0.01 <0.01 0.02 <0.01 0.07 <0.01 

FL Ground <0.01 <0.01 0.02 <0.01 0.20 <0.01 

Tree nuts 

CA Almond Ground <0.01 <0.01 0.02 <0.01 0.05 <0.01 

OR Filberts Ground <0.01 <0.01 0.02 <0.01 0.11 <0.01 

GA Pecans Ground <0.01 <0.01 0.09 <0.01 0.23 <0.01 

Tomatoes 

CA Aerial <0.01 <0.01 0.13 <0.01 0.24 <0.01 

Ground <0.01 <0.01 0.01 <0.01 0.04 <0.01 

FL Aerial <0.01 <0.01 0.13 <0.01 0.36 <0.01 

Ground <0.01 <0.01 0.03 <0.01 0.19 <0.01 

PA Aerial <0.01 <0.01 0.21 <0.01 0.53 <0.01 

Ground <0.01 <0.01 0.10 <0.01 0.32 <0.01 

Ornamentals 

CA Ground <0.01 <0.01 0.07 <0.01 0.16 <0.01 

FL Ground <0.01 <0.01 0.02 <0.01 0.18 <0.01 

MI Ground <0.01 <0.01 0.02 <0.01 0.21 <0.01 

NJ Ground <0.01 <0.01 0.03 <0.01 0.19 <0.01 

OR Ground <0.01 <0.01 0.02 <0.01 0.06 <0.01 

TN Ground <0.01 <0.01 0.03 <0.01 0.19 <0.01 
59 

6.1.2.3 Aquatic Plants 

RQs for listed aquatic plants were calculated for the maximum application rate for each proposed 

use using the NOAECs from toxicity studies with parent cyflumetofen (duckweed NOAEC = 

38.3 μg a.i./L, MRID 48542804; most sensitive algal NOAEC = 23.8 μg a.i./L, MRID 

48542792) and degradate AB-11 (green algal NOAEC = 0.483 mg a.i./L, MRID 48542797) and 

parent only surface water EECs and TTR surface water EECs, respectively. RQs calculated with 

the degradate toxicity endpoint for AB-11 represent risk based on the conservative, underlying 

assumption that the collective toxicity of the parent and all of its degradates is equivalent to the 

toxicity of AB-11. 

For parent cyflumetofen, RQs for listed non-vascular and vascular aquatic plants range from 0.01 

to 0.08 and 0.01 to 0.14, respectively; for degradate AB-11, RQs for listed non-vascular plants 

range from <0.01 to 0.01 (Table 6-6). Therefore, the aquatic plant LOC of 1 is not exceeded for 

listed aquatic vascular and non-vascular plants regardless of the proposed use. 

For degradate B-1, RQs for listed aquatic non-vascular plants were not calculated because of the 

lack of a NOAEC (i.e., <). RQs for non-listed aquatic plants were not calculated because EC50

endpoints for parent cyflumetofen and degradates AB-11 and B-1 are non-definitive (i.e., >). 

Risk to listed aquatic plants from exposure to B-1 and risk to non-listed aquatic plants from 

exposure to cyflumetofen and degradates AB-11 and B-1 as a result of the proposed uses will be 

discussed in the Risk Description section of this document. 

Table 6-6. Listed Aquatic Plant Risk Quotients (RQs)

PRZM/EXAMS 

Use/Scenario 

Method of 

App. 

Aquatic Vascular 

Plant 

Cyflumetofen 

Endpoint 

Aquatic Non-Vascular 

Plant 

Cyflumetofen 

Endpoint 

Aquatic Non-Vascular 

Plant 

DegradateAB-11 

Endpoint 

Peak Parent Only 

Surface Water EEC

Peak TTR 

Surface Water EEC

Peak TTR 

Surface Water EEC

Citrus 

CA Ground 0.01 0.01 <0.01 

FL Ground 0.01 0.01 0.01 

Grapes 

CA Grapes Ground 0.01 0.01 <0.01 

CA Wine Grapes Ground 0.01 0.02 0.01 

NY Grapes Ground 0.02 0.04 0.01 

Pome fruits 

NC Ground 0.01 0.02 0.01 

OR Ground 0.01 0.01 <0.01 

PA Ground 0.01 0.02 0.01 

Strawberries 

CA Ground 0.01 0.01 <0.01 

FL Ground 0.01 0.01 0.01 

Tree nuts 

CA Almond Ground 0.01 0.01 <0.01 

OR Filberts Ground 0.01 0.01 <0.01 

GA Pecans Ground 0.02 0.04 0.01 

Tomatoes 

CA Aerial 0.08 0.12 0.01 
60 

PRZM/EXAMS 

Use/Scenario 

Method of 

App. 

Aquatic Vascular 

Plant 

Cyflumetofen 

Endpoint 

Aquatic Non-Vascular 

Plant 

Cyflumetofen 

Endpoint 

Aquatic Non-Vascular 

Plant 

DegradateAB-11 

Endpoint 

Peak Parent Only 

Surface Water EEC

Peak TTR 

Surface Water EEC

Peak TTR 

Surface Water EEC

Ground 0.01 0.01 <0.01 

FL Aerial 0.08 0.13 0.01 

Ground 0.01 0.01 0.01 

PA Aerial 0.08 0.14 0.02 

Ground 0.03 0.04 0.01 

Ornamentals 

CA Ground 0.01 0.02 0.01 

FL Ground 0.01 0.01 <0.01 

MI Ground 0.01 0.01 0.01 

NJ Ground 0.01 0.01 0.01 

OR Ground 0.01 0.01 <0.01 

TN Ground 0.01 0.01 <0.01 

6.1.2.4 Aquatic Bioaccumulation 

KABAM was used to calculate risk quotients from a bioaccumulation pathway for food items 

that may be consumed by listed and non-listed species. The RQs for bioaccumulation risk did 

not exceed levels of concern for mammals or birds (Table 6-7). 

Table 6-7. Bioaccumulation Risk Quotients (RQs) for Mammals and Birds 

Wildlife Species Acute Chronic 

Dose Based Dietary Based Dose Based Dietary Based 

Mammals 

Fog/water shrew 0.001 N/A 0.116 0.021 

Rice rat/star-nosed mole 0.001 N/A 0.140 0.021 

Small mink 0.001 N/A 0.176 0.028 

Large mink 0.001 N/A 0.195 0.028 

Small river otter 0.001 N/A 0.210 0.028 

Large river otter 0.001 N/A 0.247 0.031 

Birds 

Sandpipers 0.003 0.001 N/A 0.025 

Cranes 0.000 0.001 N/A 0.025 

Rails 0.001 0.001 N/A 0.029 

Herons 0.000 0.001 N/A 0.029 

Small osprey 0.000 0.001 N/A 0.034 

White pelican 0.000 0.001 N/A 0.037 

6.2 Risk Description 

The following risk description explains the overall direct effect conclusions regarding potential 

ecological risk from the proposed uses of cyflumetofen. The risk description takes into 

consideration all lines of evidence including: risk estimates (i.e., RQ results); information on the 

chance of individual effect (i.e., mortality or immobilization) for the acute RQ values; 

comparisons of non-definitive toxicity endpoints (i.e., >) to EECs; data from monitoring, field 

studies, and reported incidents that may provide additional insights into the likelihood of 

exposure; and other factors that modify the likelihood of exposure such as timing of application, 
61 

overlap of area affected and the degree of effect with the presence/absence of taxa, species 

sensitivity distribution, and presence/absence of dietary items. 

6.2.1 Direct Effects to Birds, Reptiles, and Terrestrial-Phase 

Amphibians 

Avian acute RQs were not calculated because avian acute oral and subacute-dietary toxicity 

studies for cyflumetofen have non-definitive endpoints (i.e., >). Instead, the most sensitive, nondefinitive acute dose- and dietary-based toxicity values for birds were compared directly to the 

highest avian acute dose- and dietary-based EECs for the proposed uses of cyflumetofen. 

An acute oral study with bobwhite quail yielded the most sensitive, non-definitive avian dosebased toxicity endpoints, LD50 > 2000 mg a.i./kg-bw and NOAEL = 74 mg a.i./kg-bw based on 

the sublethal effect of hunched posture (MRID 48542772). A sub-acute dietary study with 

bobwhite quail yielded the most sensitive, non-definitive avian dietary-based endpoints, LC50 > 

5033 mg a.i./kg-diet and NOAEC = 1133 mg a.i./kg-diet based on the sublethal effect of reduced 

weight gain (MRID 48542775). 

The highest avian dose-based EECs correspond to those for small birds (20 g) and range from 

1.33 (seeds) to 96.10 (short grass) mg/kg-bw. Dietary-based EECs range from 5.27 

(fruits/pods/seeds) to 84.38 (short grass) mg/kg-diet. These EECs are unlikely to cause avian 

mortality since they are roughly 2-3 orders of magnitude less than test concentrations that caused 

no mortality in toxicity study. Similarly, these EECs are unlikely to cause reduced weight gain 

since they are at least an order of magnitude less than test concentrations that caused this 

sublethal effect in the bobwhite quail sub-acute dietary study. However, the range of dose-based 

EECs does include test concentrations that were associated with sublethal effects (i.e., hunched 

posture) in the acute oral study with bobwhite quail. Given that hunched posture was not 

observed in the sub-acute dietary or chronic, reproductive studies with bobwhite quail, the 

potential for cyflumetofen to cause this effect as a result of the proposed uses is low. Therefore, 

this comparative analysis suggests that the likelihood of adverse effects to birds, reptiles, and 

terrestrial-phase amphibians from acute exposure to cyflumetofen for all proposed uses is low. 

The avian chronic LOC (=1) is not exceeded for birds of any feeding category regardless of use. 

suggesting that the likelihood of adverse effects to birds, reptiles, and terrestrial-phase 

amphibians from chronic exposure to cyflumetofen for all proposed uses is low. 

6.2.2 Direct Effects to Mammals 

Mammalian acute RQs were not calculated because the mammalian acute oral toxicity study has 

a non-definitive endpoint (i.e., >), and a mammalian acute dietary-based endpoint (i.e., LC50,

mg/kg-diet) is not available. Instead, the non-definitive acute dose-based toxicity endpoint for 

mammals was compared directly to the highest mammalian acute dose-based EECs for the 

proposed uses of cyflumetofen. 

An acute oral study with female Wistar rats yielded the non-definitive dose-based toxicity 

endpoint of LD50 > 2000 mg a.i./kg-bw (MRID 48542669). The highest mammalian dose-based 

EECs correspond to those for small mammals (15 g) and range from 1.12 (seeds) to 80.45 (short 
62 

grass) mg/kg-bw. These EECs are unlikely to result in mammalian mortality or sublethal effects 

since they are roughly 2-3 orders of magnitude less than test concentrations that caused no 

mortality or transitory sublethal effects in the acute oral toxicity study. Therefore, this 

comparative analysis suggests that the likelihood of adverse effects to mammals from acute 

exposure to cyflumetofen for all proposed uses is low. 

The mammalian chronic LOC of 1 is exceeded for small and medium mammals consuming short 

grass, tall grass, broadleaf plants, or arthropods and large mammals consuming short grass or tall 

grass for all of the proposed uses of cyflumetofen. The exceedances across multiple sizes and 

feeding categories of mammals suggest that they may be at risk from chronic exposure as a result 

of the proposed uses of cyflumetofen. Reducing the foliar dissipation half-life in T-REX from 

the default of 35 days to 1 day and number of applications from 2 to 1 still results in chronic 

LOC exceedances for small and medium consuming short grass or broadleaf plants, small 

mammals consuming tall grass, and large mammals consuming short grass. 

6.2.3 Direct Effects to Terrestrial Invertebrates 

Presently, the Agency does not have a formal methodology for evaluating risk to non-target 

terrestrial invertebrates. Instead, acute contact- and dietary-based EECs for the proposed uses of 

cyflumetofen were calculated (Table 6-7) and directly compared to acute contact- and oral-based 

toxicity values for honey bees, respectively. 

Table 6-7. Calculation of Contact and Dietary EECs for Honey Bees 

Contact EEC for forager bees receiving direct spray (μg a.i./bee) = 

maximum single application rate (lb a.i./A) x 2.7 (μg a.i./bee per 1 lb a.i./A) = 

0.2 lb a.i./A x 2.7 μg a.i./bee per 1 lb a.i./A = 

0.54 μg a.i./bee 

Dietary (oral) EEC for adult bees (μg a.i./bee) = 

T-REX-generated upper-bound EECs for tall grass (mg a.i./kg-diet = μg a.i./g-diet) x 0.292 (g/day)b

 = 

38.67 μg a.i./g-dieta x 0.292 (g/day) = 

11.29 μg a.i./bee a

 from Table 4-4

b

 most conservative food consumption rate for worker bees 

For both technical grade cyflumetofen and a 20.4% formulation of cyflumetofen, the honey bee 

acute contact LD50 is >100 μg a.i./bee (MRIDs 48542805 and 48542914). This non-definitive 

contact toxicity endpoint is almost 3 orders of magnitude greater than the honey bee contact EEC 

of 0.54 μg a.i./bee. The NOAEL of 20.7 μg a.i./bee for the acute contact study with technical 

grade cyflumetofen, which is based on statistically-significant mortality at 45.5 lb a.i./bee, is 

almost 2 orders of magnitude greater than the honey bee contact EEC. The NOAEL of 4.6 μg 

a.i./bee for the acute contact study with a 20.4% formulation of cyflumetofen, which is based on 

the sublethal effect of lethargy, is almost an order of magnitude greater that the honey bee 

contact EEC. For a 20.3% formulation of cyflumetofen, the acute oral LD50 is >116 μg a.i./bee, 

and the NOAEL is 116 μg a.i./bee (MRID 48542923). These oral toxicity endpoints are an order 

of magnitude greater than the honey bee dietary (oral) EEC of 11.29 μg a.i./bee. 

Additional toxicity data from studies with beneficial terrestrial arthropods bolsters the conclusion 

of the low likelihood of adverse effects to non-target terrestrial invertebrates from the proposed 
63 

uses of cyflumetofen. Acute limit tests with two beneficial terrestrial arthropods – the parasitic 

wasp (A. rhopalosiphi) and the predatory mite (T. pyri) – using a 20.3% formulation of 

cyflumetofen both yielded a LR50 of >1.2 lb a.i./A and a NOAEC of 1.2 lb a.i./A which are 

greater than the single maximum application rate of 0.2 lb a.i./A for cyflumetofen (MRIDs 

48542924 and 48542725). 

Collectively, this comparative analysis suggests that the likelihood of adverse effects to honey 

bees and some beneficial terrestrial arthropods from acute contact and/or dietary/oral exposure to 

cyflumetofen for all proposed uses appears to be low. However, given the insecticidal mode of 

action of cyflumetofen, the potential for risk to sensitive, non-target terrestrial invertebrates 

exists. 

6.2.4 Direct Effects to Terrestrial (Upland and Semi-Aquatic) Plants 

The terrestrial plant LOC of 1 is not exceeded for non-listed dicots from exposure via total 

loading (runoff and spray drift) or spray drift only regardless of use suggesting that the 

likelihood of adverse effects to non-listed dicots from exposure to cyflumetofen for all proposed 

uses is low. In contrast, the terrestrial plant LOC of 1 is exceeded for listed dicots from exposure 

via total loading and spray drift only for all proposed uses suggesting that listed dicots may be at 

risk from exposure as a result of the proposed uses of cyflumetofen. 

It should be noted that the most sensitive dicot in the seedling emergence study – tomato – is one 

of the proposed uses for cyflumetofen; the seedling emergence EC25 and NOAEC for tomato are 

0.0393 lb a.i./A and 0.000706 lb a.i./A, respectively. However, effects noted in the seedling 

emergence study should not be applicable to the proposed uses of cyflumetofen since application 

presumably will not occur until plants reach the vegetative growth stage when no effects are 

expected based on results of the vegetative vigor study (i.e., in the vegetative vigor study, there 

were no statistically-significant effects on tomato up to the highest concentration tested – 0.273 

lb a.i./A – which is greater than the proposed maximum single application rate of 0.2 lb a.i./A). 

RQs were not calculated for monocots due to the lack of appropriate endpoints for monocots. 

Specifically, for the most sensitive monocot of oat, a seedling emergence EC25 could not be 

determined because the endpoints of dry weight and shoot length displayed atypical 

concentration-responses leading to issues with model convergence. In addition, dry weight and 

shoot length of the lowest treatment group (i.e., 0.000706 lb a.i./A) were significantly reduced 

when compared to the control group resulting in the lack of a NOAEC for monocots. In the 

absence of RQs for monocots, the lowest seedling emergence treatment concentration that 

yielded significant effects – 0.000706 lb a.i./A – was compared to the range of terrestrial plant 

EECs as presented in Table 4-6 (i.e., 0.002-0.02 lb a.i./A). The comparison indicates that 

terrestrial plant EECs are greater than an exposure concentration that caused a significant a 

decrease in oat dry weight and shoot length implying that listed monocots may be at risk from 

exposure via total loading (runoff and spray drift) and spray drift only for all proposed uses. 

Furthermore, given the inability to determine a seedling emergence EC25 for monocots, risk to 

non-listed monocots cannot be precluded. 

Overall, adverse effects to terrestrial plants (listed dicots and all monocots) from exposure to 

cyflumetofen as a result of the proposed uses are possible. A Tier II seedling emergence 
64 

continuation study with oat is necessary to reduce uncertainty associated with the risk conclusion 

for non-listed monocots as well as buffer distances for listed monocots. 

6.2.4.1 Buffer Distances for Reducing Risk to Non-Target 

Terrestrial Plants from Spray Drift 

Buffer distances for listed dicots and listed and non-listed monocots were determined via 

AgDRIFT using the NOAEC and EC25 endpoints for seedling emergence in Table 5-3. These 

buffer distances are provided in Table 6-8. In the absence of a NOAEC for oat, buffer distances 

for oat were calculated using the LOAEC. Therefore, the distance offsite where effects to oat are 

no longer expected are actually greater than those presented in the table. It should be noted that 

buffer distances for the aerial application scenarios exceed the AgDRIFT Tier 1 aerial modeling 

limit of ~1000 feet for oat and tomato. 

Table 6-8. Buffer Distances for Listed Dicots and Listed and Non-Listed Monocots 

Species 

Distance (feet) From the Edge of Field Where the RQ Falls Below the 

Terrestrial Plant LOC for Seedling Emergence Endpoints 

Ground Applicationa Aerial Application 

VF-F Drop Size F-M/C Drop Size VF-F Drop Size F-M Drop Size

Listed Nonlisted Listed Nonlisted Listed Nonlisted Listed Nonlisted

Monocots 

Oat(Avena sativa)

b

 299 CBDc 138 CBDc >1000 CBDc >1000 CBDc

Onion (Allium sepa) 10 CBDd 3 CBDd 256 CBDd 82 CBDd

Corn (Zea mays) 0 CBDd 0 CBDd 0 CBDd 0 CBDd

Ryegrass (Lolium perenne) 0 CBDd 0 CBDd 0 CBDd 0 CBDd

Dicots 

Tomato (Lycopersicon esculentum) 299 

NA 

138 

NA 

>1000 

NA 

>1000 

NA 

Cucumber (Cucumis sativa) 10 3 269 89 

Sugarbeet (Beta vulgaris) 3 3 0 0 

Radish (Raphanus sativus) 0 0 0 0 

Lettuce (Lactuca sativa) 0 0 0 0 

Soybean (Glycine max) 0 0 0 0 

CBD = could not be determined; NA = not applicable 

VF-F = ASAE Very Fine to Fine; F-M/C = ASAE Fine to Medium/Course; F-M = ASAE Fine to Medium 

a

 Low boom (20 inches) 

b

 buffer distances calculated using the LOAEC due to the lack of a NOAEC c

 While statistically-significant reductions were detected, there were issues with model convergence. Therefore, an 

EC25 could not be determined. 

d

 The EC25 is greater than the highest tested concentration. 

6.2.5 Direct Effects to Fish, Aquatic-Phase Amphibians, and Aquatic 

Invertebrates 

The acute RQs calculated for freshwater fish and invertebrate represent risk based on the 

conservative assumption that the collective toxicity of parent cyflumetofen and all of its 

degradates is equivalent to the toxicity of the most toxic chemical among the parent and 

degradates for which data is available (i.e., degradate A-2). Even under this conservative 

assumption, acute aquatic animal LOCs (>0.05) were not exceeded for freshwater fish or 

invertebrates regardless of use suggesting that the likelihood of adverse effects to freshwater fish 
65 

and invertebrates and aquatic-phase amphibians from acute exposure as a result of the proposed 

uses of cyflumetofen is low. 

 

It should be noted that the freshwater fish acute toxicity study with A-2 yielded a NOAEC of 

<5.04 mg a.i./L (MRID 48542782). This NOAEC is based on sublethal effects including 

unbalanced swimming, faulty respiratory function, loss of equilibrium, and non-typical 

pigmentation observed at the lowest concentration tested. Overall, the likelihood of adverse 

effects to freshwater fish and aquatic-phase amphibians from acute exposure to A-2 is considered 

low because: 1) acute RQs calculated using the LC50 endpoint did not exceed LOCs; 2) no 

sublethal effects were observed in fish acute toxicity studies with parent cyflumetofen where the 

organisms were presumably exposed to A-2 as a result of rapid hydrolysis, and 3) TTR surface 

water EECs, which represent parent cyflumetofen and multiple degradates including A-2, are at 

least 3 orders of magnitude less than the observed NOAEC for A-2. 

 

The aquatic animal chronic LOC (=1) is not exceeded for freshwater fish or invertebrates 

regardless of use suggesting that the likelihood of adverse effects to freshwater fish and 

invertebrates and aquatic-phase amphibians from chronic exposure as a result the proposed uses 

of cyflumetofen is low. 

Estuarine/marine fish and invertebrate RQs were not calculated because of the lack of 

appropriate toxicity endpoints. Based on a comparison of acute toxicity endpoints between 

freshwater and estuarine/marine organisms, there is no indication that estuarine/marine 

fish/invertebrates are more sensitive to parent cyflumetofen than freshwater fish/invertebrates. 

In addition, estuarine/marine fish/invertebrates would have to be several orders of magnitude 

more sensitive than freshwater fish/invertebrates to the most toxic degradate tested, A-2, to 

exceed Agency LOCs suggesting that the likelihood of adverse effects to estuarine/marine fish 

and invertebrates as a result of the proposed uses of cyflumetofen is low. 

6.2.6 Direct Effects to Sediment-Dwelling (Benthic) Invertebrates 

The aquatic animal acute and chronic LOCs (>0.05 and 1, respectively) are not exceeded for 

sediment-dwelling (benthic) invertebrates regardless of use suggesting that the likelihood of 

adverse effects to benthic invertebrates from acute or chronic exposure to cyflumetofen for all 

proposed uses is low. 

6.2.7 Direct Effects to Aquatic Plants 

The aquatic plant LOC (=1) is not exceeded for listed aquatic plants exposed to parent 

cyflumetofen or degradate AB-11 regardless of use suggesting that the likelihood of adverse 

effects to listed aquatic plants as a result of the proposed uses of cyflumetofen is low. 

It should be noted that a P. subcapitata toxicity study with B-1 yielded a NOAEC of <0.10 mg 

a.i./L based on cell density, growth rate, and yield (MRID 48542797). However, there is 

uncertainty associated with this NOAEC due to the lack of a clear concentration-response 

relationship. Given that B-1 was not considered in the TTR approach for modeling surface water 

EECs because of its low expected toxicity (i.e., due to lack of a cyano group) and the actual 

NOAEC for B-1would have to be 2 orders of magnitude lower than the lowest concentration 
66 

tested to exceed the Agency LOC for listed aquatic plants, the likelihood of adverse effects to 

aquatic non-vascular plants from exposure to B-1 for all proposed uses is considered low. 

RQs for non-listed aquatic plants were not calculated for parent cyflumetofen or degradates AB11 and B-1 because of the lack of definitive EC50 endpoints (i.e., >). Given that risk to listed 

aquatic plants is based on the NOAEC, which is a more sensitive endpoint than the EC50, and 

there were no exceedances for listed aquatic plants, the likelihood of adverse effects to non-listed 

aquatic non-vascular and vascular plants as a result of the proposed uses of cyflumetofen is low. 

6.3 Summary of Direct Effects 

A summary of the direct effects of cyflumetofen to terrestrial and aquatic taxa is provided in 

Table 6-9. 

Table 6-9. Summary of Direct Effects 

Taxon Risk Concern for Direct Effects? 

Non-Listed Listed* 

Birds (surrogate for terrestrial-phase amphibians and 

reptiles) No No 

Mammals Yes (chronic exposurea

) Yes (chronic exposurea) 

Terrestrial invertebrates No No 

Terrestrial (upland and semi-aquatic) plants : monocots Yesb Yes 

Terrestrial (upland and semi-aquatic) plants: dicots No Yes 

Freshwater fish (surrogate for aquatic-phase amphibians) No No 

Freshwater invertebrates No No 

Estuarine/marine fish No No 

Estuarine/marine invertebrates No No 

Sediment-dwelling (benthic) invertebrates No No 

Aquatic vascular plants (vascular and non-vascular) No No 

Aquatic non-vascular plants No NA 

NA = not applicable because there are no listed aquatic non-vascular plants 

* Direct or indirect effects to specific listed species have not been definitively determined; further investigation into 

temporal, geographical, and biological associations between the proposed uses and affected taxa is needed before 

definitive effects determinations can be made. a

 small and medium mammals consuming short grass, tall grass, broadleaf plants, or arthropods and large mammals 

consuming short grass or tall grass 

b

 Given the inability to determine a seedling emergence EC25 for monocots, risk to non-listed monocots cannot be 

precluded. 

6.4 Indirect Effects 

Direct effects to mammals (non-listed and listed) from chronic exposure could result in indirect 

effects to terrestrial organisms including birds, terrestrial invertebrates, and terrestrial plants due 

to general habitat modification and/or food/prey supply disruption. 

Direct effects to monocots (listed and non-listed) and listed dicots could result in indirect effects 

to terrestrial organisms including birds, mammals, and terrestrial invertebrates due to general 

habitat modification (most likely due to effects on non-listed plants), host plant loss, and/or food 

supply disruption as well as indirect effects to aquatic organisms due to changes in water quality 

and/or habitat. 
67 

6.5 Federally Threatened and Endangered (Listed) Species Concerns 

6.5.1 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 conservatively assumes that listed species within those broad groups are 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 the listed species are located 

within an assumed area that has the relatively highest potential exposure to the pesticide, and that 

exposures are likely to decrease with distance from the treatment area. 

If the assumptions associated with the screening-level action area result in risk quotients 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, 

risk quotients 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 risk 

quotient as a resource. However, in situations where the screening assumptions lead to risk 

quotients 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 affect 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. 

6.5.2 Taxonomic Groups Potentially at Risk 

The Level I screening assessment process for listed species uses the generic taxonomic groupbased process to make inferences on direct effect concerns for listed species. The first iteration 

of reporting the results of the Level I screening is a listing of pesticide use sites and taxonomic 

groups for which RQ calculations reveal values that meet or exceed the listed species LOCs or 

other evidence suggests that adverse effects are likely or cannot be precluded (for more 

information see, USEPA, 2004). 

Results of this screening-level ecological risk assessment indicate that the proposed uses of 

cyflumetofen have the potential for direct adverse effects to listed mammals, dicots, and 

monocots (Table 6-10). 

The Agency acknowledges that pesticides have the potential to exert indirect effects upon listed 

organisms by, for example, perturbing forage or prey availability, altering the extent of nesting 

habitat, and creating gaps in the food chain. In conducting a screen for indirect effects, direct 

effect LOCs for each taxonomic group are used to make inferences concerning the potential for 
68 

indirect effects upon listed species that rely upon non-listed organisms in these taxonomic groups 

as resources critical to their life cycle. 

Results of this screening-level ecological risk assessment indicate that the proposed uses of 

cyflumetofen have the potential for direct adverse effects to non-listed mammals and monocots. 

Therefore, there is potential for indirect effects to all listed species that depend on non-listed 

mammals and monocots for food, habitat, or other environmental resources (Table 6-10). 

Species-specific concerns for indirect effects to listed organisms will require a determination of 

the coincidence of cyflumetofen use with locations of listed species and the biologically-based 

resources upon which they depend. 

Table 6-10. Risk to Listed Taxa Associated with Potential Direct or Indirect Effects from 

the Proposed Uses of Cyflumetofen* 

Listed Taxon Direct Effects Indirect Effects

Birds No Yesa,b

Reptiles No Yesa,b

Terrestrial-phase amphibians No Yesa,b

Mammals Yes (chronic exposure) Yesb

Terrestrial invertebrates No Yesa,b

Terrestrial (upland and semi-aquatic) plants : monocots Yes Yesa

Terrestrial (upland and semi-aquatic) plants: dicots Yes Yesa

Freshwater fish No Yesb

Aquatic-phase amphibians No Yesb

Freshwater invertebrates No Yesb

Estuarine/marine fish No Yesb

Estuarine/marine invertebrates No Yesb

Sediment-dwelling (benthic) invertebrates No Yesb

Aquatic vascular plants No Yesb

Aquatic non-vascular plants NA Yesb

NA = not applicable because there are no listed aquatic non-vascular plants 

* Direct or indirect effects to specific listed species have not been definitively determined; further investigation into 

temporal, geographical, and biological associations between the proposed uses and affected taxa is needed before 

definitive effects determinations can be made. a

 due to direct effects to non-listed mammals 

b

 due to direct effects to non-listed monocots which cannot be precluded given the inability to determine a seedling 

emergence EC25 for monocots 

6.5.2.1 Probit Slope Dose-Response Analysis of LOC and Acute 

RQ Values 

As part of risk estimation, the Agency provides additional information on the potential for acute 

direct effects to exposed individuals in terms of the chance of an individual event (i.e., mortality 

or immobilization) should exposure at the EEC actually occur for a species with sensitivity to 

cyflumetofen on par with the acute toxicity endpoint selected for RQ calculation. This is 

accomplished using the slope of the dose-response relationship available from the toxicity study 

used to establish the acute toxicity measures of effect for each taxonomic group. The individual 

effects probability associated with the acute RQ is based on the mean estimate of the slope and 

an assumption of a probit dose-response relationship. In addition to a single effects probability 

estimate based on the mean, upper and lower estimates of the effects probability are also 

provided to account for variance in the slope, if available. Individual effect probabilities are 
69 

calculated based on an Excel spreadsheet tool IECv1.1 (Individual Effect Chance Model Version 

1.1) developed by U.S. EPA, OPP, Environmental Fate and Effects Division (June 22, 2004). 

The model provides the option of inserting taxa-specific probit slopes and confidence intervals. 

If specific information is not available, the model uses a default value of 4.5 for the probit slope 

and 2 and 9 for the upper and lower 95% confidence interval bounds. 

For cyflumetofen, avian, mammalian, fish, and aquatic invertebrate acute toxicity studies with 

parent cyflumetofen yielded non-definitive endpoint values (i.e., >), so this probit slope analysis 

is not applicable. 

6.5.2.2 Critical Habitat 

In the evaluation of pesticide effects on designated critical habitat, consideration is given to the 

physical and biological features (constituent elements) of a critical habitat identified by the U.S. 

Fish and Wildlife and National Marine Fisheries Services (the Services) as essential to the 

conservation of a listed species and which may require special management considerations or 

protection. The evaluation of effects for a screening-level pesticide risk assessment focuses on 

the biological features that are constituent elements and is accomplished using the screeninglevel taxonomic analysis (RQs) and levels of concern (LOCs) that are used to evaluate direct and 

indirect effects to listed organisms. 

The screening-level risk assessment has identified potential concerns for indirect effects to listed 

species dependent upon some non-listed species (mammals and monocots). In light of the 

potential for indirect effects, the next step for EPA and the Services is to identify which listed 

species and their designated critical habitat(s), if applicable, are potentially implicated. 

Analytically, the identification of such species and their critical habitat can occur by determining 

whether the action area overlaps designated critical habitat or the occupied range of any listed 

species. If so, EPA would examine whether the pesticide's potential effects to non-listed species 

would affect the listed species indirectly, or directly affect a constituent element of the critical 

habitats. At present, the information reviewed by EPA does not permit use of this analytical 

approach to make a definitive identification of species that are potentially affected indirectly or 

designated critical habitats that are potentially affected directly by the proposed uses of 

cyflumetofen. 

This screening-level risk assessment for critical habitats provides a listing of potential biological 

features that, if they are constituent elements of one or more critical habitats, would be of 

potential concern. These correspond to the taxa identified above as being of potential concern 

for adverse effects. This should serve as an initial step in problem formulation for further 

assessment of designated critical habitat impacts outlined above, should additional work be 

necessary. 

6.5.2.3 Co-occurrence Analysis 

The goal of the analysis for co-location is to determine whether sites of cyflumetofen proposed 

use are geographically associated with known locations of listed species. At the screening level, 

this analysis is accomplished using the LOCATES (version 2.2.5) database. The database uses 

location information for listed species at the county level and compares it to agricultural census 
70 

data (from 2007) for crop production at the same county level of resolution. The product is a 

listing of federally-listed species that are located within counties known to produce the crops 

upon which cyflumetofen is proposed to be used. The current analysis is based on the following 

proposed uses of cyflumetofen: almonds, apples, chestnut, cironjas, citron, citrus fruit-all, 

grapefruit, grapes, hazel nuts (filberts), kumquats, lemons, lemons and limes, limes, macadamia 

nuts, pears-all, pears-Bartlett, pears-other, pecans-all, pecans-improved, pecans-native and 

seedling, tangelo, tangerine, walnuts-English. For potential direct effects, only listed mammals, 

monocots, and dicots will be considered, since they were the only taxa for which direct risks 

were identified. For indirect effects, all other taxa will be considered since there is a potential 

for indirect effects to taxa that might rely on non-listed mammals and monocots for some stage 

of their life-cycle. 

LOCATES identified a total of 1368 listed species that overlap at the county level with areas 

where cyflumetofen is proposed to be used (see Appendix F for a complete species list). This 

preliminary analysis indicates that there is a potential for cyflumetofen use to overlap with listed 

species and that a more refined assessment is warranted. The more refined assessment should 

involve clear delineation of the action area associated with proposed uses of cyflumetofen and 

best available information on the temporal and spatial co-location of listed species with respect 

to the action area. This analysis has not been conducted for this assessment. 

7 Uncertainties 

A description of basic assumptions, uncertainties, strengths, and limitations of a typical risk 

assessment is described in Chapter 6 of the Agency’s Overview Document (USEPA, 2004) and 

includes those related to exposure for all taxa, those related to exposure for aquatic species, those 

related to exposure for terrestrial animals, those related to the effects assessment, and those 

associated with the acute LOC values. Additional uncertainties for this assessment are discussed 

below. 

7.1 Data Gaps 

7.1.1 Environmental Fate 

Uncertainties in the fate data with the dimers and unextracted residues were described in detail in 

Sections 2.6 and 4.2. Dimers that formed in the hydrolysis, aerobic and anaerobic soil 

metabolism, aerobic aquatic metabolism, and terrestrial field dissipation studies. Unextracted 

residues formed in the aerobic and anaerobic soil metabolism and aerobic and anaerobic aquatic 

metabolism studies. The issues of dimers and unextracted residues are somewhat intertwined in 

that: the dimers are expected to be hydrophobic and would likely accumulate in soil and 

sediment; the dimers and unextracted residues tend to occur at their highest quantities at the end 

of the fate studies; and high quantities of dimers and unextracted residues tend to occur in the 

same studies (aerobic and anaerobic soil metabolism and aerobic aquatic metabolism). 

The concern would be that dimers will form, persist and accumulate in the environment. 

However, this risk assessment did not identify risks to aquatic organisms. Therefore, it seems 

further clarification on these issues would be unlikely to change this aquatic risk finding. If 
71 

future risk assessments were to identify aquatic risks, more information of the formation of 

dimers and composition of the unextracted residues might be useful. 

7.1.2 Ecological Effects 

Oat data from a Tier II seedling emergence continuation study (Guideline 850.4100 – Seedling 

Emergence and Seedling Growth) would allow the Agency to better characterize potential risks 

by eliminating uncertainties for both non-listed and listed monocots that cannot be accounted for 

using alternate methods or weight of evidence. The submitted seedling emergence study (MRID 

48542933) was classified as Supplemental because for the most sensitive monocot – oat, dry 

weight and shoot length of the lowest treatment group (i.e., 0.000706 lb a.i./A) were significantly 

reduced (i.e., 33.2 and 27.3 %, respectively) when compared to the control group resulting in a 

non-definitive NOAEC for monocots. In addition, an EC25 for monocots could not be 

determined because the oat endpoints of dry weight and shoot length an displayed atypical 

concentration-response relationship leading to issues with model convergence 

8 References 

Arnot, J.A. and F.A.P.C. Gobas. 2004. A food web bioaccumulation model for organic chemicals 

in aquatic ecosystems. Environmental Toxicology & Chemistry, 23 (10): 2343-2355. 

Fletcher, J.S., J.E. Nellessen, and T.G. Pfleeger. 1994. Literature review and evaluation of the 

EPA food-chain (Kenaga) nomogram, an instrument for estimating pesticide residues on 

plants. Environmental Toxicology & Chemistry 13:1383-1391. 

Hoerger, F. and E. E. Kenaga. 1972. Pesticide Residues on Plants: Correlation of 

Representative Data as a Basis for Estimation of their Magnitude in the Environment. In F. 

Coulston and F. Korte, eds., Environmental Quality and Safety: Chemistry, Toxicology, and 

Technology, Georg Thieme Publ., Stuttgart, West Germany, pp. 9-28. 

USEPA. 1999. Downwind Deposition Tolerance Bounds for Orchards. Scientific Advisory Panel 

background document. Office of Pesticide Programs. Washington, D.C. July 23, 1999. 

http://www.epa.gov/scipoly/sap/1999/july/airblast.pdf

USEPA. 1997. Estimating Drinking Water Exposure as a Component of the Dietary Risk 

Assessment; Spray Drift Program, Washington, D.C. 

http://www.epa.gov/scipoly/sap/meetings/1997/121097

USEPA. 1998. Guidelines for Ecological Risk Assessment. Risk Assessment Forum, Office of 

Research and Development, Washington, D.C. EPA/630/R-95/002F. April 1998. 

http://cfpub.epa.gov/ncea/cfm/recordisplay.cfm?deid=30759 

USEPA. 2004. Overview of the Ecological Risk Assessment Process in the Office of Pesticide 

Programs. United States Environmental Protection Agency (USEPA). Environmental Fate 

and Effects Division. Office of Pesticide Programs. Available at: 

http://www.epa.gov/espp/consultation/ecorisk-overview.pdf 
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U.S. Fish and Wildlife Service (USFWS) and National Marine Fisheries Service (NMFS). 1998. 

Endangered Species Consultation Handbook: Procedures for Conducting Consultation and 

Conference Activities Under Section 7 of the Endangered Species Act. Final Draft. March 

1998. 

9 Bibliography of Cited MRIDs 

Fate studies 

48542624 Knight, L. (2004) OK-5101 - Hydrolysis Under Laboratory Conditions. Project 

Number: OTSA/0076/US/OCR, OSK/035/032048, EU/OSK/035. Unpublished study 

prepared by Huntingdon Life Sciences, Ltd. 75p. 

48542625 Nakamura, H. (2004) (Carbon 14)OK-5101 (Phenyl-ring-U-and tolyl-ring-U-label): 

A Hydrolysis Study. Project Number: OTSA/0156/EN//FR/US/OCR, 

EU/IET/02/8006. Unpublished study prepared by Institute of Environmental 

Toxicology. 167p. 

48542626 Knight, L. (2004) OK-5101 - Photodegradation in Water and Quantum Yield of 

Direct Photodegradation in Water. Project Number: OTSA/0078/US/OCR, 

OSK/036/032551, EU/OSK/036. Unpublished study prepared by Huntingdon Life 

Sciences, Ltd. 104p. 

48542627 Ohyama, K. (2004) (Carbon 14)OK-5101 (Phenyl-ring-U-and Tolyl-ring-U-label): A 

Photolysis Study in Water. Project Number: OTSA/0157/EN//FR/US/OCR, 

EU/IET/02/8007. Unpublished study prepared by Institute of Environmental 

Toxicology. 193p. 

48542750 Noorloos, B.; Brands, C.; Stienstra, N. (2007) Photodegradation of A-(Ring-U-

(Carbon 14)) OK-5101 on Soil Surfaces. Project Number: 2007/1067406/US/OCR 

EU/477282. Unpublished study prepared by Notox B.V. 54p. 

48542751 Noorloos, B.; Brands, C.; Stienstra, N. (2007) Photodegradation of B-(Ring-U-

(Carbon 14)) OK-5101 on Soil Surfaces. Project Number: 2007/1067407/US/OCR 

EU/475932. Unpublished study prepared by Notox B.V. 56p. 

48542759 Iijima, K. (2004) OK-5101 Pure: Adsorption Study in Soil. Project Number: 

A/0044/EN//FR/US/OCR EU/IET/01/6018/11. Unpublished study prepared by 

Institute of Environmental Toxicology. 30p. 

48542760 Noorloos, B.; Stienstra, N. (2011) Adsorption of B-1 on Three Soils (Including 

Amendment No. 1). Project Number: 2011/7005177/OCR EU/475897. Unpublished 

study prepared by Notox B.V. 47p. 

48542761 Noorloos, B.; Stienstra, N. (2011) Adsorption of AB-1 on Three Soils (Including 

Amendment No. 1). Project Number: 2011/7005180/OCR EU/475919. Unpublished 

study prepared by Notox B.V. 50p. 
73 

48542762 Brands, C.; Willems, H. (2008) Adsorption of B-3 on Three Soils. Project Number: 

2008/1098894/US/OCR EU/487923. Unpublished study prepared by Notox B.V. 

47p. 

48542763 Vasques, A. (2011) Adsorption/Desorption Behavior of Cyflumetofen Metabolites 

(Carbon 14)-B1, (Carbon 14)-B3 and (Carbon 14)-A2 on Different US and European 

Soils. Project Number: 2011/1257446/US/OCR U/2119/11 EU/379627. 

Unpublished study prepared by BASF S.A.: Global Environmental and Consumer 

Safety Laboratory - GENCS. 198p. 

48542786 Singh, M.; Traversa, E. (2011) Adsorption/Desorption of AB-1 Dimer Metabolite 

(Reg. No. 5756389) of BAS 9210 I: Final Report. Project Number: 

2011/7005168/OCR 111/06/01 415935. Unpublished study prepared by BASF Crop 

Protection. 62p. 

48542764 Tan, N. (2009) Leaching of B-1 in Three Soils. Project Number: 

2009/1126720/US/OCR EU/488795. Unpublished study prepared by Notox B.V. 

36p. 

48542765 Tan, N. (2009) Leaching of B-1 in One Soil. Project Number: 

2009/1126721/US/OCR EU/490991. Unpublished study prepared by Notox B.V. 

29p. 

48542766 Brands, C. (2008) Photochemical Degradation of A-(Ring-U-(Carbon 14))OK-5101 

in Water. Project Number: OTSA/0341/FR/US/OCR EU/477293. Unpublished 

study prepared by Notox B.V. 43p. 

48542767 Brands, C. (2008) Photochemical Degradation of B-(Ring-U-(Carbon 14))OK-5101 

in Water. Project Number: OTSA/0342/FR/US/OCR EU/475943. Unpublished study 

prepared by Notox B.V. 56p. 

48542629 Willems, H. (2008) OK-5101 - Atkinson Calculation. Project Number: 

OTSA/0330/FR/US/OCR, EU/480228. Unpublished study prepared by Notox B.V. 

7p. 

48542746 Knight, L. (2007) OK-5101 - Investigations into the Identity of Aerobic Soil 

Metabolites of OK-5101. Project Number: 2007/1067405/US/OCR 

NOT0003/072339 EU/NOT0003. Unpublished study prepared by Huntingdon Life 

Sciences, Ltd. 37p. 

48542747 Willems, H. (2008) OK-5101 - Estimation of Soil DT50 and DT90 Values Using 

Degradation Data Taken from a Soil Degradation Study by Knight L. (2004) - Annex 

IIA 7.1.1. Project Number: OTSA/0431/FR/US/OCR US/488454. Unpublished 

study prepared by Notox B.V. 19p. 

48542748 Ta, C.; Strobush, A. (2011) Aerobic Soil Metabolism of (Carbon 14)-BAS 9210 I: 

Final Report. Project Number: 2011/7000200/OCR 111/13/01 US/350780. 

Unpublished study prepared by Agvise Inc., BASF Corporation and BASF SE. 318p.

48542752 Brands, C. (2011) Determination of the Aerobic Degradation Rate of B-(Ring-U-

(Carbon 14))OK-5101 in Three Soils (Including Amendment No. 1). Project 
74 

Number: 2011/7005186/OCR EU/478338. Unpublished study prepared by Notox 

B.V. 80p. 

48542753 Willems, H. (2008) OK-5101 - Estimation of Soil DT50 and DT90 Values Using 

Degradation Data Taken from a Soil Degradation Study by Brands (2008)- Annex 

llA 7.2.1. Project Number: 2008/1098893/US/OCR EU/488456. Unpublished study 

prepared by Notox B.V. 23p. 

48542754 Brands, C.; Corral, E. (2011) Determination of the Aerobic Degradation Rate of B-1 

in Three Soils (Including Amendment 1 and Amendment 2). Project Number: 

2011/7005183/OCR EU/485925. Unpublished study prepared by Notox B.V. 44p. 

48542755 Brands, C.; Corral, E. (2010) Determination of the Aerobic Degradation Rate of AB1 in Three Soils (Including Amendment No. 1). Project Number: 

2010/1224815/US/OCR EU/485926. Unpublished study prepared by Notox B.V. 

50p. 

48542756 Brands, C.; Corral, E. (2010) Determination of the Aerobic Degradation Rate of B-3 

in Three Soils (Including Amendment No. 1). Project Number: 

2010/1224816/US/OCR EU/487925. Unpublished study prepared by Notox B.V. 

46p. 

48542749 Ta, C.; Traversa, E. (2011) Anaerobic Soil Metabolism of (Carbon 14)-BAS 9210 I: 

Final Report. Project Number: 2011/7005339/OCR US/350781. Unpublished study 

prepared by BASF Corporation and Agvise Laboratories, Inc. 203p. 

48542768 Ta, C.; Traversa, E. (2011) Aerobic Aquatic Metabolism of (Carbon 14)-BAS 9210 I: 

Final Report. Project Number: 2011/7000768/OCR 111/14/01 US/395301. 

Unpublished study prepared by BASF Corporation and Agvise, Inc. 203p. 

48542769 Singh, M. (2011) BAS 9210 I (Cyflumetofen): Anaerobic Aquatic Metabolism: Final 

Report. Project Number: 2011/7001153/OCR 111/07/01 US/350777. Unpublished 

study prepared by Agvise Laboratories, Inc., and BASF Agro Research. 196p. 

48542647 Perez, S.; Miska, J.; Saha, M. (2011) Independent Laboratory Validation of BASF 

Analytical Method D1002: Determination of Cyflumetofen (BAS 9210 I) and its 

Metabolites in Soil Using LC-MS/MS: Final Report. Project Number: 

2011/7005075/OCR, 379626, ADPEN/2K11/903/379626. Unpublished study 

prepared by ADPEN Laboratories, Inc. 156p. 

48542757 Jordon, J.; Warren, R. (2011) Terrestrial Field Dissipation of Cyflumetofen (BAS 

9210 I) following Applications of BAS 9210 0I in Orchard/Vineyard and Row Crop 

Use Patterns. Project Number: 2011/7004042/OCR 111/27/02 US/350785. 

Unpublished study prepared by BASF Agricultural Research Center. 926p. 

48542828 Carter, M. (2011) Validation of BASF Analytical Method D1002: Determination of 

Cyflumetofen (BAS 9210 I) and Its Metabolites in Soil using LC-MS/MS. Project 

Number: 2011/7005073/OCR, US/ADPEN/2K11/416947. Unpublished study 

prepared by ADPEN Laboratories, Inc. 209p. 

48542829 Gordon, B. (2011) Freezer Storage Stability of Cyflumetofen (BAS 9210 I) and Its 
75 

Relevant Metabolites in Soil Samples. Project Number: 2011/7002604/OCR, 

350786. Unpublished study prepared by BASF Crop Protection. 135p. 

48542785 Bouwman, L. (2007) Bioconcentration Test in Carp with OK-5101 (Flow-through). 

Project Number: 2007/1067412/US/OCR EU/472872. Unpublished study prepared 

by Notox B.V. 61p. 

Ecological effects studies 

48542772 Teunissen, M. (2011) Acute Oral Toxicity Study in Northern Bobwhite with OK5101 (Including Amendment No. 1). Project Number: 2011/7005171/OCR 

EU/381926. Unpublished study prepared by Notox B.V. 74p. 

48542773 Gallagher, S.; Beavers, J. (2006) OK-5101: An Acute Oral Toxicity Study with the 

Mallard. Project Number: 2006/1048773/US/OCR EU/181/116. Unpublished study 

prepared by Wildlife International, Ltd. 58p. 

48542774 Zok, S. (2010) BAS 9210 I (Cyflumetofen) - Acute Toxicity in the Zebra Finch 

(Taeniopygia guttata) after Single Oral Administration (LD50). Project Number: 

2010/1009633/US/OCR 15W0510/095034 375046. Unpublished study prepared by 

BASF SE. 69p. 

48542775 Teunissen, M. (2011) 5-Day Dietary Toxicity Study in Northern Bobwhite with OK5101 (Including Amendment No. 1). Project Number: 2011/7005174/OCR 

EU/381937. Unpublished study prepared by Notox B.V. 107p. 

48542776 Gallagher, S.; Martin, K.; Beavers, J. (2006) OK-5101: A Dietary LC50 Study with 

the Mallard. Project Number: 2011/7005174/OCR EU/381937. Unpublished study 

prepared by Wildlife International, Ltd. 65p. 

48542777 Temple, D.; Beavers, J.; Martin, K. et al. (2008) OK-5101: A Reproduction Study 

with the Northern Bobwhite Quail. Project Number: 2008/1098900/US/OCR 

EU/181/118. Unpublished study prepared by Wildlife International, Ltd. 161p. 

48542778 Zok, S. (2010) BAS 9210 I (Cyflumetofen) - 1-Generation Reproduction Study on 

the Mallard Duck (Anas platyrhynchus) by Administration in the Diet. Project 

Number: 2010/1065743/US/OCR 72W0510/095026 350826. Unpublished study 

prepared by BASF SE. 351p. 

48542779 Salinas, E. (2011) BAS 9210 I (Cyflumetofen) - Acute Toxicity Study with the 

Rainbow Trout (Oncorhynchus mykiss). Project Number: 2011/1109258/US/OCR 

12F0510/09E023 365853. Unpublished study prepared by BASF SE. 45p. 

48542780 Salinas, E. (2011) BAS 9210 I (Cyflumetofen) - Acute Toxicity Study with the 

Fathead Minnow (Pimephales promelas). Project Number: 2011/1102368/US/OCR 

19F0510/09E024 375047. Unpublished study prepared by BASF SE. 47p. 

48542781 Nierzedska, E. (2011) Reg.No. 104415 (Metabolite B-1 of BAS 9210 I, 

Cyflumetofen) - Acute Toxicity for Rainbow Trout. Project Number: 
76 

2011/1123577/US/OCR 1869190 W/31/11. Unpublished study prepared by Institute 

of Industrial Organic Chemistry. 37p. 

48542782 Nierzedska, E. (2011) Reg.No. 133276 - (Metabolite A-2 of BAS 9210 I, 

Cyflumetofen) - Acute Toxicity for Rainbow Trout. Project Number: 

2011/1123576/US/OCR 382915 1/86/91/99. Unpublished study prepared by Institute 

of Industrial Organic Chemistry. 39p. 

48542783 Salinas, E. (2011) BAS 9210 I (Cyflumetofen) - Early Life-stage Toxicity Test on the 

Fathead Minnow (Pimephales promelas) in a Flow-through System. Project Number: 

2011/1109259/US/OCR 375050 50F0510/09E021. Unpublished study prepared by 

BASF SE. 84p. 

48542784 Migchielsen, M. (2011) Carp, Juvenile Growth test - 28 Days with OK-5101 (Flowthrough) (Including Amendment No. 1). Project Number: 2011/7005297/OCR 

EU/475763. Unpublished study prepared by Notox B.V. 46p. 

48542787 Migchielsen, M. (2008) Acute Toxicity Study in Daphnia magna with B-1 (Static). 

Project Number: 2008/1098912/US/OCR EU/488671. Unpublished study prepared 

by Notox B.V. 27p. 

48542788 Bouwman, L. (2009) Acute Toxicity Study in Daphnia magna with B-2 (Static). 

Project Number: 2009/1126740/US/OCR EU/488674. Unpublished study prepared 

by Notox B.V. 26p. 

48542789 Salinas, E. (2011) BAS 9210 I (Cyflumetofen) - Acute Toxicity (Immobilisation) 

Study in the Water Flea Daphnia magna STRAUS (Including Amendment No. 1). 

Project Number: 2011/7006303/OCR 50E0510/09E025 375048. Unpublished study 

prepared by BASF SE. 54p. 

48542790 Swierkot, A. (2011) Reg.No. 133276 (Metabolite A-2 of BAS 9210 I, Cyflumetofen) 

- Daphnia magna Acute Immobilization Test. Project Number: 

2011/1124105/US/OCR W/33/11 1/86/91/87. Unpublished study prepared by 

Institute of Industrial Organic Chemistry. 36 p. 

48542791 Salinas, E. (2011) BAS 9210 I (Cyflumetofen) - Daphnia magna Reproduction Test. 

Project Number: 2011/1109261/US/OCR 51E0510/09E022 375049. Unpublished 

study prepared by BASF SE. 58p. 

48542792 Bergfield, A. (2011) BAS 9210 I: Static Toxicity Test with the Green Alga, 

Pseudokirchneriella subcapitata. Project Number: 2011/7001354/OCR US/65258 

350816. Unpublished study prepared by ABC Laboratories, Inc. 65p. 

48542793 Rebstock, M. (2011) BAS 9210 I: Static Toxicity Test with the Blue-green Alga, 

Anabaena flos-aquae. Project Number: 2011/7001234/OCR 350817 65259. 

Unpublished study prepared by ABC Laboratories, Inc. 60p. 

48542794 Rebstock, M. (2011) BAS 9210 I: Static Growth Inhibition Test with the Marine 

Diatom, Skeletonema costatum. Project Number: 2011/7000375/OCR 

SUBNO/201104/05/01 65261. Unpublished study prepared by ABC Laboratories, 

Inc. 62p. 
77 

48542795 Rebstock, M. (2011) BAS 9210 I: Growth Inhibition Test with the Freshwater 

Diatom, Navicula pelliculosa. Project Number: 2011/7000374/OCR 

SUBNO/201104/03/01 65260. Unpublished study prepared by ABC Laboratories, 

Inc. 62p. 

48542796 Migchielsen, M. (2011) Fresh Water Algal Growth Inhibition Test with AB-11 

(Including Amendment No. 1). Project Number: 2011/7005237/OCR EU/488678. 

Unpublished study prepared by Notox B.V. 36p. 

48542797 Migchielsen, M. (2008) Fresh Water Algal Growth Inhibition Test with B-1. Project 

Number: 2008/1098913/US/OCR EU/488672. Unpublished study prepared by Notox 

B.V. 34p. 

48542798 Gerke, A. (2011) BAS 9210 I: Whole Sediment Acute Toxicity to the Marine 

Amphipod, Leptocheirus plumulosus. Project Number: 2011/7000699/OCR 

105/02/01 375053. Unpublished study prepared by ABC Laboratories, Inc. 68p. 

48542799 Koopmans, D. (2009) Sediment-water Chironomid Toxicity Test Using Water Spiked 

with OK-5101. Project Number: 2009/1126743/US/OCR EU/487988. Unpublished 

study prepared by Notox B.V. 59p. 

48542801 Desmares-Koopmans, M. (2009) Sediment-Water Chironomid Toxicity Test Using 

Sediment Spiked with AB-1. Project Number: 2009/1126744/OCR, 489663. 

Unpublished study prepared by Notox B.V. 52p. 

48542802 Backfisch, K.; Weltje, L. (2011) Chronic Toxicity of Reg. No. 5465430 (BAS 9210 I; 

Cyflumetofen) to the Non-Biting Midge Chironomus riparius - A Spiked Sediment 

Study. Project Number: 2010/1145507/OCR, 375052. Unpublished study prepared by 

BASF Aktiengesellschaft. 39p. 

48542803 Weltje, L.; Backfisch, K. (2011) Chronic Toxicity of Reg. No. 5756389 (AB-1 

Dimer; Metabolite of Cyflumetofen) to the Non-Biting Midge Chironomus riparius - 

A Spiked Sediment Study. Project Number: 2011/1266754/OCR, 382909. 

Unpublished study prepared by BASF SE. 44p. 

48542804 Bergfield, A. (2011) BAS 9210 I: Growth Inhibition Test with the Freshwater 

Aquatic Plant, Duckweed, Lemna gibba. Project Number: 2011/7005069/OCR, 

375041, 65262. Unpublished study prepared by ABC Laboratories, Inc. 71p. 

48542805 Geuijen, W. (2002) Acute Contact Toxicity Study in the Honeybee with OK-5101 

(Laboratory Test). Project Number: OTSA/0080/FR/OCR, 358594. Unpublished 

study prepared by Notox B.V. 23p. 

48542806 Migchielsen, M. (2008) Acute Toxicity Study in the Earthworm Eisenia fetida with 

AB-1. Project Number: 2008/1098914/OCR, 488673. Unpublished study prepared by 

Notox B.V. 25p. 

48542807 Migchielsen, M. (2008) Acute Toxicity Study in the Earthworm Eisenia fetida with 

B-1 (Combined Limit/Range-Finding Test). Project Number: 2008/1098915/OCR, 

488670. Unpublished study prepared by Notox B.V. 19p. 
78 

48542808 McCormac, A. (2009) Determination of Chronic (Sub-Lethal) Toxicity of TechnicalGrade OK-5101 to the Earthworm Eisenia fetida in an Artificial Soil Substrate. 

Project Number: 2009/1126745/OCR, NOT/09/1. Unpublished study prepared by 

Mambo-Tox, Ltd. 40p. 

48542810 Gerke, A. (2011) BAS 9210 I: Effect on New Shell Growth of the Eastern Oyster 

(Crassostrea virginica). Project Number: 2011/7005234/OCR, 350824, 65256. 

Unpublished study prepared by ABC Laboratories, Inc. 61p. 

48542811 Bergfield, A. (2011) BAS 9210 I: Acute Toxicity to the Mysid Shrimp, Americamysis 

bahia, Determined under Flow-Through Conditions. Project Number: 

2011/7005280/OCR, 65255, 350823. Unpublished study prepared by ABC 

Laboratories, Inc. 55p. 

48542812 Gerke, A. (2011) BAS 9210 I: Acute Toxicity to the Sheepshead Minnow, 

Cyprinodon variegatus, Determined under Flow-Through Conditions. Project 

Number: 2011/7005233/OCR, 65254, 350822. Unpublished study prepared by ABC 

Laboratories, Inc. 56p. 

48542824 Van-Sikkelerus, B. (2003) Acute Toxicity Study in the Earthworm Eisenia fetida

with OK-5101 (Combined Range-Finding and Limit Test). Project Number: 

OTSA/0108/OCR, 358605. Unpublished study prepared by Notox B.V. 16p. 

48542914 Geuijen, W. (2006) Acute Contact Toxicity Study in the Honeybee with OK-5101 

20% SC (Laboratory Test). Project Number: EU/472927 OTSA/0309/FR/US/OCR. 

Unpublished study prepared by Notox B.V. 21p. 

48542916 Geuijen, W. (2006) Acute Toxicity Study in the Earthworm Eisenia fetida fetida

(Sic) with OK-5101 20% SC. Project Number: OTSA/0323/FR/US/OCR EU/472938. 

Unpublished study prepared by Notox B.V. 21p. 

48542920 Migchielsen, M. (2006) 96-Hour Acute Toxicity Study in Rainbow Trout with OK5101 20% SC (Static). Project Number: OTSA/0304/FR/US/OCR EU/472894. 

Unpublished study prepared by Notox B.V. 27p. 

48542921 Migchielsen, M. (2006) Acute Toxicity Study in Daphnia magna with OK-5101 20% 

SC (Static). Project Number: OTSA/0303/FR/US/OCR EU/472905. Unpublished 

study prepared by Notox B.V. 28p. 

48542922 Migchielsen, M. (2006) Fresh Water Algal Growth Inhibition Test with OK-5101 

20% SC. Project Number: OTSA/0302/FR/US/OCR EU/472916. Unpublished study 

prepared by Notox B.V. 32p. 

48542923 Geuijen, W. (2003) Acute Oral Toxicity Study in the Honeybee with OK-5101 20 SC 

(Laboratory Test). Project Number: OTSA/0137/FR/US/OCR EU/366751. 

Unpublished study prepared by Notox B.V. 22p. 

48542924 Geuijen, W. (2004) Toxicity Study in the Parasitic Wasp Aphidius rhopalosiphi with 

OK-5101 20 SC (Laboratory Test). Project Number: OTSA/0142/US/OCR 

EU/386156. Unpublished study prepared by Notox B.V. 18p. 
79 

48542925 Geuijen, W. (2004) Dose Response Toxicity Study in the Predatory Mite 

Typhlodromus pyri with OK-5101 20 SC (Laboratory Test). Project Number: 

OTSA/0143/US/OCR EU/386167. Unpublished study prepared by Notox B.V. 20p. 

48542932 Lee, B. (2011) Cyflumetofen 20SC: Effects on the Vegetative Vigor of Non-target 

Terrestrial Plants (Tier II). Project Number: 2011/7000530/OCR 350814 65248. 

Unpublished study prepared by ABC Laboratories, Inc. 114p. 

48542933 Lee, B. (2011) Cyflumetofen 20SC: Effects on the Seedling Emergence and Growth 

of Non-target Terrestrial Plants (Tier II). Project Number: 2011/7000529/OCR 65247 

350813. Unpublished study prepared by ABC Laboratories, Inc. 125p. 
80 

Appendix A: Input and Results of Screening Imbibition Program (SIP v. 1.0) 

Assumptions:

 

SIP employs the following conservative assumptions to derive upper bound exposure estimates: 

1) The chemical concentration in drinking water is at the solubility limit in water (at 25oC). 

2) The assessed animals obtain 100% of their daily water needs through drinking water. 

3) The daily water need is equivalent to the daily water flux rate as calculated by Nagy and Peterson 

(1988). 

4) The body weight of the assessed bird is equivalent to the smallest generic bird modeled in T-REX 

(i.e., 20 g). This assumption results in the highest ratio of exposure to toxicity for the 3 assessed avian 

body weights of T-REX (i.e., 20, 100, 1000 g). 

 

Table 1. Inputs 

Parameter Value 

Chemical name cyflumetofen 

Solubility (in water at 25oC; mg/L) 0.0281 

 

Mammalian LD50 (mg/kg-bw) 2000 Non-definitive endpoint 

Mammalian test species laboratory rat 

Body weight (g) of "other" mammalian 

species 

 

Mammalian NOAEL (mg/kg-bw) 9.21 

Mammalian test species laboratory rat 

Body weight (g) of "other" mammalian 

species 

 

Avian LD50 (mg/kg-bw) 2000 NOTE: Non-definitive 

Avian test species northern bobwhite quail 

Body weight (g) of "other" avian species 

Mineau scaling factor 1.15 

 

Mallard NOAEC (mg/kg-diet) 930 

Bobwhite quail NOAEC (mg/kg-diet) 154 

NOAEC (mg/kg-diet) for other bird species 

Body weight (g) of other avian species 

NOAEC (mg/kg-diet) for 2nd other bird 

species 

Body weight (g) of 2nd other avian species 

 

 

 

 

 
81 

Table 2. Mammalian Results 

Parameter Acute Chronic 

Upper bound exposure (mg/kg-bw) 0.0048 0.0048 

Adjusted toxicity value (mg/kg-bw) 1538.3211 7.0840 

Ratio of exposure to toxicity 0.0000 0.0007 

Conclusion* 

Drinking water exposure 

alone is NOT a potential 

concern for mammals 

Drinking water exposure 

alone is NOT a potential 

concern for mammals 

 

Table 3. Avian Results 

Parameter Acute Chronic 

Upper bound exposure (mg/kg-bw) 0.0228 0.0228 

Adjusted toxicity value (mg/kg-bw) 1440.8590 16.3699 

Ratio of exposure to acute toxicity 0.0000 0.0014 

Conclusion* 

Drinking water exposure 

alone is NOT a potential 

concern for birds 

Drinking water exposure 

alone is NOT a potential 

concern for birds 

 

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

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

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

animals. 
82 

Appendix B: Input and Output of Screening Tool for Inhalation Risk (STIR v. 

1.0) 

A. Ground application 

Welcome to the EFED 

Screening Tool for Inhalation Risk 

This tool is designed to provide the risk assessor with a rapid method for determining 

the potential 

significance of the inhalation exposure route to birds and mammals in a risk 

assessment. 

 

Input 

Application and Chemical Information 

Enter Chemical Name cyflumetofen 

Enter Chemical Use all proposed uses 

Is the Application a Spray? (enter y or n) y 

If Spray What Type (enter ground or air) ground 

Enter Chemical Molecular Weight (g/mole) 447.45 

Enter Chemical Vapor Pressure (mmHg) 4.40E-08 

Enter Application Rate (lb a.i./acre) 0.2 

 

Toxicity Properties 

Bird 

Enter Lowest Bird Oral LD50 (mg/kg bw) 2000 Non-definitive endpoint 

Enter Mineau Scaling Factor 1.15 

Enter Tested Bird Weight (kg) 0.178 

Mammal 

Enter Lowest Rat Oral LD50 (mg/kg bw) 2000 Non-definitive endpoint 

Enter Lowest Rat Inhalation LC50 (mg/L) 2.65 Non-definitive endpoint 

Duration of Rat Inhalation Study (hrs) 4 

Enter Rat Weight (kg) 0.35 

 

Output 

Results Avian (0.020 kg ) 

Maximum Vapor Concentration in Air at Saturation 

(mg/m3) 1.06E-03 

Maximum 1-hour Vapor Inhalation Dose (mg/kg) 1.33E-04 

Adjusted Inhalation LD50 1.48E+01 

Ratio of Vapor Dose to Adjusted Inhalation LD50 9.01E-06

Exposure not Likely 

Significant 

Maximum Post-treatment Spray Inhalation Dose (mg/kg) 2.11E-02 

Ratio of Droplet Inhalation Dose to Adjusted Inhalation 

LD50 1.43E-03

Exposure not Likely 

Significant 
83 

 

Results Mammalian (0.015 kg ) 

Maximum Vapor Concentration in Air at Saturation 

(mg/m3) 1.06E-03 

Maximum 1-hour Vapor Inhalation Dose (mg/kg) 1.67E-04 

Adjusted Inhalation LD50 1.58E+02 

Ratio of Vapor Dose to Adjusted Inhalation LD50 1.06E-06

Exposure not Likely 

Significant 

Maximum Post-treatment Spray Inhalation Dose (mg/kg) 2.66E-02 

Ratio of Droplet Inhalation Dose to Adjusted Inhalation 

LD50 1.68E-04

Exposure not Likely 

Significant 

B. Aerial application 

Welcome to the EFED 

Screening Tool for Inhalation Risk 

This tool is designed to provide the risk assessor with a rapid method for determining 

the potential 

significance of the inhalation exposure route to birds and mammals in a risk 

assessment. 

 

Input 

Application and Chemical Information 

Enter Chemical Name cyflumetofen 

Enter Chemical Use tomato 

Is the Application a Spray? (enter y or n) y 

If Spray What Type (enter ground or air) air 

Enter Chemical Molecular Weight (g/mole) 447.45 

Enter Chemical Vapor Pressure (mmHg) 4.40E-08 

Enter Application Rate (lb a.i./acre) 0.2 

 

Toxicity Properties 

Bird 

Enter Lowest Bird Oral LD50 (mg/kg bw) 2000 Non-definitive endpoint 

Enter Mineau Scaling Factor 1.15 

Enter Tested Bird Weight (kg) 0.178 

Mammal 

Enter Lowest Rat Oral LD50 (mg/kg bw) 2000 Non-definitive endpoint 

Enter Lowest Rat Inhalation LC50 (mg/L) 2.65 Non-definitive endpoint 

Duration of Rat Inhalation Study (hrs) 4 

Enter Rat Weight (kg) 0.35 

 

Output 
84 

Results Avian (0.020 kg ) 

Maximum Vapor Concentration in Air at Saturation 

(mg/m3) 1.06E-03 

Maximum 1-hour Vapor Inhalation Dose (mg/kg) 1.33E-04 

Adjusted Inhalation LD50 1.48E+01 

Ratio of Vapor Dose to Adjusted Inhalation LD50 9.01E-06

Exposure not Likely 

Significant 

Maximum Post-treatment Spray Inhalation Dose (mg/kg) 1.92E-02 

Ratio of Droplet Inhalation Dose to Adjusted Inhalation 

LD50 1.30E-03

Exposure not Likely 

Significant 

 

Results Mammalian (0.015 kg ) 

Maximum Vapor Concentration in Air at Saturation 

(mg/m3) 1.06E-03 

Maximum 1-hour Vapor Inhalation Dose (mg/kg) 1.67E-04 

Adjusted Inhalation LD50 1.58E+02 

Ratio of Vapor Dose to Adjusted Inhalation LD50 1.06E-06

Exposure not Likely 

Significant 

Maximum Post-treatment Spray Inhalation Dose (mg/kg) 2.42E-02 

Ratio of Droplet Inhalation Dose to Adjusted Inhalation 

LD50 1.53E-04

Exposure not Likely 

Significant 
85 

Appendix C: Cyflumetofen and Its Environmental Transformation Products and Degrad

Table 2. Cyflumetofen and Its Environmental Transformation Products. A

Code Name/ Synonym 

Chemical Name, Solubility, and KOC Chemical Structure Study Type MRID 

L

Max

%A

PARENT

Cyflumetofen 

BAS 92102I OK-5101 

IUPAC: 2-methoxyethyl (RS)-2-(4-tert-butylphenyl)-2-cyano-3-oxo-3-(α,α,α-trifluoro-o-tolyl)propionate 

CAS: 2-methoxyethyl α-cyano-α-

[4-(1,1-dimethylethyl)phenyl]-βoxo-2-(trifluoromethyl) 

benzenepropanoate CAS No.: 400882-07-7 Formula: C24H24F3NO4

MW: 447.45g/molSMILES: FC(F)(F)c2ccccc2C(=O)C(C#N)(c1ccc(cc1)C(C)(C)C)C(=O)OCCOC Mobility

Water solubility: 0.0281 mg/L Koc: 173,900 L/kg 

Hydrolysis pH4 

48542625

Hydrolysis pH5 Hydrolysis pH7 Hydrolysis pH9 Aqueous photolysis 48542627 Aerobic soil NJ 

48542748

Aerobic soil CA Aerobic soil IN Aerobic soil WI Aerobic soil 1

48542752

Aerobic soil 2 Aerobic soil 3 Aerobic soil 48542745 Anaerobic soil NJ 

48542748

Anaerobic soil CA Anaerobic soil IN Anaerobic soil WI Aerobic aquatic FL 

48542768

Aerobic aquatic PA Aerobic aquatic 1 48542770

48542771

Aerobic aquatic 2 Anaerobic aquatic FL 48542769 
86 

Code Name/ Synonym 

Chemical Name, Solubility, and KOC Chemical Structure Study Type MRID 

L

Max

%A

Anaerobic aquatic PA TFD WA 

48542757

TFD NY TFD FL TFD CA 

MAJOR (>10%) TRANSFORMATION PRODUCTS 

A-1 (A label 

only)

Formula: C16H21NO3

MW: 275.35 g/molSMILES: C(C#N)(c1ccc(cc1)C(C)(C)C)C(=O)OCCOC Mobility

Water solubility: 38 mg/L Koc: 459.1 L/kg (EpiSuite estimates) 

Hydrolysis pH4 

48542625

26.

Hydrolysis pH5 10Hydrolysis pH7 14

(8 

Hydrolysis pH9 28

(1

Anaerobic soil NJ 

48542748

A 20

Anaerobic soil CA B 

Metab

Anaerobic soil IN Anaerobic soil WI 

A-2 (A label 

only)

Formula: C12H15N 

MW: 173.26 g/mol SMILES:C(C#N)(c1ccc(cc1)C(C)(C)C) Mobility

Water solubility: 34.95mg/L Koc: 1200 L/kg (EpiSuite estimates) 

Hydrolysis pH4 

48542625

14.

Hydrolysis pH5 14.Hydrolysis pH7 44.Hydrolysis pH9 15.0Aerobic soil NJ 

48542748

2.

Aerobic soil CA 

B lab

n

Aerobic soil IN Aerobic soil WI Anaerobic aquatic FL 48542769 46.Anaerobic aquatic PA 26.TFD WA 

48542757

<

TFD NY <TFD FL <TFD CA <

A-12 (A label 

only)

Formula: C11H14O2MW: 178.23 g/molSMILES:

Anaerobic soil NJ 

48542749

9.9 

Anaerobic soil CA B labAnaerobic soil IN n

NC

O

O

O

NC

O

HO
87 

Code Name/ Synonym 

Chemical Name, Solubility, and KOC Chemical Structure Study Type MRID 

L

Max

%A

C(=O)(c1ccc(cc1)C(C)(C)C)O MobilityWater solubility: 28.94 mg/L Koc: 113.7 L/kg (EpiSuite estimates) 

Anaerobic soil WI 

Aerobic aquatic FL 48542768 17Aerobic aquatic PA 4Anaerobic aquatic FL 48542769 Anaerobic aquatic PA 30.

A-18 (A label 

only)

Formula: C13

H15NO2

MW: 217.27 g/molSMILES:C(C#N)(c1ccc(cc1)C(C)(C)C)C(=O)O Mobility

Water solubility: 201.8 mg/L Koc: 139 L/kg (EpiSuite estimates)

Hydrolysis pH4 

48542625

12.

Hydrolysis pH5 8.6Hydrolysis pH7 36Hydrolysis pH9 48Aerobic aquatic 1 

48542770

4.

Aerobic aquatic 2 22

AB-1 (both 

labels)

Formula: C20

H18F3NO 

MW: 345.37 g/mol SMILES:FC(F)(F)c2ccccc2C(=O)C(C#N)(c1ccc(cc1)C(C)(C)C) Mobility

Water solubility: 0.142 mg/L Koc: 66,920 L/kg (EpiSuite estimates) 

Hydrolysis pH4 

48542625

34

Hydrolysis pH5 23.Hydrolysis pH7 44Hydrolysis pH9 45Aerobic soil NJ 

48542748

9.7

Aerobic soil CA 6.Aerobic soil IN 6.2Aerobic soil WI 11.Aerobic soil 48542745

A 8

B 7

Anaerobic soil NJ 

48542749

A 20

B 2

Anaerobic soil CA B 1Anaerobic soil IN B 1Anaerobic soil WI B 3Aerobic aquatic FL 

48542768

A 8

B 1

Aerobic aquatic PA A 3

B 7

Aerobic aquatic 1 48542770

48542771

A 6

B 

Aerobic aquatic 2 A 1

NC

O

OH

CF3

O

NC
88 

Code Name/ Synonym 

Chemical Name, Solubility, and KOC Chemical Structure Study Type MRID 

L

Max

%A

B 1

Anaerobic aquatic FL

48542769

A 34

B 26

Anaerobic aquatic PA A 38

B 3

Fate Studies Using AB

Aerobic soil 1

48542755

9

Aerobic soil 2 8Aerobic soil 3 9

AB-7 Formula: C24H24F3NO4

MW: 447.46 SMILES:C(C#N)(c1c(C(=O)c2ccccc2C(F)(F)(F))cc(cc1)C(C)(C)C)C(=O)OCCOC Mobility

Water solubility: 0.05367 mg/L Koc: 25,600 L/kg (EpiSuite estimates)

Aquatic Photolysis 48542627 10.8

AB-11 CAS No.: 400882-00-0 

Formula: C24H24F3NO3

MW: 431.5 SMILES:FC(F)(F)c2ccccc2C(=O)C(C#N)(c1ccc(cc1)C(C)(C)C)C(=O)OC(C)C Mobility

Water solubility: 0.0102 mg/L Koc: 85,630 L/kg (EpiSuite estimates) 

Aerobic aquatic 1 

48542770

Aerobic aquatic 2 A 1

CF3 O

NC

O

O

O

CF3 O

NC

O

O
89 

Code Name/ Synonym 

Chemical Name, Solubility, and KOC Chemical Structure Study Type MRID 

L

Max

%A

AB-15 Formula: C24H24F3NO4

MW: 447.46 SMILES:FC(F)(F)c2ccccc2C(=O)C(C#N)(c1c(C(=O)O)cc(cc1)C(C)(C)C)CCOCMobility

Water solubility: 0.04085 mg/L Koc: 10,400 L/kg (EpiSuite estimates)

Aquatic Photolysis 48542627 54

AB-1 Dimer Formula: C40H36F6N2O2

MW: 690.73 SMILES:C(C#N)(c1ccc(cc1)C(C)(C)C)(FC(F)(F)c2ccccc2C(=O))C(C#N)(c1ccc(cc1)C(C)(C)C)(FC(F)(F)c2ccccc2C(=O)) Mobility

Water solubility: 4.082×10-10

mg/L Koc: 1.617×108 L/kg (EpiSuite 

estimates) 

Aerobic soil NJ 

48542748

25.3

Aerobic soil CA 18.Aerobic soil IN 10.Aerobic soil WI 23.Anaerobic soil NJ 

48542748

A 1

B 1

Anaerobic soil CA B 1Anaerobic soil IN B 1Anaerobic soil WI B 1Aerobic aquatic FL 

48542768

A 5

B 3

Aerobic aquatic PA A 5

B 6

CF3

O

CN

F3C

O

NC

CF3 O

NC

O

O

OH

CF3 O

NC

O

O

OH

CF3 O

NC

O

O

OH
90 

Code Name/ Synonym 

Chemical Name, Solubility, and KOC Chemical Structure Study Type MRID 

L

Max

%A

TFD WA 

48542757

0.004 

TFD NY 0.012 TFD FL 0.003 TFD CA 0.003 

AU16 (A-1/A-1 

Dimer) (A label only)

Formula: C32

H40

N2O6

MW: 548.69g/mol SMILES:C(C#N)(c1ccc(cc1)C(C)(C)C)(C(=O)OCCOC)C(C#N)(c1ccc(cc1)C(C)(C)C)(C(=O)OCCOC) Mobility

Water solubility: 0.00722 mg/L Koc: 50,600 L/kg (EpiSuite estimates) 

Hydrolysis pH4 

48542625

6.5

Hydrolysis pH5 15.Hydrolysis pH7 5.0Hydrolysis pH9 4.Aerobic soil NJ 

48542748

A 2

Aerobic soil CA 

B labe

no

Aerobic soil IN Aerobic soil WI 

AU17 (A-1/AB1 Dimer) 

(both labels)

Formula: C36

H38F3N2O4

MW: 619.71g/mol SMILES:C(C#N)(c1ccc(cc1)C(C)(C)C)(FC(F)(F)c2ccccc2C(=O))C(C#N)(c1ccc(cc1)C(C)(C)C)(C(=O)OCCOC) Mobility

Water solubility: 1.728×10-6 mg/L

Koc: 2.86×106 L/kg (EpiSuite 

estimates) 

Hydrolysis pH4 

48542625

7.7

Hydrolysis pH5 21.Hydrolysis pH7 Hydrolysis pH9 Aerobic soil NJ 

48542748

6.9

Aerobic soil CA 8.2 Aerobic soil IN 4.7Aerobic soil WI 3.8

B-1 2-(trifluoro 

methyl) benzoic acid 

2-TFMBA (B label only)

IUPAC: o-trifluoromethylbenzoic acid CAS: 2-(trifluoromethyl)benzoic acid CAS No.: 433-97-6 Formula: CF3C6H4COOH 

MW: 190.12 g/molSMILES: OC(=O)c1ccccc1C(F)(F)F 

Hydrolysis pH4 

48542625

48

Hydrolysis pH5 52.Hydrolysis pH7 53Hydrolysis pH9 50Aerobic soil NJ 

48542748

30.

Aerobic soil CA 43.Aerobic soil IN 23Aerobic soil WI 21Aerobic soil 1

48542752

55

Aerobic soil 2 43Aerobic soil 3 52

O

O

CN

NC

O

O

O

O

CF3

O

CN

NC

O

O

O

CF3

O

OH
91 

Code Name/ Synonym 

Chemical Name, Solubility, and KOC Chemical Structure Study Type MRID 

L

Max

%A

MobilityWater solubility: 363.3 mg/L (EpiSuite estimate) Koc: 79 L/kg 

Aerobic soil 48542745 22

Anaerobic soil NJ 

48542749

49 

Anaerobic soil CA 50.Anaerobic soil IN 50.Anaerobic soil WI 44.Aerobic aquatic FL 48542768 58Aerobic aquatic PA 60Aerobic aquatic 1 48542771 56Aerobic aquatic 2 84Anaerobic aquatic FL 48542769 68.Anaerobic aquatic PA 72.TFD WA 

48542757

0.030 

TFD NY 0.056 TFD FL 0.026 TFD CA 0.079 

Fate Studies Using B-

Aerobic soil 1

48542754

1

Aerobic soil 2 1Aerobic soil 3 1

B-3 2-(trifluoro 

methyl) benzamide 

(B label only)

CAS: 2-(trifluoromethyl) benzamide CAS No.: 360-64-5 Formula: C8H6F3NO 

MW: 189.137 g/mol

SMILES: C(C1=C(C(=O)N)C=CC=C1)(F)(F)F Mobility

Water solubility: 13,000 mg/L Koc: 121.5 (EpiSuite estimate) 

Aerobic soil NJ 

48542748

4.

Aerobic soil CA 17.Aerobic soil IN 4.Aerobic soil WI 3.2Aerobic soil 1

48542752

23

Aerobic soil 2 12Aerobic soil 3 4.Anaerobic soil NJ 

48542749

B 0

Anaerobic soil CA B 2Anaerobic soil IN B 3Anaerobic soil WI B 1TFD WA 

48542757

<

TFD NY <TFD FL <

CF3

O

NH2
92 

Code Name/ Synonym 

Chemical Name, Solubility, and KOC Chemical Structure Study Type MRID 

L

Max

%A

TFD CA 0.005 

Fate Studies Using B-3 

Aerobic soil 1

48542756

8

Aerobic soil 2 8Aerobic soil 3 8

Unextracted 

residues (both labels)

(not applicable) 

(not applicable) 

Aerobic soil NJ 

48542748

B 35

A 43

Aerobic soil CA B 21Aerobic soil IN B 38Aerobic soil WI B 35Aerobic soil 1

48542752

B 3

Aerobic soil 2 B 40Aerobic soil 3 B 3Aerobic soil 48542745 A 4

B 3

Anaerobic soil NJ 

48542749

A 32

B 2

Anaerobic soil CA B Anaerobic soil IN B 2Anaerobic soil WI B 1Aerobic aquatic FL 

48542768

A 34

B 29

Aerobic aquatic PA A 4

B 23

Anaerobic aquatic FL

48542769

A 4.

B 12

Anaerobic aquatic PA A 8

B 8

Carbon dioxide Carbon dioxide 

Formula: CO2

MW: 44.1 g/molSMILES: O=C=O 

O O

Aerobic soil NJ 

48542748

B 24

A 17

Aerobic soil CA B 9Aerobic soil IN B 17Aerobic soil WI B 17Aerobic soil 1 48542752 B 9Aerobic soil 2 B 20
93 

Code Name/ Synonym 

Chemical Name, Solubility, and KOC Chemical Structure Study Type MRID 

L

Max

%A

Aerobic soil 3 B 1Aerobic soil 48542745 A 27

B 39

Anaerobic soil NJ 

48542749

A 2

B 1

Anaerobic soil CA B 0Anaerobic soil IN B 1Anaerobic soil WI B 1Aerobic aquatic FL 

48542768

A 8

B 3

Aerobic aquatic PA A 8

B 3

Aerobic aquatic 1 48542770

48542771

A 1

B 2

Aerobic aquatic 2 A 

B 3

Anaerobic aquatic FL

48542769

A 0.

B 0.

Anaerobic aquatic PA A 1.

B 0.

MINOR (<10%) TRANSFORMATION PRODUCTS

AB-12 Formula: C32H32F3NO3

MW: 535.6 SMILES: FC(F)(F)c2ccccc2C(=O)C(C#N)(c1ccc(cc1)C(C)(C)C)C(=O)OC(c1ccc(cc1)C(C)(C)C) Mobility

Water solubility: 1.074×10-5 mg/L

Koc: 7.876×106 (EpiSuite 

estimates) 

Aerobic aquatic 1 

48542770

Aerobic aquatic 2 A 

A nd means “not detected”. AR means “applied radioactivity”. MW means “molecular weight”. LOQ means “limit of quantitation”. Bolded values a>10%AR. TFD means Terrestrial Field Dissipation Study. 

CF3 O

NC

O

O
94 

1. Appendix Figure C-1 Abiotic hydrolysis. 
95 

Appendix Figure C-2. Aquatic photolysis. 
96 

Appendix Figure C-3. Aerobic soil metabolism. 

Appendix Figure C-4. Aerobic aquatic metabolism. 
97 

Appendix Figure C-5. Anaerobic aquatic metabolism. 
98 

Appendix D: Parent and Total Toxic Residue (TTR) PestDF Degradation Half-life Estimat

Available Degradate Study Half-life Estimation Output 

Appendix Table D-1. Parent and Total Toxic Residue (TTR) PestDF Degradation Half-life Estimation Output 

Parent Only Total Toxic Residue (TTR

Hydrolysis – pH 4 (MRID 48542625) Hydrolysis – pH 5 (MRID 48542625)Hydrolysis – pH 7 (MRID 48542625)
99 

Parent Only Total Toxic Residue (TTR

Hydrolysis – pH 9 (MRID 48542625)
100 

Parent Only Total Toxic Residue (TTR

Aquatic Photolysis – Distilled Water (MRID 48542627) Aquatic Photolysis – Natural Water (MRID 48542627) 
101 

Parent Only Total Toxic Residue (TTR

Soil Photolysis – A-label (MRID 48542750) Soil Photolysis – B-label (MRID 48542751) 

Not Applicable 
102 

Parent Only Total Toxic Residue (TTR

Aerobic Soil Metabolism – Sandy Loam (MRID 48542745) Aerobic Soil Metabolism – CA Soil B-label Only (MRID 48542748) 

Not Applicable 
103 

Parent Only Total Toxic Residue (TTR

Aerobic Soil Metabolism – IN Soil B-label Only (MRID 48542748) 

Not Applicable 

Aerobic Soil Metabolism – NJ Soil A- and B-label (MRID 48542748) 
104 

Parent Only Total Toxic Residue (TTR

Aerobic Soil Metabolism – WI Soil B-label Only (MRID 48542748) 

Not Applicable 

Aerobic Soil Metabolism – Speyer 2.2 Soil B-label Only (MRID 48542752) 

Not Applicable 
105 

Parent Only Total Toxic Residue (TTR

Aerobic Soil Metabolism – Speyer 2.3 Soil B-label Only (MRID 48542752) 

Not Applicable 

Aerobic Soil Metabolism – Speyer 6S Soil B-label Only (MRID 48542752) 

Not Applicable 
106 

Parent Only Total Toxic Residue (TTR

Anaerobic Soil Metabolism – CA Soil B-label Only (MRID 48542749) 

Not Applicable 

Anaerobic Soil Metabolism – IN Soil B-label Only (MRID 48542749) 

Not Applicable 
107 

Parent Only Total Toxic Residue (TTR

Anaerobic Soil Metabolism – NJ Soil A- and B-label (MRID 48542749) Anaerobic Soil Metabolism – WI Soil B-label Only (MRID 48542749) 

Not Applicable 
108 

Parent Only Total Toxic Residue (TTR

Aerobic Aquatic Metabolism – FL System A- and B-label (MRID 48542768) Aerobic Aquatic Metabolism – PA System A- and B-label (MRID 48542768) 
109 

Parent Only Total Toxic Residue (TTR

Aerobic Aquatic Metabolism – Goorven System A- and B-label (MRIDs 48542770/48542771) Aerobic Aquatic Metabolism – Schoonrewoerdsewiel System A- and B-label (MRIDs 48542770/48542771) 
110 

Parent Only Total Toxic Residue (TTR

Anaerobic Aquatic Metabolism – FL System A- and B-label (MRID 48542769) Anaerobic Aquatic Metabolism – PA System A- and B-label (MRID 48542769) 
111 

Appendix Table D-2. Available Degradate Study Half-life Estimation Output B-1 Aerobic Soil Metabolism – Speyer 2.2 (MRID 48542754) B-1 Aerobic Soil Metabolism – Speyer 2.3 (MRID 485B-1 Aerobic Soil Metabolism – Speyer 6S (MRID 48542754) AB-1 Aerobic Soil Metabolism – Speyer 2.1 (MRID 48
112 

AB-1 Aerobic Soil Metabolism – Speyer 2.2 (MRID 48542755) AB-1 Aerobic Soil Metabolism – Speyer 6S (MRID 485B-3 Aerobic Soil Metabolism – Speyer 2.2 (MRID 48542755) B-3 Aerobic Soil Metabolism – Speyer 2.3 (MRID 485
113 

B-3 Aerobic Soil Metabolism – Speyer 6S (MRID 48542755)
114 

Appendix E: Example PRZM/EXAMS Modeling Output and AgDRIFT® 

Input Data Summary 

Surface Water – Aerial PA Tomatoes 

stored as Cyflu.out 

Chemical: Cyflumetofen 

PRZM environment: PAtomatoSTD.txt modified Tueday, 29 May 2007 at 14:01:58 

EXAMS environment: pond298.exv modified Tueday, 26 August 2008 at 06:14:08 

Metfile: w14751.dvf modified Tueday, 26 August 2008 at 06:15:00 

Water segment concentrations (ppb) 

Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 

1961 2.964 1.058 0.454 0.2667 0.2435 0.1253 

1962 3.39 1.356 0.7062 0.4681 0.4407 0.3393 

1963 3.395 1.488 0.8839 0.6628 0.6261 0.5379 

1964 3.619 1.711 1.134 0.9079 0.8638 0.7529 

1965 3.806 1.899 1.301 1.074 1.045 0.9381 

1966 3.98 2.073 1.468 1.274 1.263 1.141 

1967 4.203 2.297 1.692 1.509 1.487 1.37 

1968 4.41 2.503 1.9 1.681 1.666 1.562 

1969 4.582 2.675 2.072 1.927 1.893 1.764 

1970 4.821 3.015 2.347 2.14 2.099 1.97 

1971 4.98 3.073 2.471 2.242 2.251 2.145 

1972 5.935 4.202 3 2.682 2.617 2.407 

1973 5.417 3.512 2.907 2.685 2.657 2.573 

1974 5.587 3.682 3.077 2.877 2.847 2.754 

1975 5.793 3.872 3.294 3.114 3.062 2.944 

1976 6.297 4.128 3.469 3.241 3.197 3.112 

1977 6.111 4.204 3.6 3.379 3.333 3.25 

1978 6.256 4.349 3.779 3.622 3.571 3.431 

1979 6.426 4.519 3.915 3.722 3.675 3.589 

1980 6.559 4.652 4.048 3.816 3.769 3.691 

1981 6.702 4.783 4.18 3.976 3.938 3.834 

1982 8.044 5.335 4.556 4.229 4.167 4.003 

1983 6.979 5.075 4.471 4.236 4.191 4.116 

1984 7.19 5.538 4.722 4.477 4.422 4.288 

1985 7.26 5.354 4.755 4.522 4.475 4.393 

1986 7.368 5.461 4.858 4.648 4.628 4.528 

1987 7.491 5.584 5.04 4.798 4.749 4.668 

1988 7.625 5.718 5.116 4.901 4.855 4.767 

1989 9.021 6.288 5.322 5.084 5.04 4.9 

1990 7.856 5.949 5.348 5.136 5.109 5.017 

Sorted results 

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

0.032258064516129 9.021 6.288 5.348 5.136 5.109 5.017 

0.0645161290322581 8.044 5.949 5.322 5.084 5.04 4.9 

0.0967741935483871 7.856 5.718 5.116 4.901 4.855 4.767 

0.129032258064516 7.625 5.584 5.04 4.798 4.749 4.668 
115 

0.161290322580645 7.491 5.538 4.858 4.648 4.628 4.528 

0.193548387096774 7.368 5.461 4.755 4.522 4.475 4.393 

0.225806451612903 7.26 5.354 4.722 4.477 4.422 4.288 

0.258064516129032 7.19 5.335 4.556 4.236 4.191 4.116 

0.290322580645161 6.979 5.075 4.471 4.229 4.167 4.003 

0.32258064516129 6.702 4.783 4.18 3.976 3.938 3.834 

0.354838709677419 6.559 4.652 4.048 3.816 3.769 3.691 

0.387096774193548 6.426 4.519 3.915 3.722 3.675 3.589 

0.419354838709677 6.297 4.349 3.779 3.622 3.571 3.431 

0.451612903225806 6.256 4.204 3.6 3.379 3.333 3.25 

0.483870967741936 6.111 4.202 3.469 3.241 3.197 3.112 

0.516129032258065 5.935 4.128 3.294 3.114 3.062 2.944 

0.548387096774194 5.793 3.872 3.077 2.877 2.847 2.754 

0.580645161290323 5.587 3.682 3 2.685 2.657 2.573 

0.612903225806452 5.417 3.512 2.907 2.682 2.617 2.407 

0.645161290322581 4.98 3.073 2.471 2.242 2.251 2.145 

0.67741935483871 4.821 3.015 2.347 2.14 2.099 1.97 

0.709677419354839 4.582 2.675 2.072 1.927 1.893 1.764 

0.741935483870968 4.41 2.503 1.9 1.681 1.666 1.562 

0.774193548387097 4.203 2.297 1.692 1.509 1.487 1.37 

0.806451612903226 3.98 2.073 1.468 1.274 1.263 1.141 

0.838709677419355 3.806 1.899 1.301 1.074 1.045 0.9381 

0.870967741935484 3.619 1.711 1.134 0.9079 0.8638 0.7529 

0.903225806451613 3.395 1.488 0.8839 0.6628 0.6261 0.5379 

0.935483870967742 3.39 1.356 0.7062 0.4681 0.4407 0.3393 

0.967741935483871 2.964 1.058 0.454 0.2667 0.2435 0.1253 

0.1 7.8329 5.7046 5.1084 4.8907 4.8444 4.7571 

 Average of yearly averages: 2.83035 

Inputs generated by pe5.pl - Novemeber 2006 

Data used for this run: 

Output File: Cyflu 

Metfile: w14751.dvf 

PRZM scenario: PAtomatoSTD.txt 

EXAMS environment file: pond298.exv 

Chemical Name: Cyflumetofen 

Description Variable Name Value Units Comments 

Molecular weight mwt 447.45 g/mol 

Henry's Law Const. henry atm-m^3/mol 

Vapor Pressure vapr 4.43e-8 torr 

Solubility sol 0.028 mg/L 

Kd Kd mg/L 

Koc Koc 72000 mg/L 

Photolysis half-life kdp 17.6 days Half-life 

Aerobic Aquatic Metabolism kbacw 173 days Halfife 

Anaerobic Aquatic Metabolism kbacs 6e4 days Halfife 

Aerobic Soil Metabolism asm 1096 days Halfife 

Hydrolysis: pH 7 0 days Half-life 

Method: CAM 2 integer See PRZM manual 

Incorporation Depth: DEPI cm 

Application Rate: TAPP .224 kg/ha 

Application Efficiency: APPEFF .95 fraction 

Spray Drift DRFT .305 fraction of application rate applied to pond 
116 

Application Date Date 1-6 dd/mm or dd/mmm or dd-mm or dd-mmm 

Interval 1 interval 14 days Set to 0 or delete line for single app. 

app. rate 1 apprate kg/ha 

Record 17: FILTRA 

 IPSCND 1 

 UPTKF 

Record 18: PLVKRT 

 PLDKRT 

 FEXTRC 0.5 

Flag for Index Res. Run IR EPA Pond 

Flag for runoff calc. RUNOFF none none, monthly or total(average of entire run) 

Benthic Pore Water – Aerial PA Tomatoes 

stored as Cyfluben.out 

Chemical: Cyflumetofen 

PRZM environment: PAtomatoSTD.txt modified Tueday, 29 May 2007 at 14:01:58 

EXAMS environment: pond298.exv modified Tueday, 26 August 2008 at 06:14:08 

Metfile: w14751.dvf modified Tueday, 26 August 2008 at 06:15:00 

Benthic segment concentrations (ppb) 

Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 

1961 0.1238 0.1238 0.1225 0.1202 0.1187 0.05893 

1962 0.2696 0.2696 0.2695 0.2642 0.2583 0.1907 

1963 0.3895 0.3895 0.3894 0.3791 0.3688 0.3178 

1964 0.5097 0.5095 0.5079 0.5036 0.5015 0.4526 

1965 0.614 0.6139 0.6138 0.6132 0.6126 0.5705 

1966 0.771 0.771 0.7709 0.767 0.7649 0.6918 

1967 0.905 0.905 0.9046 0.9013 0.8974 0.8381 

1968 1.027 1.027 1.027 1.025 1.024 0.9593 

1969 1.154 1.154 1.153 1.148 1.147 1.086 

1970 1.27 1.27 1.27 1.269 1.266 1.216 

1971 1.391 1.391 1.391 1.383 1.379 1.325 

1972 1.572 1.572 1.571 1.568 1.566 1.483 

1973 1.661 1.66 1.654 1.649 1.647 1.595 

1974 1.763 1.763 1.761 1.759 1.759 1.709 

1975 1.897 1.897 1.896 1.894 1.893 1.824 

1976 1.992 1.992 1.992 1.991 1.989 1.933 

1977 2.07 2.07 2.066 2.055 2.05 2.022 

1978 2.194 2.194 2.192 2.188 2.186 2.133 

1979 2.281 2.281 2.28 2.278 2.277 2.232 

1980 2.348 2.348 2.347 2.34 2.33 2.299 

1981 2.428 2.428 2.427 2.424 2.421 2.389 

1982 2.554 2.553 2.552 2.548 2.545 2.49 

1983 2.627 2.627 2.623 2.604 2.595 2.563 

1984 2.726 2.726 2.725 2.721 2.718 2.672 

1985 2.778 2.778 2.778 2.773 2.769 2.739 

1986 2.87 2.87 2.865 2.858 2.855 2.821 

1987 2.963 2.963 2.962 2.958 2.956 2.91 

1988 3.007 3.006 3.004 3 2.999 2.977 

1989 3.111 3.111 3.109 3.107 3.104 3.053 

1990 3.174 3.174 3.173 3.172 3.168 3.131 

Sorted results 

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

0.032258064516129 3.174 3.174 3.173 3.172 3.168 3.131 

0.0645161290322581 3.111 3.111 3.109 3.107 3.104 3.053 

0.0967741935483871 3.007 3.006 3.004 3 2.999 2.977 
117 

0.129032258064516 2.963 2.963 2.962 2.958 2.956 2.91 

0.161290322580645 2.87 2.87 2.865 2.858 2.855 2.821 

0.193548387096774 2.778 2.778 2.778 2.773 2.769 2.739 

0.225806451612903 2.726 2.726 2.725 2.721 2.718 2.672 

0.258064516129032 2.627 2.627 2.623 2.604 2.595 2.563 

0.290322580645161 2.554 2.553 2.552 2.548 2.545 2.49 

0.32258064516129 2.428 2.428 2.427 2.424 2.421 2.389 

0.354838709677419 2.348 2.348 2.347 2.34 2.33 2.299 

0.387096774193548 2.281 2.281 2.28 2.278 2.277 2.232 

0.419354838709677 2.194 2.194 2.192 2.188 2.186 2.133 

0.451612903225806 2.07 2.07 2.066 2.055 2.05 2.022 

0.483870967741936 1.992 1.992 1.992 1.991 1.989 1.933 

0.516129032258065 1.897 1.897 1.896 1.894 1.893 1.824 

0.548387096774194 1.763 1.763 1.761 1.759 1.759 1.709 

0.580645161290323 1.661 1.66 1.654 1.649 1.647 1.595 

0.612903225806452 1.572 1.572 1.571 1.568 1.566 1.483 

0.645161290322581 1.391 1.391 1.391 1.383 1.379 1.325 

0.67741935483871 1.27 1.27 1.27 1.269 1.266 1.216 

0.709677419354839 1.154 1.154 1.153 1.148 1.147 1.086 

0.741935483870968 1.027 1.027 1.027 1.025 1.024 0.9593 

0.774193548387097 0.905 0.905 0.9046 0.9013 0.8974 0.8381 

0.806451612903226 0.771 0.771 0.7709 0.767 0.7649 0.6918 

0.838709677419355 0.614 0.6139 0.6138 0.6132 0.6126 0.5705 

0.870967741935484 0.5097 0.5095 0.5079 0.5036 0.5015 0.4526 

0.903225806451613 0.3895 0.3895 0.3894 0.3791 0.3688 0.3178 

0.935483870967742 0.2696 0.2696 0.2695 0.2642 0.2583 0.1907 

0.967741935483871 0.1238 0.1238 0.1225 0.1202 0.1187 0.05893 

0.1 3.0026 3.0017 2.9998 2.9958 2.9947 2.9703 

 Average of yearly averages: 1.75605766666667 

Inputs generated by pe5.pl - Novemeber 2006 

Data used for this run: 

Output File: Cyflu 

Metfile: w14751.dvf 

PRZM scenario: PAtomatoSTD.txt 

EXAMS environment file: pond298.exv 

Chemical Name: Cyflumetofen 

Description Variable Name Value Units Comments 

Molecular weight mwt 447.45 g/mol 

Henry's Law Const. henry atm-m^3/mol 

Vapor Pressure vapr 4.43e-8 torr 

Solubility sol 0.028 mg/L 

Kd Kd mg/L 

Koc Koc 72000 mg/L 

Photolysis half-life kdp 17.6 days Half-life 

Aerobic Aquatic Metabolism kbacw 173 days Halfife 

Anaerobic Aquatic Metabolism kbacs 6e4 days Halfife 

Aerobic Soil Metabolism asm 1096 days Halfife 

Hydrolysis: pH 7 0 days Half-life 

Method: CAM 2 integer See PRZM manual 

Incorporation Depth: DEPI cm 

Application Rate: TAPP .224 kg/ha 

Application Efficiency: APPEFF .95 fraction 

Spray Drift DRFT .305 fraction of application rate applied to pond 

Application Date Date 1-6 dd/mm or dd/mmm or dd-mm or dd-mmm 

Interval 1 interval 14 days Set to 0 or delete line for single app. 

app. rate 1 apprate kg/ha 

Record 17: FILTRA 

 IPSCND 1 

 UPTKF 

Record 18: PLVKRT 
118 

 PLDKRT 

 FEXTRC 0.5 

Flag for Index Res. Run IR EPA Pond 

Flag for runoff calc. RUNOFF none none, monthly or total(average of entire run) 

AgDRIFT® Input Data Summary – Aerial 

AgDRIFT® Input Data Summary 

--General-- 

Tier: II 

Title: Untitled 

Notes: 

Calculations Done: Yes 

Run ID: AgDRIFT® 2.1.1 03-14-2013 11:27:08 

Default values appear when they differ from the Current values. 

--Aircraft-- ----------Current----------- ----------Default----------- 

Name Air Tractor AT-401 

Type Slow Fixed-wing 

Boom Length (%) 76.3 

Boom Height (ft) 15 10 

Flight Lines 20 

--Drop Size Distribution-- ----------Current----------- ----------Default----------- 

Name ASAE Fine to Medium 

Type Basic 

Drop Categories # Diam (um) Frac Diam (um) Frac 

 1 10.77 0.0010 

 2 16.73 0.0003 

 3 19.39 0.0007 

 4 22.49 0.0003 

 5 26.05 0.0007 

 6 30.21 0.0010 

 7 35.01 0.0010 

 8 40.57 0.0020 

 9 47.03 0.0033 

 10 54.50 0.0053 

 11 63.16 0.0067 

 12 73.23 0.0090 

 13 84.85 0.0133 

 14 98.12 0.0223 

 15 113.71 0.0330 

 16 131.73 0.0393 

 17 152.79 0.0480 

 18 177.84 0.0647 

 19 205.84 0.0830 

 20 238.45 0.1147 

 21 276.48 0.1283 

 22 320.60 0.1380 

 23 372.18 0.1127 

 24 430.74 0.0640 

 25 498.91 0.0440 

 26 578.54 0.0317 

 27 670.72 0.0203 

 28 777.39 0.0093 

 29 900.61 0.0010 

 30 1044.42 0.0007 

 31 1210.66 0.0003 
119 

--Swath-- ----------Current----------- ----------Default----------- 

Swath Width 60 ft 

Swath Displacement 0.3722 x Swath Width 

--Spray Material-- ----------Current----------- ----------Default----------- 

Nonvolatile Rate (lb/ac) 1 0.501 

Active Rate (lb/ac) 1 0.2505 

Spray Volume 

 Rate (gal/ac) 10 2 

Carrier Type Water 

--Meteorology-- ----------Current----------- ----------Default----------- 

Wind Speed (mph) 15 10 

Temperature (deg F) 86 

Relative Humidity (%) 50 

--Transport-- ----------Current----------- ----------Default----------- 

Flux Plane (ft) 0 
120 

Appendix F: Listed Species That Overlap at the County Level with Areas Where Cyflumet

To Be Used as Identified by LOCATES (v. 2.2.5) 

Based on the following crops: almonds, apples, chestnut, cironjas, citron, citrus fruit-all, grapefruit, grapes, hazel 

kumquats, lemons, lemons and limes, limes, macadamia nuts, pears-all, pears-Bartlett, pears-other, pecans-all, pe

pecans-native and seedling, tangelo, tangerine, walnuts-English 

Common Name Scientific Name Status Taxon Coqui, Golden Eleutherodactylus jasperi T AmphibiaFrog, California Red-legged Rana aurora draytonii T AmphibiaFrog, Chiricahua Leopard Rana chiricahuensis T AmphibiaFrog, Dusky Gopher (Mississippi DPS) Rana capito sevosa E AmphibiaFrog, Mountain Yellow-legged Rana muscosa E AmphibiaGuajon Eleutherodactylus cooki T AmphibiaOzark Hellbender Cryptobranchus alleganiensis bishopi E AmphibiaSalamander, Barton Springs Eurycea sosorum E AmphibiaSalamander, California Tiger Ambystoma californiense E AmphibiaSalamander, Cheat Mountain Plethodon nettingi T AmphibiaSalamander, Desert Slender Batrachoseps aridus E AmphibiaSalamander, Frosted Flatwoods Ambystoma cingulatum T AmphibiaSalamander, Red Hills Phaeognathus hubrichti T AmphibiaSalamander, Reticulated flatwoods Ambystoma bishopi E AmphibiaSalamander, San Marcos Eurycea nana T AmphibiaSalamander, Santa Cruz Long-toed Ambystoma macrodactylum croceum E AmphibiaSalamander, Shenandoah Plethodon shenandoah E AmphibiaSalamander, Sonora Tiger Ambystoma tigrinum stebbinsi E AmphibiaSalamander, Texas Blind Typhlomolge rathbuni E AmphibiaToad, Arroyo Southwestern Bufo californicus (=microscaphus) E AmphibiaToad, Houston Bufo houstonensis E AmphibiaToad, Puerto Rican Crested Peltophryne lemur T AmphibiaHarvestman, Bee Creek Cave Texella reddelli E Arachnid Harvestman, Bone Cave Texella reyesi E Arachnid 
121 

Common Name Scientific Name Status Taxon Harvestman, Cokendolpher Cave Texella cokendolpheri E Arachnid Meshweaver, Braken Bat Cave Cicurina venii E Arachnid Meshweaver, Government Canyon Bat Cave Cicurina vespera E Arachnid Meshweaver, Madla's Cave Cicurina madla E Arachnid Meshweaver, Robber Baron Cave Cicurina baronia E Arachnid Pseudoscorpion, Tooth Cave Tartarocreagris texana E Arachnid Spider, Government Canyon Bat Cave Neoleptoneta microps E Arachnid Spider, Kauai Cave Wolf Adelocosa anops E Arachnid Spider, Spruce-fir Moss Microhexura montivaga E Arachnid Spider, Tooth Cave Leptoneta myopica E Arachnid Akekee Loxops caeruleirostris E Bird 'Akepa, Hawaii Loxops coccineus coccineus E Bird 'Akepa, Maui Loxops coccineus ochraceus E Bird 'Akia Loa, Kauai (Hemignathus procerus) Hemignathus procerus E Bird 'Akia Pola'au (Hemignathus munroi) Hemignathus munroi E Bird Albatross, Short-tailed Phoebastria (=Diomedea) albatrus E Bird Blackbird, Yellow-shouldered Agelaius xanthomus E Bird Bobwhite, Masked Colinus virginianus ridgwayi E Bird Caracara, Audubon's Crested Polyborus plancus audubonii T Bird Condor, California Gymnogyps californianus E Bird Coot, Hawaiian (=Alae keo keo) Fulica americana alai E Bird Crane, Mississippi Sandhill Grus canadensis pulla E Bird Crane, Whooping Grus americana E Bird Creeper, Hawaii Oreomystis mana E Bird Creeper, Oahu (Alauwahio) Paroreomyza maculata E Bird Crow, Hawaiian ('Alala) Corvus hawaiiensis E Bird Crow, Mariana Corvus kubaryi E Bird Curlew, Eskimo Numenius borealis E Bird Duck, Hawaiian (Koloa) Anas wyvilliana E Bird Eider, Steller's Polysticta stelleri T Bird Elepaio, Oahu Chasiempis sandwichensis ibidis E Bird Falcon, Northern Aplomado Falco femoralis septentrionalis E Bird Flycatcher, Southwestern Willow Empidonax traillii extimus E Bird 
122 

Common Name Scientific Name Status Taxon Gnatcatcher, Coastal California Polioptila californica californica T Bird Goose, Hawaiian (Nene) Branta (=Nesochen) sandvicensis E Bird Hawk, Hawaiian (Io) Buteo solitarius E Bird Hawk, Puerto Rican Broad-winged Buteo platypterus brunnescens E Bird Hawk, Puerto Rican Sharp-shinned Accipiter striatus venator E Bird Honeycreeper, Crested ('Akohekohe) Palmeria dolei E Bird Kauai creeper Oreomystis bairdi E Bird Kingfisher, Guam Micronesian Halcyon cinnamomina cinnamomina E Bird Kite, Everglades Snail Rostrhamus sociabilis plumbeus E Bird Megapode, Micronesian (La Perouse's) Megapodius laperouse E Bird Moorhen, Hawaiian Common Gallinula chloropus sandvicensis E Bird Moorhen, Mariana Common Gallinula chloropus guami E Bird Murrelet, Marbled Brachyramphus marmoratus T Bird Nightjar, Puerto Rico Caprimulgus noctitherus E Bird Nuku Pu'u, Kauai Hemignathus lucidus hanapepe E Bird Nuku Pu'u, Maui Hemignathus lucidus affinus E Bird 'O'o, Kauai (='A'a) Moho braccatus E Bird 'O'u (Honeycreeper) Psittirostra psittacea E Bird Owl, Mexican Spotted Strix occidentalis lucida T Bird Owl, Northern Spotted Strix occidentalis caurina T Bird Palila Loxioides bailleui E Bird Parrot, Puerto Rican Amazona vittata E Bird Parrotbill, Maui Pseudonestor xanthophrys E Bird Petrel, Hawaiian Dark-rumped Pterodroma phaeopygia sandwichensis E Bird Pigeon, Puerto Rican Plain Columba inornata wetmorei E Bird Plover, Piping Charadrius melodus E/T Bird Plover, Western Snowy Charadrius alexandrinus nivosus T Bird Po'ouli Melamprosops phaeosoma E Bird Prairie-chicken, Attwater's Greater Tympanuchus cupido attwateri E Bird Rail, California Clapper Rallus longirostris obsoletus E Bird Rail, Guam Rallus owstoni E Bird Rail, Light-footed Clapper Rallus longirostris levipes E Bird Rail, Yuma Clapper Rallus longirostris yumanensis E Bird 
123 

Common Name Scientific Name Status Taxon Scrub-Jay, Florida Aphelocoma coerulescens T Bird Shearwater, Newell's Townsend's Puffinus auricularis newelli T Bird Shrike, San Clemente Loggerhead Lanius ludovicianus mearnsi E Bird Sparrow, Cape Sable Seaside Ammodramus maritimus mirabilis E Bird Sparrow, Florida Grasshopper Ammodramus savannarum floridanus E Bird Sparrow, San Clemente Sage Amphispiza belli clementeae T Bird Stilt, Hawaiian (=Ae'o) Himantopus mexicanus knudseni E Bird Stork, Wood Mycteria americana E Bird Swiftlet, Mariana Gray (=Vanikoro) Aerodramus vanikorensis bartschi E Bird Tern, California Least Sterna antillarum browni E Bird Tern, Interior (population) Least Sterna antillarum E Bird Tern, Roseate Sterna dougallii dougallii E/T Bird Thrush, Large Kauai Myadestes myadestinus E Bird Thrush, Small Kauai (Puaiohi) Myadestes palmeri E Bird Towhee, Inyo Brown Pipilo crissalis eremophilus T Bird Vireo, Black-capped Vireo atricapilla E Bird Vireo, Least Bell's Vireo bellii pusillus E Bird Warbler (=Wood), Golden-cheeked Dendroica chrysoparia E Bird Warbler (=Wood), Kirtland's Dendroica kirtlandii E Bird Warbler, Bachman's Vermivora bachmanii E Bird Warbler, nightingale reed (old world warbler) Acrocephalus luscinia E Bird White-eye, Bridled (Nossa) Zosterops conspicillatus conspicillatus E Bird White-eye, Rota Bridled Zosterops rotensis E Bird Woodpecker, Ivory-billed Campephilus principalis E Bird Woodpecker, Red-cockaded Picoides borealis E Bird Alabama pearlshell Margaritifera marrianae E Bivalve Bankclimber, Purple Elliptoideus sloatianus T Bivalve Choctaw Bean Villosa choctawensis E Bivalve Combshell, Southern (=Penitent mussel) Epioblasma penita E Bivalve Combshell, Upland Epioblasma metastriata E Bivalve Elktoe, Appalachian Alasmidonta raveneliana E Bivalve Fanshell Cyprogenia stegaria E Bivalve Fatmucket, Arkansas Lampsilis powelli T Bivalve 
124 

Common Name Scientific Name Status Taxon fuzzy pigtoe Pleurobema strodeanum T Bivalve Kidneyshell, Triangular Ptychobranchus greenii E Bivalve Mucket, Orange-nacre Lampsilis perovalis T Bivalve Mucket, Pink (Pearlymussel) Lampsilis abrupta E Bivalve Mussel, Acornshell Southern Epioblasma othcaloogensis E Bivalve Mussel, Alabama Moccasinshell Medionidus acutissimus T Bivalve Mussel, Black (=Curtus' Mussel) Clubshell Pleurobema curtum E Bivalve Mussel, Clubshell Pleurobema clava E Bivalve Mussel, Coosa Moccasinshell Medionidus parvulus E Bivalve Mussel, Cumberland Combshell Epioblasma brevidens E Bivalve Mussel, Cumberland Elktoe Alasmidonta atropurpurea E Bivalve Mussel, Cumberland Pigtoe Pleurobema gibberum E Bivalve Mussel, Dark Pigtoe Pleurobema furvum E Bivalve Mussel, Dwarf Wedge Alasmidonta heterodon E Bivalve Mussel, Fat Threeridge Amblema neislerii E Bivalve Mussel, Fine-lined Pocketbook Lampsilis altilis T Bivalve Mussel, Fine-rayed Pigtoe Fusconaia cuneolus E Bivalve Mussel, Flat Pigtoe (=Marshall's Mussel) Pleurobema marshalli E Bivalve Mussel, Georgia pigtoe Pleurobema hanleyianum E Bivalve Mussel, Gulf Moccasinshell Medionidus penicillatus E Bivalve Mussel, Heavy Pigtoe (=Judge Tait's Mussel) Pleurobema taitianum E Bivalve Mussel, Heelsplitter Carolina Lasmigona decorata E Bivalve Mussel, Heelsplitter Inflated Potamilus inflatus T Bivalve Mussel, Ochlockonee Moccasinshell Medionidus simpsonianus E Bivalve Mussel, Oval Pigtoe Pleurobema pyriforme E Bivalve Mussel, Ovate Clubshell Pleurobema perovatum E Bivalve Mussel, Oyster Epioblasma capsaeformis E Bivalve Mussel, Ring Pink (=Golf Stick Pearly) Obovaria retusa E Bivalve Mussel, Rough Pigtoe Pleurobema plenum E Bivalve Mussel, Scaleshell Leptodea leptodon E Bivalve Mussel, Shiny Pigtoe Fusconaia cor E Bivalve Mussel, Shiny-rayed Pocketbook Lampsilis subangulata E Bivalve Mussel, snuffbox Epioblasma triquetra E Bivalve 
125 

Common Name Scientific Name Status Taxon Mussel, Southern Clubshell Pleurobema decisum E Bivalve Mussel, Southern Pigtoe Pleurobema georgianum E Bivalve Mussel, Speckled Pocketbook Lampsilis streckeri E Bivalve Mussel, Winged Mapleleaf Quadrula fragosa E Bivalve Narrow Pigtoe Fusconaia escambia T Bivalve Pearlshell, Louisiana Margaritifera hembeli T Bivalve Pearlymussel, Alabama Lamp Lampsilis virescens E Bivalve Pearlymussel, Appalachian Monkeyface Quadrula sparsa E Bivalve Pearlymussel, Birdwing Lemiox rimosus E Bivalve Pearlymussel, Cracking Hemistena lata E Bivalve Pearlymussel, Cumberland Bean Villosa trabalis E Bivalve Pearlymussel, Cumberland Monkeyface Quadrula intermedia E Bivalve Pearlymussel, Curtis' Epioblasma florentina curtisii E Bivalve Pearlymussel, Dromedary Dromus dromas E Bivalve Pearlymussel, Fat Pocketbook Potamilus capax E Bivalve Pearlymussel, Green-blossom Epioblasma torulosa gubernaculum E Bivalve Pearlymussel, Higgins' Eye Lampsilis higginsii E Bivalve Pearlymussel, Little-wing Pegias fabula E Bivalve Pearlymussel, Orange-footed Plethobasus cooperianus E Bivalve Pearlymussel, Pale Lilliput Toxolasma cylindrellus E Bivalve Pearlymussel, Purple Cat's Paw Epioblasma obliquata obliquata E Bivalve Pearlymussel, Tubercled-blossom Epioblasma torulosa torulosa E Bivalve Pearlymussel, Turgid-blossom Epioblasma turgidula E Bivalve Pearlymussel, White Cat's Paw Epioblasma obliquata perobliqua E Bivalve Pearlymussel, White Wartyback Plethobasus cicatricosus E Bivalve Pearlymussel, Yellow-blossom Epioblasma florentina florentina E Bivalve Purple Bean Villosa perpurpurea E Bivalve Rabbitsfoot, Rough Quadrula cylindrica strigillata E Bivalve Rayed Bean Villosa fabalis E Bivalve Riffleshell, Northern Epioblasma torulosa rangiana E Bivalve Riffleshell, Tan Epioblasma florentina walkeri (=E. walkeri) E Bivalve Rock-pocketbook, Ouachita (=Wheeler's pm) Arkansia wheeleri E Bivalve Round Ebonyshell Fusconaia rotulata E Bivalve 
126 

Common Name Scientific Name Status Taxon Sheepnose mussel Plethobasus cyphyus E Bivalve Slabshell, Chipola Elliptio chipolaensis T Bivalve Southern Kidneyshell Ptychobranchus jonesi E Bivalve Southern Sandshell Hamiota australis T Bivalve Spectaclecase mussel Cumberlandia monodonta E Bivalve Spinymussel, Altamaha Elliptio spinosa E Bivalve Spinymussel, James River Pleurobema collina E Bivalve Spinymussel, Tar River Elliptio steinstansana E Bivalve Stirrupshell Quadrula stapes E Bivalve Tapered Pigtoe Fusconaia burkei T Bivalve Cypress, Gowen Cupressus goveniana ssp. goveniana T Conf/cycdCypress, Santa Cruz Cupressus abramsiana E Conf/cycdTorreya, Florida Torreya taxifolia E Conf/cycdCoral, Elkhorn Acropora palmata T Coral Coral, Staghorn Acropora cervicornis T Coral Amphipod, Illinois Cave Gammarus acherondytes E Crustacean Amphipod, Kauai Cave Spelaeorchestia koloana E Crustacean Amphipod, Noel's Gammarus desperatus E Crustacean Amphipod, Peck's Cave Stygobromus (=Stygonectes) pecki E Crustacean Crayfish, Cave (Cambarus aculabrum) Cambarus aculabrum E Crustacean Crayfish, Cave (Cambarus zophonastes) Cambarus zophonastes E Crustacean Crayfish, Nashville Orconectes shoupi E Crustacean Crayfish, Shasta Pacifastacus fortis E Crustacean Fairy Shrimp, Conservancy Fairy Branchinecta conservatio E Crustacean Fairy Shrimp, Longhorn Branchinecta longiantenna E Crustacean Fairy Shrimp, Riverside Streptocephalus woottoni E Crustacean Fairy Shrimp, San Diego Branchinecta sandiegonensis E Crustacean Fairy Shrimp, Vernal Pool Branchinecta lynchi T Crustacean Isopod, Lee County Cave Lirceus usdagalun E Crustacean Isopod, Madison Cave Antrolana lira T Crustacean Isopod, Socorro Thermosphaeroma thermophilus E Crustacean Shrimp, Alabama Cave Palaemonias alabamae E Crustacean Shrimp, California Freshwater Syncaris pacifica E Crustacean 
127 

Common Name Scientific Name Status Taxon Shrimp, Kentucky Cave Palaemonias ganteri E Crustacean Shrimp, Squirrel Chimney Cave Palaemonetes cummingi T Crustacean Tadpole Shrimp, Vernal Pool Lepidurus packardi E Crustacean (ncn) Cyanea kolekoleensis E Dicot (ncn) Keysseria (=Lagenifera) erici E Dicot (ncn) Keysseria (=Lagenifera) helenae E Dicot (ncn) Lysimachia iniki E Dicot (ncn) Lysimachia pendens E Dicot (ncn) Lysimachia scopulensis E Dicot (ncn) Lysimachia venosa E Dicot (ncn) Phyllostegia hispida E Dicot (ncn) Phyllostegia renovans E Dicot (ncn) Platydesma cornuta var. cornuta E Dicot (ncn) Platydesma cornuta var. decurrens E Dicot (ncn) Schiedea attenuata E Dicot (ncn) Stenogyne kealiae E Dicot (ncn) Tetraplasandra bisattenuata E Dicot (ncn) Tetraplasandra flynnii E Dicot (ncn) Tetraplasandra lydgatei E Dicot Abutilon sandwicense (ncn) Abutilon sandwicense E Dicot Achyranthes mutica (ncn) Achyranthes mutica E Dicot Achyranthes splendens var. rotundata (ncn) Achyranthes splendens var. rotundata E Dicot Adobe Sunburst, San Joaquin Pseudobahia peirsonii T Dicot a'e Zanthoxylum oahuense E Dicot A'e (Zanthoxylum dipetalum var. tomentosum) Zanthoxylum dipetalum var. tomentosum E Dicot A'e (Zanthoxylum hawaiiense) Zanthoxylum hawaiiense E Dicot 'Aiea (Nothocestrum breviflorum) Nothocestrum breviflorum E Dicot 'Aiea (Nothocestrum peltatum) Nothocestrum peltatum E Dicot Akoko Chamaesyce remyi var. kauaiensis E Dicot 'akoko Chamaesyce eleanoriae E Dicot 'Akoko (Chamaesyce celastroides var. kaenana) Chamaesyce celastroides var. kaenana E Dicot 'Akoko (Chamaesyce deppeana) Chamaesyce deppeana E Dicot 'Akoko (Chamaesyce herbstii) Chamaesyce herbstii E Dicot 
128 

Common Name Scientific Name Status Taxon 'Akoko (Chamaesyce kuwaleana) Chamaesyce kuwaleana E Dicot 'Akoko (Chamaesyce rockii) Chamaesyce rockii E Dicot 'Akoko (Chamaesyce skottsbergii var. skottsbe Chamaesyce skottsbergii var. kalaeloana E Dicot 'Akoko (Euphorbia haeleeleana) Euphorbia haeleeleana E Dicot alani Melicope christophersenii E Dicot alani Melicope degeneri E Dicot alani Melicope hiiakae E Dicot alani Melicope makahae E Dicot alani Melicope paniculata E Dicot alani Melicope puberula E Dicot Alani (Melicope adscendens) Melicope adscendens E Dicot Alani (Melicope balloui) Melicope balloui E Dicot Alani (Melicope haupuensis) Melicope haupuensis E Dicot Alani (Melicope knudsenii) Melicope knudsenii E Dicot Alani (Melicope lydgatei) Melicope lydgatei E Dicot Alani (Melicope mucronulata) Melicope mucronulata E Dicot Alani (Melicope ovalis) Melicope ovalis E Dicot Alani (Melicope pallida) Melicope pallida E Dicot Alani (Melicope quadrangularis) Melicope quadrangularis E Dicot Alani (Melicope saint-johnii) Melicope saint-johnii E Dicot Alani (Melicope zahlbruckneri) Melicope zahlbruckneri E Dicot Allocarya, Calistoga Plagiobothrys strictus E Dicot Alsinidendron obovatum (ncn) Alsinidendron obovatum E Dicot Alsinidendron trinerve (ncn) Alsinidendron trinerve E Dicot Alsinidendron viscosum (ncn) Alsinidendron viscosum E Dicot Amaranth, Seabeach Amaranthus pumilus T Dicot Ambrosia, San Diego Ambrosia pumila E Dicot Ambrosia, South Texas Ambrosia cheiranthifolia E Dicot Amphianthus, Little Amphianthus pusillus T Dicot 'Anaunau (Lepidium arbuscula) Lepidium arbuscula E Dicot 'Anunu (Sicyos alba) Sicyos alba E Dicot Aster, Decurrent False Boltonia decurrens T Dicot Aster, Florida Golden Chrysopsis floridana E Dicot 
129 

Common Name Scientific Name Status Taxon Aster, Ruth's Golden Pityopsis ruthii E Dicot Auerodendron pauciflorum (ncn) Auerodendron pauciflorum E Dicot Aupaka (Isodendrion hosakae) Isodendrion hosakae E Dicot Aupaka (Isodendrion laurifolium) Isodendrion laurifolium E Dicot Aupaka (Isodendrion longifolium) Isodendrion longifolium T Dicot Avens, Spreading Geum radiatum E Dicot awikiwiki Canavalia napaliensis E Dicot 'Awiwi (Centaurium sebaeoides) Centaurium sebaeoides E Dicot 'Awiwi (Hedyotis cookiana) Hedyotis cookiana E Dicot Ayenia, Texas Ayenia limitaris E Dicot Baccharis, Encinitas Baccharis vanessae T Dicot Barbara Buttons, Mohr's Marshallia mohrii T Dicot Barberry, Island Berberis pinnata ssp. insularis E Dicot Barberry, Nevin's Berberis nevinii E Dicot Bariaco Trichilia triacantha E Dicot Bearclaw poppy, Dwarf Arctomecon humilis E Dicot Bedstraw, El Dorado Galium californicum ssp. sierrae E Dicot Bedstraw, Island Galium buxifolium E Dicot Bellflower, Brooksville Campanula robinsiae E Dicot Birch, Virginia Round-leaf Betula uber T Dicot Bird's-beak, Palmate-bracted Cordylanthus palmatus E Dicot Bird's-beak, Pennell's Cordylanthus tenuis ssp. capillaris E Dicot Bird's-beak, salt marsh Cordylanthus maritimus ssp. maritimus E Dicot Bird's-beak, Soft Cordylanthus mollis ssp. mollis E Dicot Birds-in-a-nest, White Macbridea alba T Dicot Bittercress, Small-anthered Cardamine micranthera E Dicot Bladderpod, Dudley Bluffs Lesquerella congesta T Dicot Bladderpod, Kodachrome Lesquerella tumulosa E Dicot Bladderpod, Lyrate Lesquerella lyrata T Dicot Bladderpod, Missouri Lesquerella filiformis T Dicot Bladderpod, San Bernardino Mountains Lesquerella kingii ssp. bernardina E Dicot Bladderpod, Spring Creek Lesquerella perforata E Dicot Bladderpod, White Lesquerella pallida E Dicot 
130 

Common Name Scientific Name Status Taxon Bladderpod, Zapata Lesquerella thamnophila E Dicot Blazing Star, Ash Meadows Mentzelia leucophylla T Dicot Blazing Star, Heller's Liatris helleri T Dicot Blazing Star, Scrub Liatris ohlingerae E Dicot Bluecurls, Hidden Lake Trichostema austromontanum ssp. compactum T Dicot Blue-star, Kearney's Amsonia kearneyana E Dicot Bluet, Roan Mountain Hedyotis purpurea var. montana E Dicot Bonamia menziesii (ncn) Bonamia menziesii E Dicot Bonamia, Florida Bonamia grandiflora T Dicot Boxwood, Vahl's Buxus vahlii E Dicot Broom, San Clemente Island Lotus dendroideus ssp. traskiae E Dicot Buckwheat, Cushenbury Eriogonum ovalifolium var. vineum E Dicot Buckwheat, Ione (incl. Irish Hill) Eriogonum apricum (incl. var. prostratum) E Dicot Buckwheat, Scrub Eriogonum longifolium var. gnaphalifolium T Dicot Buckwheat, Southern Mountain Wild Eriogonum kennedyi var. austromontanum T Dicot Buckwheat, Steamboat Eriogonum ovalifolium var. williamsiae E Dicot Bush-mallow, San Clemente Island Malacothamnus clementinus E Dicot Bush-mallow, Santa Cruz Island Malacothamnus fasciculatus var. nesioticus E Dicot Buttercup, Autumn Ranunculus aestivalis (=acriformis) E Dicot Butterfly Plant, Colorado Gaura neomexicana var. coloradensis T Dicot Butterweed, Layne's Senecio layneae T Dicot Butterwort, Godfrey's Pinguicula ionantha T Dicot Button-celery, San Diego Eryngium aristulatum var. parishii E Dicot Cactus, Arizona Hedgehog Echinocereus triglochidiatus var. arizonicus E Dicot Cactus, Bakersfield Opuntia treleasei E Dicot Cactus, Black Lace Echinocereus reichenbachii var. albertii E Dicot Cactus, Brady Pincushion Pediocactus bradyi E Dicot Cactus, Bunched Cory Coryphantha ramillosa T Dicot Cactus, Chisos Mountain Hedgehog Echinocereus chisoensis var. chisoensis T Dicot Cactus, Cochise Pincushion Coryphantha robbinsorum T Dicot Cactus, Colorado hookless Sclerocactus glaucus T Dicot Cactus, Knowlton Pediocactus knowltonii E Dicot Cactus, Kuenzler Hedgehog Echinocereus fendleri var. kuenzleri E Dicot Cactus, Lee Pincushion Coryphantha sneedii var. leei T Dicot 
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Common Name Scientific Name Status Taxon Cactus, Lloyd's Mariposa Echinomastus mariposensis T Dicot Cactus, Mesa Verde Sclerocactus mesae-verdae T Dicot Cactus, Nellie Cory Coryphantha minima E Dicot Cactus, Nichol's Turk's Head Echinocactus horizonthalonius var. nicholii E Dicot Cactus, Pariette Sclerocactus brevispinus T Dicot Cactus, Peebles Navajo Pediocactus peeblesianus peeblesianus E Dicot Cactus, Pima Pineapple Coryphantha scheeri var. robustispina E Dicot Cactus, San Rafael Pediocactus despainii E Dicot Cactus, Siler Pincushion Pediocactus (=Echinocactus,=Utahia) sileri T Dicot Cactus, Sneed Pincushion Coryphantha sneedii var. sneedii E Dicot Cactus, Star Astrophytum asterias E Dicot Cactus, Tobusch Fishhook Ancistrocactus tobuschii E Dicot Cactus, Uinta Basin hookless Sclerocactus wetlandicus T Dicot Cactus, Winkler Pediocactus winkleri T Dicot Cactus, Wright Fishhook Sclerocactus wrightiae E Dicot Calyptranthes Thomasiana (ncn) Calyptranthes thomasiana E Dicot Campion, Fringed Silene polypetala E Dicot Capa Rosa Callicarpa ampla E Dicot Catchfly, Spalding's Silene spaldingii T Dicot Catesbaea Melanocarpa (ncn) Catesbaea melanocarpa E Dicot Cat's-eye, Terlingua Creek Cryptantha crassipes E Dicot Ceanothus, Coyote Ceanothus ferrisae E Dicot Ceanothus, Pine Hill Ceanothus roderickii E Dicot Ceanothus, Vail Lake Ceanothus ophiochilus T Dicot Centaury, Spring-loving Centaurium namophilum T Dicot Chaffseed, American Schwalbea americana E Dicot Chamaecrista glandulosa (ncn) Chamaecrista glandulosa var. mirabilis E Dicot Chamaesyce Halemanui (ncn) Chamaesyce halemanui E Dicot Checker-mallow, Keck's Sidalcea keckii E Dicot Checker-mallow, Kenwood Marsh Sidalcea oregana ssp. valida E Dicot Checker-mallow, Nelson's Sidalcea nelsoniana T Dicot Checker-mallow, Pedate Sidalcea pedata E Dicot Checker-mallow, Wenatchee Mountains Sidalcea oregana var. calva E Dicot 
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Common Name Scientific Name Status Taxon Chumbo, Higo Harrisia portoricensis T Dicot Chupacallos Pleodendron macranthum E Dicot Clarkia, Pismo Clarkia speciosa ssp. immaculata E Dicot Clarkia, Presidio Clarkia franciscana E Dicot Clarkia, Springville Clarkia springvillensis T Dicot Clarkia, Vine Hill Clarkia imbricata E Dicot Cliffrose, Arizona Purshia (=cowania) subintegra E Dicot Clover, Fleshy Owl's Castilleja campestris ssp. succulenta T Dicot Clover, Leafy Prairie Dalea foliosa E Dicot Clover, Monterey Trifolium trichocalyx E Dicot Clover, Prairie Bush Lespedeza leptostachya T Dicot Clover, Running Buffalo Trifolium stoloniferum E Dicot Clover, Showy Indian Trifolium amoenum E Dicot Cobana Negra Stahlia monosperma T Dicot Coneflower, Smooth Echinacea laevigata E Dicot Cordia bellonis (ncn) Cordia bellonis E Dicot Coyote-thistle, Loch Lomond Eryngium constancei E Dicot Crownbeard, Big-leaved Verbesina dissita T Dicot Crownscale, San Jacinto Valley Atriplex coronata var. notatior E Dicot Cyanea undulata (ncn) Cyanea undulata E Dicot Cycladenia, Jones Cycladenia jonesii (=humilis) T Dicot Daisy, Lakeside Hymenoxys herbacea T Dicot Daisy, Parish's Erigeron parishii T Dicot Daisy, Willamette Erigeron decumbens var. decumbens E Dicot Daphnopsis hellerana (ncn) Daphnopsis hellerana E Dicot Dawn-flower, Texas Prairie (=Texas Bitterweed) Hymenoxys texana E Dicot DeBeque phacelia Phacelia submutica T Dicot Delissea rhytodisperma (ncn) Delissea rhytidosperma E Dicot Dogweed, Ashy Thymophylla tephroleuca E Dicot Dropwort, Canby's Oxypolis canbyi E Dicot Dubautia latifolia (ncn) Dubautia latifolia E Dicot Dubautia pauciflorula (ncn) Dubautia pauciflorula E Dicot Dudleya, Conejo Dudleya abramsii ssp. parva T Dicot 
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Common Name Scientific Name Status Taxon Dudleya, Marcescent Dudleya cymosa ssp. marcescens T Dicot Dudleya, Santa Clara Valley Dudleya setchellii E Dicot Dudleya, Santa Cruz Island Dudleya nesiotica T Dicot Dudleya, Santa Monica Mountains Dudleya cymosa ssp. ovatifolia T Dicot Dudleya, Verity's Dudleya verityi T Dicot Dwarf-flax, Marin Hesperolinon congestum T Dicot Erubia Solanum drymophilum E Dicot Eugenia Woodburyana Eugenia woodburyana E Dicot Evening-primrose, Antioch Dunes Oenothera deltoides ssp. howellii E Dicot Evening-primrose, Eureka Valley Oenothera avita ssp. eurekensis E Dicot Evening-primrose, San Benito Camissonia benitensis T Dicot Fiddleneck, Large-flowered Amsinckia grandiflora E Dicot Flannelbush, Mexican Fremontodendron mexicanum E Dicot Flannelbush, Pine Hill Fremontodendron californicum ssp. decumbens E Dicot Fleabane, Zuni Erigeron rhizomatus T Dicot Four-o'clock, Macfarlane's Mirabilis macfarlanei T Dicot Frankenia, Johnston's Frankenia johnstonii E Dicot Fringe Tree, Pygmy Chionanthus pygmaeus E Dicot Fringepod, Santa Cruz Island Thysanocarpus conchuliferus E Dicot Fruit, Earth (=geocarpon) Geocarpon minimum T Dicot Geranium, Hawaiian Red-flowered Geranium arboreum E Dicot Gerardia, Sandplain Agalinis acuta E Dicot Gesneria pauciflora (ncn) Gesneria pauciflora T Dicot Gilia, Hoffmann's Slender-flowered Gilia tenuiflora ssp. hoffmannii E Dicot Gilia, Monterey Gilia tenuiflora ssp. arenaria E Dicot Goetzea, Beautiful (Matabuey) Goetzea elegans E Dicot Golden Sunburst, Hartweg's Pseudobahia bahiifolia E Dicot Goldenrod, Blue Ridge Solidago spithamaea T Dicot Goldenrod, Houghton's Solidago houghtonii T Dicot Goldenrod, Short's Solidago shortii E Dicot Goldenrod, White-haired Solidago albopilosa T Dicot Goldfields, Burke's Lasthenia burkei E Dicot Goldfields, Contra Costa Lasthenia conjugens E Dicot 
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Common Name Scientific Name Status Taxon Gooseberry, Miccosukee Ribes echinellum T Dicot Gouania hillebrandii (ncn) Gouania hillebrandii E Dicot Gouania meyenii (ncn) Gouania meyenii E Dicot Gouania vitifolia (ncn) Gouania vitifolia E Dicot Gourd, Okeechobee Cucurbita okeechobeensis ssp. okeechobeensis E Dicot Grass, Hairy Orcutt Orcuttia pilosa E Dicot Grass, Sacramento Orcutt Orcuttia viscida E Dicot Grass, Slender Orcutt Orcuttia tenuis T Dicot Ground-plum, Guthrie's Astragalus bibullatus E Dicot Groundsel, San Francisco Peaks Senecio franciscanus T Dicot Gumplant, Ash Meadows Grindelia fraxino-pratensis T Dicot ha`iwale Cyrtandra kaulantha E Dicot ha`iwale Cyrtandra sessilis E Dicot Haha Cyanea calycina E Dicot Haha Cyanea dolichopoda E Dicot haha Cyanea eleeleensis E Dicot Haha Cyanea kuhihewa E Dicot Haha Cyanea lanceolata E Dicot haha Cyanea purpurellifolia E Dicot Haha (Cyanea acuminata) Cyanea acuminata E Dicot Haha (Cyanea asarifolia) Cyanea asarifolia E Dicot Haha (Cyanea copelandii ssp. copelandii) Cyanea copelandii ssp. copelandii E Dicot Haha (Cyanea copelandii ssp. haleakalaensis) Cyanea copelandii ssp. haleakalaensis E Dicot Haha (Cyanea Crispa) (=Rollandia crispa) Cyanea (=Rollandia) crispa E Dicot Haha (Cyanea glabra) Cyanea glabra E Dicot Haha (Cyanea grimesiana ssp. grimesiana) Cyanea grimesiana ssp. grimesiana E Dicot Haha (Cyanea grimesiana ssp. obatae) Cyanea grimesiana ssp. obatae E Dicot Haha (Cyanea hamatiflora ssp. carlsonii) Cyanea hamatiflora ssp. Carlsonii E Dicot Haha (Cyanea hamatiflora ssp. hamatiflora) Cyanea hamatiflora ssp. hamatiflora E Dicot Haha (Cyanea humboldtiana) Cyanea humboldtiana E Dicot Haha (Cyanea koolauensis) Cyanea koolauensis E Dicot Haha (Cyanea lobata) Cyanea lobata E Dicot Haha (Cyanea longiflora) Cyanea longiflora E Dicot 
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Common Name Scientific Name Status Taxon Haha (Cyanea mceldowneyi) Cyanea mceldowneyi E Dicot Haha (Cyanea pinnatifida) Cyanea pinnatifida E Dicot Haha (Cyanea platyphylla) Cyanea platyphylla E Dicot Haha (Cyanea recta) Cyanea recta T Dicot Haha (Cyanea remyi) Cyanea remyi E Dicot Haha (Cyanea shipmanii) Cyanea shipmannii E Dicot Haha (Cyanea stictophylla) Cyanea stictophylla E Dicot Haha (Cyanea St-Johnii) (=Rollandia St-Johnii) Cyanea st-johnii E Dicot Haha (Cyanea superba) Cyanea superba E Dicot Haha (Cyanea truncata) Cyanea truncata E Dicot haiwale Cyrtandra gracilis E Dicot haiwale Cyrtandra paliku E Dicot haiwale Cyrtandra waiolani E Dicot Ha'Iwale (Cyrtandra crenata) Cyrtandra crenata E Dicot Ha'Iwale (Cyrtandra dentata) Cyrtandra dentata E Dicot Ha'Iwale (Cyrtandra giffardii) Cyrtandra giffardii E Dicot Ha'Iwale (Cyrtandra limahuliensis) Cyrtandra limahuliensis T Dicot Ha'Iwale (Cyrtandra munroi) Cyrtandra munroi E Dicot Ha'iwale (Cyrtandra oenobarba) Cyrtandra oenobarba E Dicot Ha'Iwale (Cyrtandra polyantha) Cyrtandra polyantha E Dicot Ha'Iwale (Cyrtandra subumbellata) Cyrtandra subumbellata E Dicot Ha'Iwale (Cyrtandra tintinnabula) Cyrtandra tintinnabula E Dicot Ha'Iwale (Cyrtandra viridiflora) Cyrtandra viridiflora E Dicot Haplostachys Haplostachya (ncn) Haplostachys haplostachya E Dicot Harebells, Avon Park Crotalaria avonensis E Dicot Harperella Ptilimnium nodosum E Dicot Hau Kauhiwi (Hibiscadelphus woodi) Hibiscadelphus woodii E Dicot Hau Kuahiwi (Hibiscadelphus distans) Hibiscadelphus distans E Dicot Hau Kuahiwi (Hibiscadelphus giffardianus) Hibiscadelphus giffardianus E Dicot Hau Kuahiwi (Hibiscadelphus hualalaiensis) Hibiscadelphus hualalaiensis E Dicot Hayun Lagu (Tronkon Guafi) Serianthes nelsonii E Dicot Heartleaf, Dwarf-flowered Hexastylis naniflora T Dicot Heather, Mountain Golden Hudsonia montana T Dicot 
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Common Name Scientific Name Status Taxon Heau (Exocarpos luteolus) Exocarpos luteolus E Dicot Hedyotis degeneri (ncn) Hedyotis degeneri E Dicot Hedyotis parvula (ncn) Hedyotis parvula E Dicot Hedyotis St.-Johnii (ncn) Hedyotis st.-johnii E Dicot Hesperomannia arborescens (ncn) Hesperomannia arborescens E Dicot Hesperomannia arbuscula (ncn) Hesperomannia arbuscula E Dicot Hesperomannia lydgatei (ncn) Hesperomannia lydgatei E Dicot Hibiscus, Clay's Hibiscus clayi E Dicot Higuero De Sierra Crescentia portoricensis E Dicot ho'awa Pittosporum napaliense E Dicot Holei (Ochrosia kilaueaensis) Ochrosia kilaueaensis E Dicot Holly, Cook's Ilex cookii E Dicot Howellia, Water Howellia aquatilis T Dicot Hypericum, Highlands Scrub Hypericum cumulicola E Dicot Ilex sintenisii (ncn) Ilex sintenisii E Dicot Iliau (Wilkesia hobdyi) Wilkesia hobdyi E Dicot Ipomopsis, Holy Ghost Ipomopsis sancti-spiritus E Dicot Ivesia, Ash Meadows Ivesia kingii var. eremica T Dicot Jacquemontia, Beach Jacquemontia reclinata E Dicot Jewelflower, California Caulanthus californicus E Dicot Jewelflower, Metcalf Canyon Streptanthus albidus ssp. albidus E Dicot Jewelflower, Tiburon Streptanthus niger E Dicot Joint-vetch, Sensitive Aeschynomene virginica T Dicot kamakahala Labordia helleri E Dicot kamakahala Labordia pumila E Dicot Kamakahala (Labordia cyrtandrae) Labordia cyrtandrae E Dicot Kamakahala (Labordia lydgatei) Labordia lydgatei E Dicot Kamakahala (Labordia tinifolia var. wahiawaen) Labordia tinifolia var. wahiawaensis E Dicot Kauila (Colubrina oppositifolia) Colubrina oppositifolia E Dicot kaulu Pteralyxia macrocarpa E Dicot Kaulu (Pteralyxia kauaiensis) Pteralyxia kauaiensis E Dicot Kio'Ele (Hedyotis coriacea) Hedyotis coriacea E Dicot Kiponapona (Phyllostegia racemosa) Phyllostegia racemosa E Dicot 
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Common Name Scientific Name Status Taxon ko`oko`olau Bidens amplectens E Dicot Koki'o (Kokia drynarioides) Kokia drynarioides E Dicot Koki'o (Kokia kauaiensis) Kokia kauaiensis E Dicot Koki'o Ke'oke'o (Hibiscus waimeae ssp. hannerae) Hibiscus waimeae ssp. hannerae E Dicot Kolea Myrsine knudsenii E Dicot kolea Myrsine mezii E Dicot Kolea (Myrsine juddii) Myrsine juddii E Dicot Kolea (Myrsine linearifolia) Myrsine linearifolia T Dicot Ko'oko'olau (Bidens micrantha ssp. kalealaha) Bidens micrantha ssp. kalealaha E Dicot Ko'oloa'ula (Abutilon menziesii) Abutilon menziesii E Dicot kopiko Psychotria grandiflora E Dicot kopiko Psychotria hobdyi E Dicot Kuawawaenohu (Alsinidendron lychnoides) Alsinidendron lychnoides E Dicot Kulu'I (Nototrichium humile) Nototrichium humile E Dicot Larkspur, Baker's Delphinium bakeri E Dicot Larkspur, San Clemente Island Delphinium variegatum ssp. kinkiense E Dicot Larkspur, Yellow Delphinium luteum E Dicot Laukahi Kuahiwi (Plantago hawaiensis) Plantago hawaiensis E Dicot Laukahi Kuahiwi (Plantago princeps) Plantago princeps E Dicot Laulihilihi (Schiedea stellarioides) Schiedea stellarioides E Dicot Layia, Beach Layia carnosa E Dicot Lead-plant, Crenulate Amorpha crenulata E Dicot Leather-flower, Alabama Clematis socialis E Dicot Leather-flower, Morefield's Clematis morefieldii E Dicot lehua makanoe Lysimachia daphnoides E Dicot Lessingia, San Francisco Lessingia germanorum (=L.g. var. germanorum) E Dicot Liliwai (Acaena exigua) Acaena exigua E Dicot Lipochaeta venosa (ncn) Lipochaeta venosa E Dicot Liveforever, Laguna Beach Dudleya stolonifera T Dicot Liveforever, Santa Barbara Island Dudleya traskiae E Dicot Lobelia monostachya (ncn) Lobelia monostachya E Dicot Lobelia niihauensis (ncn) Lobelia niihauensis E Dicot Lobelia oahuensis (ncn) Lobelia oahuensis E Dicot 
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Common Name Scientific Name Status Taxon Locoweed, Fassett's Oxytropis campestris var. chartacea T Dicot Lomatium, Bradshaw's Lomatium bradshawii E Dicot Lomatium, Cook's Lomatium cookii E Dicot Loosestrife, Rough-leaved Lysimachia asperulaefolia E Dicot Lousewort, Furbish Pedicularis furbishiae E Dicot Lupine, Clover Lupinus tidestromii E Dicot Lupine, Kincaid's Lupinus sulphureus (=oreganus) ssp. kincaidii (=var. kincaidii) T Dicot Lupine, Nipomo Mesa Lupinus nipomensis E Dicot Lupine, Scrub Lupinus aridorum E Dicot Lyonia truncata var. proctorii (ncn) Lyonia truncata var. proctorii E Dicot Lysimachia filifolia (ncn) Lysimachia filifolia E Dicot Lysimachia lydgatei (ncn) Lysimachia lydgatei E Dicot Mahoe (Alectryon macrococcus) Alectryon macrococcus E Dicot Makou (Peucedanum sandwicense) Peucedanum sandwicense T Dicot Malacothrix, Island Malacothrix squalida E Dicot Malacothrix, Santa Cruz Island Malacothrix indecora E Dicot Mallow, Kern Eremalche kernensis E Dicot Mallow, Peter's Mountain Iliamna corei E Dicot Manioc, Walker's Manihot walkerae E Dicot Manzanita, Del Mar Arctostaphylos glandulosa ssp. crassifolia E Dicot Manzanita, Ione Arctostaphylos myrtifolia T Dicot Manzanita, Morro Arctostaphylos morroensis T Dicot Manzanita, Pallid Arctostaphylos pallida T Dicot Manzanita, Santa Rosa Island Arctostaphylos confertiflora E Dicot Ma'o Hau Hele (Hibiscus brackenridgei) Hibiscus brackenridgei E Dicot Ma'oli'oli (Schiedea apokremnos) Schiedea apokremnos E Dicot Ma'oli'oli (Schiedea kealiae) Schiedea kealiae E Dicot Mapele (Cyrtandra cyaneoides) Cyrtandra cyaneoides E Dicot Meadowfoam, Butte County Limnanthes floccosa ssp. californica E Dicot Meadowfoam, Large-flowered Woolly Limnanthes floccosa ssp. Grandiflora E Dicot Meadowfoam, Sebastopol Limnanthes vinculans E Dicot Meadowrue, Cooley's Thalictrum cooleyi E Dicot 
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Common Name Scientific Name Status Taxon Mehamehame (Flueggea neowawraea) Flueggea neowawraea E Dicot Milkpea, Small's Galactia smallii E Dicot Milk-vetch, Applegate's Astragalus applegatei E Dicot Milk-vetch, Ash Meadows Astragalus phoenix T Dicot Milk-vetch, Braunton's Astragalus brauntonii E Dicot Milk-vetch, Clara Hunt's Astragalus clarianus E Dicot Milk-vetch, Coachella Valley Astragalus lentiginosus var. coachellae E Dicot Milk-vetch, Coastal Dunes Astragalus tener var. titi E Dicot Milk-vetch, Cushenbury Astragalus albens E Dicot Milk-vetch, Deseret Astragalus desereticus T Dicot Milk-vetch, Fish Slough Astragalus lentiginosus var. piscinensis T Dicot Milk-vetch, Heliotrope Astragalus montii T Dicot Milk-vetch, Holmgren Astragalus holmgreniorum E Dicot Milk-vetch, Jesup's Astragalus robbinsii var. jesupi E Dicot Milk-vetch, Lane Mountain Astragalus jaegerianus E Dicot Milk-vetch, Mancos Astragalus humillimus E Dicot Milk-vetch, Pierson's Astragalus magdalenae var. peirsonii T Dicot Milk-vetch, Sentry Astragalus cremnophylax var. cremnophylax E Dicot Milk-vetch, Shivwits Astragalus ampullarioides E Dicot Milk-vetch, Triple-ribbed Astragalus tricarinatus E Dicot Milk-vetch, Ventura Marsh Astragalus pycnostachyus var. lanosissimus E Dicot Milkweed, Mead's Asclepias meadii T Dicot Milkweed, Welsh's Asclepias welshii T Dicot Mint, Garrett's Dicerandra christmanii E Dicot Mint, Lakela's Dicerandra immaculata E Dicot Mint, Longspurred Dicerandra cornutissima E Dicot Mint, Otay Mesa Pogogyne nudiuscula E Dicot Mint, San Diego Mesa Pogogyne abramsii E Dicot Mint, Scrub Dicerandra frutescens E Dicot Mitracarpus Maxwelliae Mitracarpus maxwelliae E Dicot Mitracarpus Polycladus Mitracarpus polycladus E Dicot Monardella, Willowy Monardella linoides ssp. viminea E Dicot Monkey-flower, Michigan Mimulus glabratus var. michiganensis E Dicot 
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Common Name Scientific Name Status Taxon Monkshood, Northern Wild Aconitum noveboracense T Dicot Morning-glory, Stebbins Calystegia stebbinsii E Dicot Mountainbalm, Indian Knob Eriodictyon altissimum E Dicot Mountain-mahogany, Catalina Island Cercocarpus traskiae E Dicot Munroidendron racemosum (ncn) Munroidendron racemosum E Dicot Mustard, Carter's Warea carteri E Dicot Mustard, Slender-petaled Thelypodium stenopetalum E Dicot Myrcia Paganii Myrcia paganii E Dicot na`ena`e Dubautia imbricata imbricata E Dicot na`ena`e Dubautia plantaginea magnifolia E Dicot Na`ena`e Dubautia waialealae E Dicot Naenae Dubautia kalalauensis E Dicot Naenae Dubautia kenwoodii E Dicot Na'ena'e (Dubautia herbstobatae) Dubautia herbstobatae E Dicot Na'ena'e (Dubautia plantaginea ssp. humilis) Dubautia plantaginea ssp. humilis E Dicot Nani Wai'ale'ale (Viola kauaensis var. wahiawaensis) Viola kauaiensis var. wahiawaensis E Dicot Nanu (Gardenia mannii) Gardenia mannii E Dicot Na'u (Gardenia brighamii) Gardenia brighamii E Dicot Naupaka, Dwarf (Scaevola coriacea) Scaevola coriacea E Dicot Navarretia, Few-flowered Navarretia leucocephala ssp. Pauciflora E Dicot Navarretia, Many-flowered Navarretia leucocephala ssp. plieantha E Dicot Navarretia, Spreading Navarretia fossalis T Dicot Nehe (Lipochaeta fauriei) Lipochaeta fauriei E Dicot Nehe (Lipochaeta kamolensis) Lipochaeta kamolensis E Dicot Nehe (Lipochaeta lobata var. leptophylla) Lipochaeta lobata var. leptophylla E Dicot Nehe (Lipochaeta micrantha) Lipochaeta micrantha E Dicot Nehe (Lipochaeta tenuifolia) Lipochaeta tenuifolia E Dicot Nehe (Lipochaeta waimeaensis) Lipochaeta waimeaensis E Dicot Neraudia angulata (ncn) Neraudia angulata E Dicot Neraudia ovata (ncn) Neraudia ovata E Dicot Neraudia sericea (ncn) Neraudia sericea E Dicot Nioi (Eugenia koolauensis) Eugenia koolauensis E Dicot Niterwort, Amargosa Nitrophila mohavensis E Dicot 
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Common Name Scientific Name Status Taxon nohoanu Geranium kauaiense E Dicot Nohoanu (Geranium multiflorum) Geranium multiflorum E Dicot Oahu wild coffee Psychotria hexandra ssp. Oahuensis E Dicot Oak, Hinckley Quercus hinckleyi T Dicot 'Oha (Delissea rivularis) Delissea rivularis E Dicot 'Oha (Delissea subcordata) Delissea subcordata E Dicot 'Oha (Delissea undulata) Delissea undulata E Dicot 'Oha (Lobelia gaudichaudii koolauensis) Lobelia gaudichaudii ssp. koolauensis E Dicot 'Oha Wai (Clermontia drepanomorpha) Clermontia drepanomorpha E Dicot 'Oha Wai (Clermontia lindseyana) Clermontia lindseyana E Dicot 'Oha Wai (Clermontia oblongifolia ssp. mauiensis) Clermontia oblongifolia ssp. mauiensis E Dicot 'Oha Wai (Clermontia peleana) Clermontia peleana E Dicot 'Oha Wai (Clermontia pyrularia) Clermontia pyrularia E Dicot 'Oha Wai (Clermontia samuelii) Clermontia samuelii E Dicot 'Ohai (Sesbania tomentosa) Sesbania tomentosa E Dicot 'Ohe'ohe (Tetraplasandra gymnocarpa) Tetraplasandra gymnocarpa E Dicot 'Olulu (Brighamia insignis) Brighamia insignis E Dicot Opuhe (Urera kaalae) Urera kaalae E Dicot Oxytheca, Cushenbury Oxytheca parishii var. goodmaniana E Dicot Pagosa Skyrocket Ipomopsis polyantha E Dicot Paintbrush, Ash-grey Indian Castilleja cinerea T Dicot Paintbrush, Golden Castilleja levisecta T Dicot Paintbrush, San Clemente Island Indian Castilleja grisea E Dicot Paintbrush, Soft-leaved Castilleja mollis E Dicot Paintbrush, Tiburon Castilleja affinis ssp. neglecta E Dicot Palo Colorado (Ternstroemia luquillensis) Ternstroemia luquillensis E Dicot Palo de Jazmin Styrax portoricensis E Dicot Palo de Nigua Cornutia obovata E Dicot Palo de Ramon Banara vanderbiltii E Dicot Palo de Rosa Ottoschulzia rhodoxylon E Dicot Pamakani (Viola chamissoniana ssp. chamissoniana) Viola chamissoniana ssp. chamissoniana E Dicot Papala Charpentiera densiflora E Dicot Parachute Beardtongue Penstemon debilis T Dicot 
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Common Name Scientific Name Status Taxon Pawpaw, Beautiful Deeringothamnus pulchellus E Dicot Pawpaw, Four-petal Asimina tetramera E Dicot Pawpaw, Rugel's Deeringothamnus rugelii E Dicot Penny-cress, Kneeland Prairie Thlaspi californicum E Dicot Pennyroyal, Todsen's Hedeoma todsenii E Dicot Penstemon, Blowout Penstemon haydenii E Dicot Pentachaeta, Lyon's Pentachaeta lyonii E Dicot Pentachaeta, White-rayed Pentachaeta bellidiflora E Dicot Peperomia, Wheeler's Peperomia wheeleri E Dicot Peppergrass, Slick Spot Lepidium papilliferum T Dicot Phacelia, Clay Phacelia argillacea E Dicot Phacelia, Island Phacelia insularis ssp. insularis E Dicot Phacelia, North Park Phacelia formosula E Dicot Phlox, Texas Trailing Phlox nivalis ssp. texensis E Dicot Phlox, Yreka Phlox hirsuta E Dicot Phyllostegia hirsuta (ncn) Phyllostegia hirsuta E Dicot Phyllostegia kaalaensis (ncn) Phyllostegia kaalaensis E Dicot Phyllostegia knudsenii (ncn) Phyllostegia knudsenii E Dicot Phyllostegia mannii (ncn) Phyllostegia mannii E Dicot Phyllostegia mollis (ncn) Phyllostegia mollis E Dicot Phyllostegia parviflora (ncn) Phyllostegia parviflora E Dicot Phyllostegia velutina (ncn) Phyllostegia velutina E Dicot Phyllostegia waimeae (ncn) Phyllostegia waimeae E Dicot Phyllostegia warshaueri (ncn) Phyllostegia warshaueri E Dicot Phyllostegia wawrana (ncn) Phyllostegia wawrana E Dicot Pilo (Hedyotis mannii) Hedyotis mannii E Dicot pilo kea lau li`i Platydesma rostrata E Dicot Pinkroot, Gentian Spigelia gentianoides E Dicot Pitaya, Davis' Green Echinocereus viridiflorus var. davisii E Dicot Pitcher-plant, Alabama Canebrake Sarracenia rubra alabamensis E Dicot Pitcher-plant, Green Sarracenia oreophila E Dicot Pitcher-plant, Mountain Sweet Sarracenia rubra ssp. jonesii E Dicot Plum, Scrub Prunus geniculata E Dicot 
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Common Name Scientific Name Status Taxon Po'e (Portulaca sclerocarpa) Portulaca sclerocarpa E Dicot Polygala, Lewton's Polygala lewtonii E Dicot Polygala, Tiny Polygala smallii E Dicot Polygonum, Scott's Valley Polygonum hickmanii E Dicot Pondberry Lindera melissifolia E Dicot Poolfish, Pahrump (= Pahrump Killifish) Empetrichthys latos E Dicot Popcornflower, Rough Plagiobothrys hirtus E Dicot Popolo 'Aiakeakua (Solanum sandwicense) Solanum sandwicense E Dicot Popolo Ku Mai (Solanum incompletum) Solanum incompletum E Dicot Poppy, Sacramento Prickly Argemone pleiacantha ssp. pinnatisecta E Dicot Poppy-mallow, Texas Callirhoe scabriuscula E Dicot Potato-bean, Price's Apios priceana T Dicot Potentilla, Hickman's Potentilla hickmanii E Dicot Prickly-apple, Fragrant Cereus eriophorus var. fragrans E Dicot Prickly-ash, St. Thomas Zanthoxylum thomasianum E Dicot Primrose, Maguire Primula maguirei T Dicot Pua'ala (Brighamia rockii) Brighamia rockii E Dicot Pussypaws, Mariposa Calyptridium pulchellum T Dicot Rattleweed, Hairy Baptisia arachnifera E Dicot Reed-mustard, Barneby Schoenocrambe barnebyi E Dicot Reed-mustard, Clay Schoenocrambe argillacea T Dicot Reed-mustard, Shrubby Schoenocrambe suffrutescens E Dicot Remya kauaiensis (ncn) Remya kauaiensis E Dicot Remya montgomeryi (ncn) Remya montgomeryi E Dicot Remya, Maui Remya mauiensis E Dicot Rhododendron, Chapman Rhododendron chapmanii E Dicot Ridge-cress (=Pepper-cress), Barneby Lepidium barnebyanum E Dicot Rock-cress, Braun's Arabis perstellata E. L. Braun var. ampla Rollins E Dicot Rock-cress, Hoffmann's Arabis hoffmannii E Dicot Rock-cress, McDonald's Arabis mcdonaldiana E Dicot Rock-cress, Santa Cruz Island Sibara filifolia E Dicot Rock-cress, Shale Barren Arabis serotina E Dicot Rock-cress, Small Arabis perstellata E. L. Braun var. perstellata Fernald E Dicot 
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Common Name Scientific Name Status Taxon Rosemary, Apalachicola Conradina glabra E Dicot Rosemary, Cumberland Conradina verticillata T Dicot Rosemary, Etonia Conradina etonia E Dicot Rosemary, Short-leaved Conradina brevifolia E Dicot Roseroot, Leedy's Sedum integrifolium ssp. leedyi T Dicot Rush-pea, Slender Hoffmannseggia tenella E Dicot Rush-rose, Island Helianthemum greenei T Dicot Sandalwood, Lanai (='Iliahi) Santalum freycinetianum var. lanaiense E Dicot Sandlace Polygonella myriophylla E Dicot Sand-verbena, Large-fruited Abronia macrocarpa E Dicot Sandwort, Bear Valley Arenaria ursina T Dicot Sandwort, Cumberland Arenaria cumberlandensis E Dicot Sandwort, Marsh Arenaria paludicola E Dicot Sanicula mariversa (ncn) Sanicula mariversa E Dicot Sanicula purpurea (ncn) Sanicula purpurea E Dicot Schiedea haleakalensis (ncn) Schiedea haleakalensis E Dicot Schiedea helleri (ncn) Schiedea helleri E Dicot Schiedea hookeri (ncn) Schiedea hookeri E Dicot Schiedea kaalae (ncn) Schiedea kaalae E Dicot Schiedea kauaiensis (ncn) Schiedea kauaiensis E Dicot Schiedea membranacea (ncn) Schiedea membranacea E Dicot Schiedea nuttallii (ncn) Schiedea nuttallii E Dicot Schiedea spergulina var. leiopoda (ncn) Schiedea spergulina var. leiopoda E Dicot Schiedea spergulina var. spergulina (ncn) Schiedea spergulina var. spergulina T Dicot Schiedea, Diamond Head (Schiedea adamantis) Schiedea adamantis E Dicot Schoepfia arenaria (ncn) Schoepfia arenaria T Dicot Sea-blite, California Suaeda californica E Dicot Silene hawaiiensis (ncn) Silene hawaiiensis T Dicot Silene lanceolata (ncn) Silene lanceolata E Dicot Silene perlmanii (ncn) Silene perlmanii E Dicot Silversword, Haleakala ('Ahinahina) Argyroxiphium sandwicense ssp. macrocephalum T Dicot Silversword, Ka'u (Argyroxiphium kauense) Argyroxiphium kauense E Dicot Silversword, Mauna Kea ('Ahinahina) Argyroxiphium sandwicense ssp. sandwicense E Dicot 
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Common Name Scientific Name Status Taxon Skullcap, Florida Scutellaria floridana T Dicot Skullcap, Large-flowered Scutellaria montana T Dicot Snakeroot Eryngium cuneifolium E Dicot Sneezeweed, Virginia Helenium virginicum T Dicot Snowbells, Texas Styrax texanus E Dicot Spermolepis hawaiiensis (ncn) Spermolepis hawaiiensis E Dicot Spineflower, Ben Lomond Chorizanthe pungens var. hartwegiana E Dicot Spineflower, Howell's Chorizanthe howellii E Dicot Spineflower, Monterey Chorizanthe pungens var. pungens T Dicot Spineflower, Orcutt's Chorizanthe orcuttiana E Dicot Spineflower, Robust Chorizanthe robusta va r. robusta E Dicot Spineflower, Scotts Valley Chorizanthe robusta var. hartwegii E Dicot Spineflower, Slender-horned Dodecahema leptoceras E Dicot Spineflower, Sonoma Chorizanthe valida E Dicot Spiraea, Virginia Spiraea virginiana T Dicot Spurge, Deltoid Chamaesyce deltoidea ssp. deltoidea E Dicot Spurge, Garber's Chamaesyce garberi T Dicot Spurge, Hoover's Chamaesyce hooveri T Dicot Spurge, Telephus Euphorbia telephioides T Dicot Stenogyne angustifolia (ncn) Stenogyne angustifolia var. angustifolia E Dicot Stenogyne campanulata (ncn) Stenogyne campanulata E Dicot Stenogyne kanehoana (ncn) Stenogyne kanehoana E Dicot Stickseed, Showy Hackelia venusta E Dicot Stickyseed, Baker's Blennosperma bakeri E Dicot Stonecrop, Lake County Parvisedum leiocarpum E Dicot Sumac, Michaux's Rhus michauxii E Dicot Sunflower, Pecos Helianthus paradoxus T Dicot Sunflower, San Mateo Woolly Eriophyllum latilobum E Dicot Sunflower, Schweinitz's Helianthus schweinitzii E Dicot Sunray, Ash Meadows Enceliopsis nudicaulis var. corrugata T Dicot Taraxacum, California Taraxacum californicum E Dicot Tarplant, Gaviota Deinandra increscens ssp. villosa E Dicot Tarplant, Otay Deinandra (=Hemizonia) conjugens T Dicot 
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Common Name Scientific Name Status Taxon Tarplant, Santa Cruz Holocarpha macradenia T Dicot Ternstroemia subsessilis (ncn) Ternstroemia subsessilis E Dicot Tetramolopium arenarium (ncn) Tetramolopium arenarium E Dicot Tetramolopium capillare (ncn) Tetramolopium capillare E Dicot Tetramolopium filiforme (ncn) Tetramolopium filiforme E Dicot Tetramolopium lepidotum ssp. lepidotum (ncn) Tetramolopium lepidotum ssp. lepidotum E Dicot Tetramolopium remyi (ncn) Tetramolopium remyi E Dicot Tetramolopium rockii (ncn) Tetramolopium rockii T Dicot Thelypody, Howell's Spectacular Thelypodium howellii spectabilis T Dicot Thistle, Chorro creek Bog Cirsium fontinale var. obispoense E Dicot Thistle, Fountain Cirsium fontinale var. fontinale E Dicot Thistle, La Graciosa Cirsium loncholepis E Dicot Thistle, Pitcher's Cirsium pitcheri T Dicot Thistle, Sacramento Mountains Cirsium vinaceum T Dicot Thistle, Suisun Cirsium hydrophilum var. hydrophilum E Dicot Thornmint, San Diego Acanthomintha ilicifolia T Dicot Thornmint, San Mateo Acanthomintha obovata ssp. duttonii E Dicot Townsendia, Last Chance Townsendia aprica T Dicot Trematolobelia singularis (ncn) Trematolobelia singularis E Dicot Tuctoria, Green's Tuctoria greenei E Dicot Twinpod, Dudley Bluffs Physaria obcordata T Dicot Uhiuhi (Caesalpinia kavaiensis) Caesalpinia kavaiense E Dicot Umbel, Huachuca Water Lilaeopsis schaffneriana var. recurva E Dicot Uvillo Eugenia haematocarpa E Dicot Vernonia Proctorii (ncn) Vernonia proctorii E Dicot Vervain, California Verbena californica T Dicot Vetch, Hawaiian (Vicia menziesii) Vicia menziesii E Dicot Vigna o-wahuensis (ncn) Vigna o-wahuensis E Dicot Viola helenae (ncn) Viola helenae E Dicot Viola oahuensis (ncn) Viola oahuensis E Dicot Wahine Noho Kula (Isodendrion pyrifolium) Isodendrion pyrifolium E Dicot Wallflower, Ben Lomond Erysimum teretifolium E Dicot Wallflower, Contra Costa Erysimum capitatum var. angustatum E Dicot 
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Common Name Scientific Name Status Taxon Wallflower, Menzie's Erysimum menziesii E Dicot Warea, Wide-leaf Warea amplexifolia E Dicot Watercress, Gambel's Rorippa gambellii E Dicot Water-willow, Cooley's Justicia cooleyi E Dicot Whitlow-wort, Papery Paronychia chartacea T Dicot Wild-buckwheat, Clay-loving Eriogonum pelinophilum E Dicot Wild-buckwheat, Gypsum Eriogonum gypsophilum T Dicot Wings, Pigeon Clitoria fragrans T Dicot Wireweed Polygonella basiramia E Dicot Woodland-star, San Clemente Island Lithophragma maximum E Dicot Woolly-star, Santa Ana River Eriastrum densifolium ssp. sanctorum E Dicot Woolly-threads, San Joaquin Monolopia (=Lembertia) congdonii E Dicot Xylosma crenatum (ncn) Xylosma crenatum E Dicot Yellowhead, Desert Yermo xanthocephalus T Dicot Yerba Santa, Lompoc Eriodictyon capitatum E Dicot Ziziphus, Florida Ziziphus celata E Dicot (ncn) Diellia mannii E Ferns (ncn) Doryopteris angelica E Ferns (ncn) Doryopteris takeuchii E Ferns Asplenium fragile var. insulare (ncn) Asplenium fragile var. insulare E Ferns aumakua, Palapalai Dryopteris crinalis podosorus E Ferns Diellia erecta (ncn) Diellia erecta E Ferns Diellia falcata (ncn) Diellia falcata E Ferns Diellia pallida (ncn) Diellia pallida E Ferns Diellia unisora (ncn) Diellia unisora E Ferns Diplazium molokaiense (ncn) Diplazium molokaiense E Ferns Fern, Adiantum vivesii Adiantum vivesii E Ferns Fern, Alabama Streak-sorus Thelypteris pilosa var. alabamensis T Ferns Fern, American hart's-tongue Asplenium scolopendrium var. americanum T Ferns Fern, Elaphoglossum serpens Elaphoglossum serpens E Ferns Fern, Pendant Kihi (Adenophorus periens) Adenophorus periens E Ferns Fern, Thelypteris inabonensis Thelypteris inabonensis E Ferns Fern, Thelypteris verecunda Thelypteris verecunda E Ferns 
148 

Common Name Scientific Name Status Taxon Fern, Thelypteris yaucoensis Thelypteris yaucoensis E Ferns 'Ihi'Ihi (Marsilea villosa) Marsilea villosa E Ferns Pauoa (Ctenitis squamigera) Ctenitis squamigera E Ferns Polystichum calderonense (ncn) Polystichum calderonense E Ferns Pteris lidgatei (ncn) Pteris lidgatei E Ferns Quillwort, Black-spored Isoetes melanospora E Ferns Quillwort, Louisiana Isoetes louisianensis E Ferns Quillwort, Mat-forming Isoetes tegetiformans E Ferns Tectaria Estremerana Tectaria estremerana E Ferns Tree Fern, Elfin Cyathea dryopteroides E Ferns Wawae'Iole (Phlegmariurus (=Huperzia) mannii) Huperzia mannii E Ferns Wawae'Iole (Phlegmariurus (=Lycopodium) nutans) Lycopodium (=Phlegmariurus) nutans E Ferns Catfish, Yaqui Ictalurus pricei T Fish Cavefish, Alabama Speoplatyrhinus poulsoni E Fish Cavefish, Ozark Amblyopsis rosae T Fish Chub, Bonytail Gila elegans E Fish Chub, Chihuahua Gila nigrescens T Fish Chub, Gila Gila intermedia E Fish Chub, Humpback Gila cypha E Fish Chub, Hutton Tui Gila bicolor ssp. T Fish Chub, Mohave Tui Gila bicolor mohavensis E Fish Chub, Oregon Oregonichthys crameri E Fish Chub, Owens Tui Gila bicolor snyderi E Fish Chub, Pahranagat Roundtail Gila robusta jordani E Fish Chub, Slender Erimystax cahni T Fish Chub, Sonora Gila ditaenia T Fish Chub, Spotfin Erimonax monachus T Fish Chub, Virgin River Gila seminuda (=robusta) E Fish Chub, Yaqui Gila purpurea E Fish Chucky Madtom Noturus crypticus E Fish Cui-ui Chasmistes cujus E Fish Cumberland darter Etheostoma susanae E Fish Dace, Ash Meadows Speckled Rhinichthys osculus nevadensis E Fish 
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Common Name Scientific Name Status Taxon Dace, Blackside Phoxinus cumberlandensis T Fish Dace, Clover Valley Speckled Rhinichthys osculus oligoporus E Fish Dace, Desert Eremichthys acros T Fish Dace, Foskett Speckled Rhinichthys osculus ssp. T Fish Dace, Independence Valley Speckled Rhinichthys osculus lethoporus E Fish Dace, Moapa Moapa coriacea E Fish Darter, Amber Percina antesella E Fish Darter, Bayou Etheostoma rubrum T Fish Darter, Bluemask (=jewel) Etheostoma sp. E Fish Darter, Boulder Etheostoma wapiti E Fish Darter, Cherokee Etheostoma scotti T Fish Darter, Duskytail Etheostoma percnurum E Fish Darter, Etowah Etheostoma etowahae E Fish Darter, Fountain Etheostoma fonticola E Fish Darter, Goldline Percina aurolineata T Fish Darter, Leopard Percina pantherina T Fish Darter, Maryland Etheostoma sellare E Fish Darter, Niangua Etheostoma nianguae T Fish Darter, Okaloosa Etheostoma okaloosae E Fish Darter, Relict Etheostoma chienense E Fish Darter, Slackwater Etheostoma boschungi T Fish Darter, Snail Percina tanasi T Fish Darter, Vermilion Etheostoma chermocki E Fish Darter, Watercress Etheostoma nuchale E Fish Gambusia, Big Bend Gambusia gaigei E Fish Gambusia, Clear Creek Gambusia heterochir E Fish Gambusia, Pecos Gambusia nobilis E Fish Gambusia, San Marcos Gambusia georgei E Fish Goby, Tidewater Eucyclogobius newberryi E Fish Laurel dace Chrosomus aylori E Fish Logperch, Conasauga Percina jenkinsi E Fish Logperch, Roanoke Percina rex E Fish Madtom, Neosho Noturus placidus T Fish 
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Common Name Scientific Name Status Taxon Madtom, Pygmy Noturus stanauli E Fish Madtom, Scioto Noturus trautmani E Fish Madtom, Smoky Noturus baileyi E Fish Madtom, Yellowfin Noturus flavipinnis T Fish Minnow, Devils River Dionda diaboli T Fish Minnow, Loach Tiaroga cobitis E Fish Minnow, Rio Grande Silvery Hybognathus amarus E Fish Pupfish, Ash Meadows Amargosa Cyprinodon nevadensis mionectes E Fish Pupfish, Comanche Springs Cyprinodon elegans E Fish Pupfish, Desert Cyprinodon macularius E Fish Pupfish, Devils Hole Cyprinodon diabolis E Fish Pupfish, Leon Springs Cyprinodon bovinus E Fish Pupfish, Owens Cyprinodon radiosus E Fish Pupfish, Warm Springs Cyprinodon nevadensis pectoralis E Fish Rockfish, Bocaccio Sebastes paucispinis E Fish Rush darter Etheostoma phytophilum E Fish Salmon, Atlantic Salmo salar E Fish Salmon, Chinook Oncorhynchus (=Salmo) tshawytscha E/T Fish Salmon, Chum Oncorhynchus (=Salmo) keta T Fish Salmon, Coho Oncorhynchus (=Salmo) kisutch E/T Fish Salmon, Sockeye Oncorhynchus (=Salmo) nerka E Fish Sawfish, Smalltooth Pristis pectinata E Fish Sculpin, Pygmy Cottus paulus (=pygmaeus) T Fish Shiner, Arkansas River Notropis girardi T Fish Shiner, Beautiful Cyprinella formosa T Fish Shiner, Blue Cyprinella caerulea T Fish Shiner, Cahaba Notropis cahabae E Fish Shiner, Cape Fear Notropis mekistocholas E Fish Shiner, Palezone Notropis albizonatus E Fish Shiner, Pecos Bluntnose Notropis simus pecosensis T Fish Shiner, Topeka Notropis topeka (=tristis) E Fish Silverside, Waccamaw Menidia extensa T Fish Smelt, Delta Hypomesus transpacificus T Fish 
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Common Name Scientific Name Status Taxon Spikedace Meda fulgida E Fish Spinedace, Big Spring Lepidomeda mollispinis pratensis T Fish Spinedace, Little Colorado Lepidomeda vittata T Fish Spinedace, White River Lepidomeda albivallis E Fish Springfish, Hiko White River Crenichthys baileyi grandis E Fish Springfish, Railroad Valley Crenichthys nevadae T Fish Springfish, White River Crenichthys baileyi baileyi E Fish Squawfish, Colorado Ptychocheilus lucius E Fish Steelhead Oncorhynchus (=Salmo) mykiss E/T Fish Stickleback, Unarmored Threespine Gasterosteus aculeatus williamsoni E Fish Sturgeon, Alabama Scaphirhynchus suttkusi E Fish Sturgeon, Gulf Acipenser oxyrinchus desotoi T Fish Sturgeon, North American green Acipenser medirostris T Fish Sturgeon, Pallid Scaphirhynchus albus E Fish Sturgeon, Shortnose Acipenser brevirostrum E Fish Sturgeon, Shovelnose Scaphirhynchus platorynchus SAT Fish Sturgeon, White Acipenser transmontanus E Fish Sucker, June Chasmistes liorus E Fish Sucker, Lost River Deltistes luxatus E Fish Sucker, Modoc Catostomus microps E Fish Sucker, Razorback Xyrauchen texanus E Fish Sucker, Santa Ana Catostomus santaanae T Fish Sucker, Shortnose Chasmistes brevirostris E Fish Sucker, Warner Catostomus warnerensis T Fish Topminnow, Gila (Yaqui) Poeciliopsis occidentalis E Fish Trout, Apache Oncorhynchus apache T Fish Trout, Bull Salvelinus confluentus T Fish Trout, Gila Oncorhynchus gilae E Fish Trout, Greenback Cutthroat Oncorhynchus clarki stomias T Fish Trout, Lahontan Cutthroat Oncorhynchus clarki henshawi T Fish Trout, Little Kern Golden Oncorhynchus aguabonita whitei T Fish Trout, Paiute Cutthroat Oncorhynchus clarki seleniris T Fish Woundfin Plagopterus argentissimus E Fish 
152 

Common Name Scientific Name Status Taxon Yellowcheek darter Etheostoma moorei E Fish Abalone, Black Haliotis cracherodii E Gastropod Abalone, White Haliotis sorenseni E Gastropod Ambersnail, Kanab Oxyloma haydeni kanabensis E Gastropod Campeloma, Slender Campeloma decampi E Gastropod Cavesnail, Tumbling Creek Antrobia culveri E Gastropod Elimia, Lacy Elimia crenatella T Gastropod Hornsnail, rough Pleurocera foremani E Gastropod Limpet, Banbury Springs Lanx sp. E Gastropod Marstonia, Royal (=Royal Snail) Pyrgulopsis ogmorhaphe E Gastropod Pebblesnail, Flat Lepyrium showalteri E Gastropod Riversnail, Anthony's Athearnia anthonyi E Gastropod Rocksnail, interrupted Leptoxis foremani E Gastropod Rocksnail, Painted Leptoxis taeniata T Gastropod Rocksnail, Plicate Leptoxis plicata E Gastropod Rocksnail, Round Leptoxis ampla T Gastropod Shagreen, Magazine Mountain Mesodon magazinensis T Gastropod Snail, Armored Pyrgulopsis (=Marstonia) pachyta E Gastropod Snail, Bliss Rapids Taylorconcha serpenticola T Gastropod Snail, Chittenango Ovate Amber Succinea chittenangoensis T Gastropod Snail, Flat-spired Three-toothed Triodopsis platysayoides T Gastropod Snail, Iowa Pleistocene Discus macclintocki E Gastropod Snail, Lioplax Cylindrical Lioplax cyclostomaformis E Gastropod Snail, Morro Shoulderband Helminthoglypta walkeriana E Gastropod Snail, Newcomb's Erinna newcombi T Gastropod Snail, Noonday Mesodon clarki nantahala T Gastropod Snail, O'ahu Tree (Achatinella abbreviata) Achatinella abbreviata E Gastropod Snail, O'ahu Tree (Achatinella apexfulva) Achatinella apexfulva E Gastropod Snail, O'ahu Tree (Achatinella bellula) Achatinella bellula E Gastropod Snail, O'ahu Tree (Achatinella buddii) Achatinella buddii E Gastropod Snail, O'ahu Tree (Achatinella bulimoides) Achatinella bulimoides E Gastropod Snail, O'ahu Tree (Achatinella byronii) Achatinella byronii E Gastropod Snail, O'ahu Tree (Achatinella caesia) Achatinella caesia E Gastropod 
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Common Name Scientific Name Status Taxon Snail, O'ahu Tree (Achatinella casta) Achatinella casta E Gastropod Snail, O'ahu Tree (Achatinella cestus) Achatinella cestus E Gastropod Snail, O'ahu Tree (Achatinella concavospira) Achatinella concavospira E Gastropod Snail, O'ahu Tree (Achatinella curta) Achatinella curta E Gastropod Snail, O'ahu Tree (Achatinella decipiens) Achatinella decipiens E Gastropod Snail, O'ahu Tree (Achatinella decora) Achatinella decora E Gastropod Snail, O'ahu Tree (Achatinella dimorpha) Achatinella dimorpha E Gastropod Snail, O'ahu Tree (Achatinella elegans) Achatinella elegans E Gastropod Snail, O'ahu Tree (Achatinella fulgens) Achatinella fulgens E Gastropod Snail, O'ahu Tree (Achatinella fuscobasis) Achatinella fuscobasis E Gastropod Snail, O'ahu Tree (Achatinella juddii) Achatinella juddii E Gastropod Snail, O'ahu Tree (Achatinella juncea) Achatinella juncea E Gastropod Snail, O'ahu Tree (Achatinella lehuiensis) Achatinella lehuiensis E Gastropod Snail, O'ahu Tree (Achatinella leucorraphe) Achatinella leucorraphe E Gastropod Snail, O'ahu Tree (Achatinella lila) Achatinella lila E Gastropod Snail, O'ahu Tree (Achatinella livida) Achatinella livida E Gastropod Snail, O'ahu Tree (Achatinella lorata) Achatinella lorata E Gastropod Snail, O'ahu Tree (Achatinella mustelina) Achatinella mustelina E Gastropod Snail, O'ahu Tree (Achatinella papyracea) Achatinella papyracea E Gastropod Snail, O'ahu Tree (Achatinella phaeozona) Achatinella phaeozona E Gastropod Snail, O'ahu Tree (Achatinella pulcherrima) Achatinella pulcherrima E Gastropod Snail, O'ahu Tree (Achatinella pupukanioe) Achatinella pupukanioe E Gastropod Snail, O'ahu Tree (Achatinella rosea) Achatinella rosea E Gastropod Snail, O'ahu Tree (Achatinella sowerbyana) Achatinella sowerbyana E Gastropod Snail, O'ahu Tree (Achatinella spaldingi) Achatinella spaldingi E Gastropod Snail, O'ahu Tree (Achatinella stewartii) Achatinella stewartii E Gastropod Snail, O'ahu Tree (Achatinella swiftii) Achatinella swiftii E Gastropod Snail, O'ahu Tree (Achatinella taeniolata) Achatinella taeniolata E Gastropod Snail, O'ahu Tree (Achatinella thaanumi) Achatinella thaahumi E Gastropod Snail, O'ahu Tree (Achatinella turgida) Achatinella turgida E Gastropod Snail, O'ahu Tree (Achatinella valida) Achatinella valida E Gastropod Snail, O'ahu Tree (Achatinella viridans) Achatinella viridans E Gastropod Snail, O'ahu Tree (Achatinella vittata) Achatinella vittata E Gastropod 
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Common Name Scientific Name Status Taxon Snail, O'ahu Tree (Achatinella vulpina) Achatinella vulpina E Gastropod Snail, Pecos Assiminea Assiminea pecos E Gastropod Snail, Snake River Physa Physa natricina E Gastropod Snail, Tulotoma Tulotoma magnifica T Gastropod Snail, Virginia Fringed Mountain Polygyriscus virginianus E Gastropod Springsnail, Alamosa Tryonia alamosae E Gastropod Springsnail, Bruneau Hot Pyrgulopsis bruneauensis E Gastropod Springsnail, Chupadera Pyrgulopsis chupaderae E Gastropod Springsnail, Koster's Juturnia kosteri E Gastropod Springsnail, Roswell Pyrgulopsis roswellensis E Gastropod Springsnail, San Bernardino Pyrgulopsis bernardina E Gastropod Springsnail, Socorro Pyrgulopsis neomexicana E Gastropod Springsnail, Three Forks Pyrgulopsis trivialis E Gastropod Beetle, American Burying Nicrophorus americanus E Insect Beetle, Casey's June Dinacoma caseyi E Insect Beetle, Coffin Cave Mold Batrisodes texanus E Insect Beetle, Comal Springs Dryopid Stygoparnus comalensis E Insect Beetle, Comal Springs Riffle Heterelmis comalensis E Insect Beetle, Delta Green Ground Elaphrus viridis T Insect Beetle, Helotes Mold Batrisodes venyivi E Insect Beetle, Hungerford's Crawling Water Brychius hungerfordi E Insect Beetle, Kretschmarr Cave Mold Texamaurops reddelli E Insect Beetle, Mount Hermon June Polyphylla barbata E Insect Beetle, Northeastern Beach Tiger Cicindela dorsalis dorsalis T Insect Beetle, Ohlone Tiger Cicindela ohlone E Insect Beetle, Puritan Tiger Cicindela puritana T Insect Beetle, Salt Creek Tiger Cicindela nevadica lincolniana E Insect Beetle, Tooth Cave Ground Rhadine persephone E Insect Beetle, Valley Elderberry Longhorn Desmocerus californicus dimorphus T Insect blackline Hawaiian damselfly Megalagrion nigrohamatum nigrolineatum E Insect Butterfly [Cassius Blue, Ceraunus Blue, Nickerbean Blue] Leptotes and Hemiargus and Cyclargus genus SAT Insect Butterfly, Bay Checkerspot (Wright's euphydryas) Euphydryas editha bayensis T Insect Butterfly, Behren's Silverspot Speyeria zerene behrensii E Insect 
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Common Name Scientific Name Status Taxon Butterfly, Callippe Silverspot Speyeria callippe callippe E Insect Butterfly, Ceranus Blue Hemiargus ceraunus antibubastus SAT Insect Butterfly, El Segundo Blue Euphilotes battoides allyni E Insect Butterfly, Fender's Blue Icaricia icarioides fenderi E Insect Butterfly, Karner Blue Lycaeides melissa samuelis E Insect Butterfly, Lange's Metalmark Apodemia mormo langei E Insect Butterfly, Lotis Blue Lycaeides argyrognomon lotis E Insect Butterfly, Miami Blue Cyclargus thomasi bethunebakeri E Insect Butterfly, Mission Blue Icaricia icarioides missionensis E Insect Butterfly, Mitchell's Satyr Neonympha mitchellii mitchellii E Insect Butterfly, Myrtle's Silverspot Speyeria zerene myrtleae E Insect Butterfly, Nickerbean Blue Cyclargus ammon SAT Insect Butterfly, Oregon Silverspot Speyeria zerene hippolyta T Insect Butterfly, Palos Verdes Blue Glaucopsyche lygdamus palosverdesensis E Insect Butterfly, Quino Checkerspot Euphydryas editha quino (=E. e. wrighti) E Insect Butterfly, Saint Francis' Satyr Neonympha mitchellii francisci E Insect Butterfly, San Bruno Elfin Callophrys mossii bayensis E Insect Butterfly, Smith's Blue Euphilotes enoptes smithi E Insect Butterfly, Uncompahgre Fritillary Boloria acrocnema E Insect Crimson Hawaiian damselfly Megalagrion leptodemas E Insect Damselfly, Flying Earwig Hawaiian Megalagrion nesiotes E Insect Damselfly, Pacific Hawaiian Megalagrion pacificum E Insect Dragonfly, Hine's Emerald Somatochlora hineana E Insect Fly, Delhi Sands Flower-loving Rhaphiomidas terminatus abdominalis E Insect Fly, Hawaiian picture-wing Drosophila aglaia E Insect Fly, Hawaiian picture-wing Drosophila hemipeza E Insect Fly, Hawaiian picture-wing Drosophila heteroneura E Insect Fly, Hawaiian picture-wing Drosophila montgomeryi E Insect Fly, Hawaiian picture-wing Drosophila mulli T Insect Fly, Hawaiian picture-wing Drosophila musaphilia E Insect Fly, Hawaiian picture-wing Drosophila neoclavisetae E Insect Fly, Hawaiian picture-wing Drosophila obatai E Insect Fly, Hawaiian picture-wing Drosophila ochrobasis E Insect 
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Common Name Scientific Name Status Taxon Fly, Hawaiian picture-wing Drosophila substenoptera E Insect Fly, Hawaiian picture-wing Drosophila tarphytrichia E Insect Grasshopper, Zayante Band-winged Trimerotropis infantilis E Insect Hawaiian picture-wing Fly Drosophila sharpi E Insect Moth, Blackburn's Sphinx Manduca blackburni E Insect Moth, Kern Primrose Sphinx Euproserpinus euterpe T Insect Naucorid, Ash Meadows Ambrysus amargosus T Insect Oceanic Hawaiian damselfly Megalagrion oceanicum E Insect Rhadine exilis (ncn) Rhadine exilis E Insect Rhadine infernalis (ncn) Rhadine infernalis E Insect Skipper, Carson Wandering Pseudocopaeodes eunus obscurus E Insect Skipper, Laguna Mountain Pyrgus ruralis lagunae E Insect Skipper, Pawnee Montane Hesperia leonardus montana T Insect Cladonia, Florida Perforate Cladonia perforata E Lichen Lichen, Rock Gnome Gymnoderma lineare E Lichen Bat, Gray Myotis grisescens E Mammal Bat, Hawaiian Hoary Lasiurus cinereus semotus E Mammal Bat, Indiana Myotis sodalis E Mammal Bat, Lesser (=Sanborn's) Long-nosed Leptonycteris curasoae yerbabuenae E Mammal Bat, Little Mariana Fruit Pteropus tokudae E Mammal Bat, Mariana Fruit (=Mariana Flying Fox) Pteropus mariannus mariannus T Mammal Bat, Mexican Long-nosed Leptonycteris nivalis E Mammal Bat, Ozark Big-eared Corynorhinus (=Plecotus) townsendii ingens E Mammal Bat, Virginia Big-eared Corynorhinus (=Plecotus) townsendii virginianus E Mammal Bear, American Black Ursus americanus SAT Mammal Bear, Grizzly Ursus arctos horribilis T Mammal Bear, Louisiana Black Ursus americanus luteolus T Mammal Bison, Wood Bison bison athabascae E Mammal Caribou, Woodland Rangifer tarandus caribou E Mammal Deer, Columbian White-tailed Odocoileus virginianus leucurus E Mammal Ferret, Black-footed Mustela nigripes E Mammal Fox, San Joaquin Kit Vulpes macrotis mutica E Mammal Fox, San Miguel Island Urocyon littoralis littoralis E Mammal 
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Common Name Scientific Name Status Taxon Fox, Santa Catalina Island Urocyon littoralis catalinae E Mammal Fox, Santa Cruz Island Urocyon littoralis santacruzae E Mammal Fox, Santa Rosa Island Urocyon littoralis santarosae E Mammal Gray Wolf Canis lupus E Mammal Jaguar Panthera onca E Mammal Jaguarundi, Gulf Coast Herpailurus (=Felis) yagouaroundi cacomitli E Mammal Jaguarundi, Sinaloan Herpailurus (=Felis) yagouaroundi tolteca E Mammal Kangaroo Rat, Fresno Dipodomys nitratoides exilis E Mammal Kangaroo Rat, Giant Dipodomys ingens E Mammal Kangaroo Rat, Morro Bay Dipodomys heermanni morroensis E Mammal Kangaroo Rat, San Bernardino Merriam's Dipodomys merriami parvus E Mammal Kangaroo Rat, Stephens' Dipodomys stephensi (incl. D. cascus) E Mammal Kangaroo Rat, Tipton Dipodomys nitratoides nitratoides E Mammal Killer whale, Southern Resident DPS Orcinus orca E Mammal Lynx, Canada Lynx canadensis T Mammal Manatee, West Indian Trichechus manatus E Mammal Mountain Beaver, Point Arena Aplodontia rufa nigra E Mammal Mouse, Alabama Beach Peromyscus polionotus ammobates E Mammal Mouse, Anastasia Island Beach Peromyscus polionotus phasma E Mammal Mouse, Choctawhatchee Beach Peromyscus polionotus allophrys E Mammal Mouse, Pacific Pocket Perognathus longimembris pacificus E Mammal Mouse, Perdido Key Beach Peromyscus polionotus trissyllepsis E Mammal Mouse, Preble's Meadow Jumping Zapus hudsonius preblei T Mammal Mouse, Salt Marsh Harvest Reithrodontomys raviventris E Mammal Mouse, Southeastern Beach Peromyscus polionotus niveiventris T Mammal Mouse, St. Andrew Beach Peromyscus polionotus peninsularis E Mammal Ocelot Leopardus (=Felis) pardalis E Mammal Otter, Northern Sea Enhydra lutris kenyoni T Mammal Otter, Southern Sea Enhydra lutris nereis T Mammal Panther, Florida Puma (=Felis) concolor coryi E Mammal Prairie Dog, Utah Cynomys parvidens T Mammal Pronghorn, Sonoran Antilocapra americana sonoriensis E Mammal Puma (=Cougar), Eastern Puma (=Felis) concolor (all subsp. except coryi) E Mammal 
158 

Common Name Scientific Name Status Taxon Rabbit, Pygmy Brachylagus idahoensis E Mammal Rabbit, Riparian Brush Sylvilagus bachmani riparius E Mammal Seal, Guadalupe Fur Arctocephalus townsendi T Mammal Seal, Hawaiian Monk Monachus schauinslandi E Mammal Seal, spotted Phoca largha T Mammal Sea-lion, Steller Eumetopias jubatus E/T Mammal Sheep, Peninsular Bighorn Ovis canadensis nelsoni E Mammal Sheep, Sierra Nevada Bighorn Ovis canadensis sierrae E Mammal Shrew, Buena Vista Lake Ornate Sorex ornatus relictus E Mammal Squirrel, Carolina Northern Flying Glaucomys sabrinus coloratus E Mammal Squirrel, Delmarva Peninsula Fox Sciurus niger cinereus E Mammal Squirrel, Mount Graham Red Tamiasciurus hudsonicus grahamensis E Mammal Squirrel, Northern Idaho Ground Spermophilus brunneus brunneus T Mammal Vole, Amargosa Microtus californicus scirpensis E Mammal Vole, Florida Salt Marsh Microtus pennsylvanicus dukecampbelli E Mammal Vole, Hualapai Mexican Microtus mexicanus hualpaiensis E Mammal Whale, beluga Delphinapterus leucas E Mammal Whale, Finback Balaenoptera physalus E Mammal Whale, Gray Eschrichtius robustus E Mammal Whale, Humpback Megaptera novaeangliae E Mammal Whale, North Atlantic right Eubalaena glacialis (incl. australis) E Mammal Whale, Sei Balaenoptera borealis E Mammal Whale, Sperm Physeter catodon (=macrocephalus) E Mammal Wolf, Red Canis rufus E Mammal Woodrat, Riparian Neotoma fuscipes riparia E Mammal Alopecurus, Sonoma Alopecurus aequalis var. sonomensis E Monocot Amole, Cammatta Canyon Chlorogalum purpureum var. reductum T Monocot Amole, Purple Chlorogalum purpureum var. purpureum T Monocot Aristida chaseae (ncn) Aristida chaseae E Monocot Arrowhead, Bunched Sagittaria fasciculata E Monocot Beaked-rush, Knieskern's Rhynchospora knieskernii T Monocot Beargrass, Britton's Nolina brittoniana E Monocot Beauty, Harper's Harperocallis flava E Monocot 
159 

Common Name Scientific Name Status Taxon Bluegrass, Hawaiian Poa sandvicensis E Monocot Bluegrass, Mann's (Poa mannii) Poa mannii E Monocot Bluegrass, Napa Poa napensis E Monocot Bluegrass, San Bernardino Poa atropurpurea E Monocot Brodiaea, Chinese Camp Brodiaea pallida T Monocot Brodiaea, Thread-leaved Brodiaea filifolia T Monocot Bulrush, Northeastern (=Barbed Bristle) Scirpus ancistrochaetus E Monocot Cranichis Ricartii Cranichis ricartii E Monocot Fritillary, Gentner's Fritillaria gentneri E Monocot Grass, California Orcutt Orcuttia californica E Monocot Grass, Colusa Neostapfia colusana T Monocot Grass, Eureka Dune Swallenia alexandrae E Monocot Grass, Fosberg's Love Eragrostis fosbergii E Monocot Grass, San Joaquin Valley Orcutt Orcuttia inaequalis T Monocot Grass, Solano Tuctoria mucronata E Monocot Grass, Tennessee Yellow-eyed Xyris tennesseensis E Monocot Hala Pepe (Pleomele hawaiiensis) Pleomele hawaiiensis E Monocot Hilo Ischaemum (Ischaemum byrone) Ischaemum byrone E Monocot Iris, Dwarf Lake Iris lacustris T Monocot Irisette, White Sisyrinchium dichotomum E Monocot Kamanomano (Cenchrus agrimonioides) Cenchrus agrimonioides E Monocot Ladies'-tresses, Canelo Hills Spiranthes delitescens E Monocot Ladies'-tresses, Navasota Spiranthes parksii E Monocot Ladies'-tresses, Ute Spiranthes diluvialis T Monocot Lau'ehu (Panicum niihauense) Panicum niihauense E Monocot Lepanthes eltorensis (ncn) Lepanthes eltoroensis E Monocot Lily, Minnesota Trout Erythronium propullans E Monocot Lily, Pitkin Marsh Lilium pardalinum ssp. pitkinense E Monocot Lily, Tiburon Mariposa Calochortus tiburonensis T Monocot Lily, Western Lilium occidentale E Monocot lo`ulu Pritchardia hardyi E Monocot Lo`ulu (Pritchardia affinis) Pritchardia affinis E Monocot Lo`ulu (Pritchardia kaalae) Pritchardia kaalae E Monocot 
160 

Common Name Scientific Name Status Taxon Lo`ulu (Pritchardia napaliensis) Pritchardia napaliensis E Monocot Lo`ulu (Pritchardia schattaueri) Pritchardia schattaueri E Monocot Lo`ulu (Pritchardia viscosa) Pritchardia viscosa E Monocot Manaca, palma de Calyptronoma rivalis T Monocot Mariscus fauriei (ncn) Mariscus fauriei E Monocot Mariscus pennatiformis (ncn) Mariscus pennatiformis E Monocot Onion, Munz's Allium munzii E Monocot Orchid, Eastern Prairie Fringed Platanthera leucophaea T Monocot Orchid, Western Prairie Fringed Platanthera praeclara T Monocot Pa'iniu Astelia waialealae E Monocot Panicgrass, Carter's (Panicum fauriei var.carteri) Panicum fauriei var. carteri E Monocot Pelos del Diablo Aristida portoricensis E Monocot Pink, Swamp Helonias bullata T Monocot Piperia, Yadon's Piperia yadonii E Monocot Platanthera holochila (ncn) Platanthera holochila E Monocot Poa siphonoglossa (ncn) Poa siphonoglossa E Monocot Pogonia, Small Whorled Isotria medeoloides T Monocot Pondweed, Little Aguja Creek Potamogeton clystocarpus E Monocot Pu'uka'a (Cyperus trachysanthos) Cyperus trachysanthos E Monocot Seagrass, Johnson's Halophila johnsonii T Monocot Sedge, Golden Carex lutea E Monocot Sedge, Navajo Carex specuicola T Monocot Sedge, White Carex albida E Monocot Trillium, Persistent Trillium persistens E Monocot Trillium, Relict Trillium reliquum E Monocot Walnut, Nogal Juglans jamaicensis E Monocot Water-plantain, Kral's Sagittaria secundifolia T Monocot Wild-rice, Texas Zizania texana E Monocot Alligator, American Alligator mississippiensis T Reptile Boa, Puerto Rican Epicrates inornatus E Reptile Boa, Virgin Islands Tree Epicrates monensis granti E Reptile Crocodile, American Crocodylus acutus T Reptile Lizard, Blunt-nosed Leopard Gambelia silus E Reptile 
161 

Common Name Scientific Name Status Taxon Lizard, Coachella Valley Fringe-toed Uma inornata T Reptile Lizard, Island Night Xantusia riversiana T Reptile Lizard, St. Croix Ground Ameiva polops E Reptile Rattlesnake, New Mexican Ridge-nosed Crotalus willardi obscurus T Reptile Sea turtle, green Chelonia mydas E/T Reptile Sea turtle, hawksbill Eretmochelys imbricata E Reptile Sea turtle, leatherback Dermochelys coriacea E Reptile Sea turtle, loggerhead Caretta caretta E/T Reptile Skink, Blue-tailed Mole Eumeces egregius lividus T Reptile Skink, Sand Neoseps reynoldsi T Reptile Snake, Atlantic Salt Marsh Nerodia clarkii taeniata T Reptile Snake, Eastern Indigo Drymarchon corais couperi T Reptile Snake, Giant Garter Thamnophis gigas T Reptile Snake, Northern Copperbelly Water Nerodia erythrogaster neglecta T Reptile Snake, San Francisco Garter Thamnophis sirtalis tetrataenia E Reptile Tortoise, Desert Gopherus agassizii T Reptile Tortoise, Gopher Gopherus polyphemus T Reptile Turtle, Alabama Red-bellied Pseudemys alabamensis E Reptile Turtle, Bog Clemmys muhlenbergii T Reptile Turtle, Flattened Musk Sternotherus depressus T Reptile Turtle, Plymouth Red-bellied Pseudemys rubriventris bangsi E Reptile Turtle, Ringed Map Graptemys oculifera T Reptile Turtle, Yellow-blotched Map Graptemys flavimaculata T Reptile Whipsnake (=Striped Racer), Alameda Masticophis lateralis euryxanthus T Reptile 
162