·---

UNITED STATES ENVIRONMENTAL PROTECTION AGENCY 

WASHINGTON D.C., 20460 

MEMORANDUM 

OFFICE OF 

CHEMICAL SAFETY AND 

POLLUTION PREVENTION 

September 19, 2012 

PC Code: 044312 

DP Barcode: D398677 

SUBJECT: FIFRA Section 3 New Use Environmental Risk Assessment for the Registration 

of Dinotefuran for Rice. 

TO: Venus Eagle, Risk Manager 

Rita Kumar, Risk Manager Reviewer 

Insecticide-Rodenticide Branch 

Registration Division (7505P ---~ 

THROUGH: Dana Spatz, Branch Chief 

Rosanna Louie-Juzwiak, RAPL 

Environmental Risk Branch III 

FROM: 

SUMMARY 

Environmental Fate and Effects Division (7507P) 

Frank T. Farruggia, Ph.D., Biologist 

James K. Wolf, Ph.D., Environmental S 

Environmental Risk Branch III 

Environmental Fate and Effects Division (7507P) 

EFED has conducted an ecological risk assessment for the insecticide dinotefuran (CAS No. 

165252-70-0) and the proposed Section 3 new use on rice to control Rice Stink Bug. Dinotefuran 

is a nitroguanidine insecticide and the active ingredient in the product LX434 Dinotefuran 20SG 

(altemant name: TENCHU 20SG) Insecticide (EPA Reg. No. 86203-25). This assessment builds 

on several previous ecological assessments (Table 1), and relies on a summary of ecological 

effects, environmental fate and physical chemical properties data from those assessments. Based 

on the available invertebrate toxicity data, dinotefuran is very highly toxic to terrestrial and 

aquatic insects and invertebrates. These organisms may be impacted from the proposed of the 

dinotefuran new use on rice; however, because the proposed dinotefuran application timing 

would be post flowering, pollinator (e.g. pollen harvesting insects) exposures in the field are 
2

expected to be minimal. Invertebrates resident in the field or visiting the field (e.g. for food, 

water, shelter, or resting) would be considered at risk. There is also a potential for off-site 

exposure from spray drift to pose a concern for terrestrial and aquatic insects and invertebrates 

from spray drift. With the exception of concerns for risks to terrestrial and aquatic invertebrates, 

there are generally no risks of concern for exposures to terrestrial or aquatic animals or plants 

from the proposed dinotefuran use on rice. 

Table 1. Past Risk Assessments on Dinotefuran. Additional summary information is provided in the recent 

problem formulation for Registration Review (DP Barcode: D389547, 2011). 

DP 

Barcode 

Year Use site Target Pest Action 

285633 2004 Leafy vegetables, turfgrasses, ornamentals, 

residential use 

Various (e.g., ants, 

flies, cockroach, 

etc.) 

Section 3: New 

Chemical 

304957 2004 Cotton, potato, head and stem brassica, fruiting 

vegetables, cucurbits, grapes, ornamental plants 

and flower beds, lawn, shrubs and additional 

residential uses

Various Section 3: New Use 

324854 2006 Head and stem brassica, cucurbits, fruiting 

vegetables, grapes, leafy vegetables, potatoes 

Various Section 3: New Use 

(increasing use rates) 

332829 2006 Leafy Brassica Sweet potato 

whitefly biotype B 

(Bemisia tabaci) 

Section 18 

355010 2008 Rice Rice stink bug Section 18 

358860 2009 Leafy Brassica Greens (Subgroup 5B), 

including turnip greens 

Various IR-4 Petition: 

Incremental 

Environmental RA 

378125 2011 Forestry Uses (Christmas trees, trees in 

plantations, reforestation nurseries, forests, 

woodland areas) 

Various Section 3: New Use 

388997+ 2011 Stone and pome fruit Brown marmorated 

stink bug 

Section 18 

390191 2012 bulb and green onion subgroups, low growing 

berry, small fruit and vine climbing (berry) 

subgroup, tuberous and corm vegetables 

subgroup, watercress, and peach. 

Various Section 3 

 + 390375, 390381, 390380, 390376, 389144, 390383, 390382, 390379, 390378, 390377, 389436, 390903, 390904 

Data Uncertainties and Data Gaps

The available studies have provided suitable information for completing the environmental fate 

and effects risk assessment for the proposed new use on rice. For a comprehensive description 

and justification of data gaps and data needs for the upcoming dinotefuran reregistration 

schedule see the most recent problem formulation for Registration Review document (i.e., Tables 

17-18 and text succeeding the tables, Appendices C and D in DP Barcode DP389547, December 

13, 2011). 
3

PROBLEM FORMULATION 

The environmental fate and toxicity of dinotefuran have been discussed in depth in previous risk 

assessments (e.g., DP285633, 2004; DP332829, 2006; and DP378125, 2011). The registrant 

submitted two environmental fate guideline studies1 to address three data requirements2: (1) 

aerobic aquatic metabolism and (2) anaerobic aquatic metabolism, and (3) freezer storage 

stability identified in the Data Call-In (GDCI-044312-1147). 

Mode of Action 

Dinotefuran, also known as MTI-446, is a broad-spectrum, systemic furanicotinyl insecticide 

belonging to the 4A nitroguanidine class of chemicals and a member of the neonicotinoids that 

were developed as an analog of nicotine. Dinotefuran acts as an agonist at (i.e., it binds to) the 

nicotinic acetylcholine receptor (nAChR) to which the neurotransmitter acetylcholine (ACh) 

would otherwise bind. Acetylcholine (ACh) is the endogenous agonist and excitatory 

neurotransmitter of the cholinergic nervous system. Therefore, dinotefuran acts on the autonomic 

nervous system by binding to the postsynaptic nicotinic acetylcholine receptor. Although the 

cholinesterase enzyme itself is not affected by dinotefuran, the nerve is continually stimulated, 

and the end result, paralysis and death, is similar to that caused by cholinesterase inhibitors. 

Dinotefuran is highly water soluble (39,830 mg/L @20oC) and is readily translocated in plant 

tissue giving it good systemic activity. Dinotefuran has stomach and contact activity and is 

effective against a wide variety of insects including aphids, whiteflies, thrips, leafhoppers, 

leafminer, sawflies, mole crickets, white grubs, lacebugs, billbugs, beetles, mealybugs, stink 

bugs, weevils, and cockroaches. 

 Use Characterization 

A complete summary of the use patterns assessed in the past for dinotefuran is available in the 

recent problem formulation for Registration Review (see Table 3 of DP Barcode: DP389547, 

2011) and FIFRA Section 3 New Use Environmental Risk Assessments (DP Barcode: 

DP390191). A cross-section of the registered agricultural use sites includes cucurbits, grapes, 

pineapple, bulbs and green onions, low growing berries, small fruit and vine climbing berries, 

tuberous and corm vegetables, watercress, peach, nut trees, fruiting vegetables, brassica 

vegetables, and leafy vegetables. Non-agricultural use sites include forest trees, ornamental 

plants (flowering and foliage plants, woody shrubs, vines, and trees), ornamental lawns and turf, 

pets and pet premises, animal premises, domestic dwellings, picnic areas, transportation vehicles, 

food handling establishments, hospitals, and commercial/institutional/industrial buildings. In 

addition to its registered uses there is an active Section 183

 for use on rice in Texas. 

The proposed maximum single aerial application rate is 0.131 pound of active ingredient per 

acre (lb a.i./A), with a maximum of two applications, and a 7-day minimum reapplication 

interval. In regions where two harvests can be produced within a single year, the grower can 

split the applications to one per crop or combine them to a single harvest. This application rate 

 

1

 MRIDs 48680002 and 48680003 

2

 OCSPP Guideline Nos. 835.4400, 835.4300 and 860.1380 

3

 EPA File No. 12TX04, EPA Establishment No. 39578-TX-1 (03/01/12). 
4

for the proposed use is lower than previously assessed uses; namely, use on turfgrass as 0.54 lb 

a.i./A (DP 285633, 2004). A detailed summary of the proposed use pattern addressed in this 

assessment is shown in Table 2. 

Table 2. Proposed New Uses for Dinotefuran 

Crop/Site Application Type/ 

Method 

Single Application 

Rate Range 

(lb a.i./A) 

Maximum Application 

Rate Per Year

(lb a.i./A) 

Maximum Number of 

Applications 

Rice Aerial Spray 0.09375 – 0.131 0.262 2 

The proposed label indicates the timing of applications and use of the higher specified rates are 

triggered by the severity and uniformity of pest pressure. 

ENVIRONMENTAL FATE SUMMARY 

The physico-chemical and environmental fate and transport properties of dinotefuran and its 

transformation products are discussed in detail in the Registration Review: Problem Formulation 

for Environmental Fate, Ecological Risk, Endangered Species, and Drinking Water Exposure 

Assessments for Dinotefuran December 13, 2011 (DP389547) and the new chemical chapter of 

June 30, 2004 (DP285633). Since these reviews, the registrant has submitted two environmental 

fate guideline studies4

 to address three data requirements5: (1) aerobic aquatic metabolism and 

(2) anaerobic aquatic metabolism, and (3) freezer storage stability identified in the Data Call-In 

(GDCI-044312-1147). Only the physico-chemical and environmental fate properties of 

dinotefuran and the transformation/degradation product DN are presented here as it is included in 

the human drinking water assessment (DP397490). 

Physico-chemical Properties 

Dinotefuran has a molecular weight of 202.2 g/mole, a very high water solubility (39,830 mg/L), 

and a low octanol/water partition coefficient (Kow = 0.283; log Kow = -0.549), suggesting a 

potential for low bioaccumulation. The low vapor pressure (1.275 x 10-8 mm Hg) and a low 

Henry’s Law Constant (8.63 x 10-14 atm • M3

/mol) suggest that this compound is not expected to 

volatilize substantially from water or soils in the environment. The selected physico-chemical 

properties of dinotefuran are listed in Table 3. 

Table 3. Physico-chemical Properties for Dinotefuran 

Parameter Value Reference/ Comments 

Selected Physicio Chemical Parameters 

Chemical Classification Nitroguanidine 

Pesticide Classification Systemic Insecticide 

 

4

 MRIDs 48680002 and 48680003 

5

 OCSPP Guideline Nos. 835.4400, 835.4300 and 860.1380 
5

Table 3. Physico-chemical Properties for Dinotefuran 

Parameter Value Reference/ Comments 

Molecular Weight 202.2 g/mol MRID # 45640101 

Water Solubility (20oC) 39,830 mg/L MRID# 45640112 

Vapor pressure (30oC) <1.275x10-8 mm Hg 

(equivalent to <1.7 x 10-6 Pa) 

MRID# 45640105 

MRID# 45639702 

Henry's Law Constant 8.63 x 10-14 Atm m3/mol Calculated 

Octanol/Water Partition, Kow 0.283 @25oC MRID # 45639702 

log KOW -0.549 MRID # 45639702 

Dissociation constant (pKa) 12.6 @20oC (estimated) MRID # 45639702 

Melting point 107.5oC MRID # 45639702 

pH 5.6 @25oC MRID # 45654201 

Density 1.40 g/cm3 @20oC MRID # 45639702 

Fate properties 

The degradation products of dinotefuran are shown in Table 4. DN, UF, MG hydrogen chloride, 

DN-2-OH+DN-3-OH, and BCDN succinate are major degradation products in aquatic 

environments. These degradation products are formed through metabolism (i.e., DN) or 

photodegradation (i.e., DN, UF, MG hydrogen chloride, DN-2-OH+DN-3-OH, and BCDN). 

MNG, is the major degradation product in soil but not in the aquatic metabolism studies. 

Table 4. Dinotefuran Degradates Identified in Environmental Fate Studies 

Short 

names Structure Study Name 

Results (calculated or observed halflife, degradates, and quantities, in 

% applied) 

DN1

Anaerobic Soil Metabolism Maximum 29.2% at 120 days in 

Switzerland soil 

Aerobic Aquatic Metabolism 

Maximum 23.1% at 180 days in river 

system and 32.6% at 103 days in pond 

system 

For the silt loam and sand sediment 

systems, the major product DN was 

detected at maximums of 69.2-69.6% 

and 39.6-47.4% of the applied, 

respectively, at study termination. 

Anaerobic Aquatic Metabolism 

For the silt loam and sand sediment 

systems, the major product DN was 

detected at maximums of 70.7-74.4% 

and 60.5-66.3% of the applied, 

respectively, at study termination. 

O N

H

NH

N

H

CH3

H3PO4
6

Table 4. Dinotefuran Degradates Identified in Environmental Fate Studies 

Short 

names Structure Study Name 

Results (calculated or observed halflife, degradates, and quantities, in 

% applied) 

Photolysis in Water Maximum 7.5% at 11 days 

UF Photolysis in Water Maximum 10.6% at 13.8 days (last 

test interval) 

MG 

hydrogen 

chloride 

Photolysis in Water 

Maximum 10.2% at 1.8 days, and 

0.8% at 13.8 days (final sampling 

interval) 

DN-2-OH 

+ 

 DN-3-OH 

Photolysis in Water Maximum 28.2% at 13.8 days (study 

termination) 

BCDN 

Succinate Photolysis in Water 

Maximum 16.1% at 1.8 days and 

4.5% at 13.8 days (study termination) 

MNG 

Aerobic Soil Metabolism 

Maximum 23.96% at 42 days 

(preliminary study) 

Maximum 13.7% at 225 days 

(conducted on radiolabeled parent), 

study termination 

Terrestrial Field Dissipation 

Maximum 31.5% at 45 days after 2nd

application; study termination at 170 

days after 2nd application 

1

 DN phosphate (1-methyl-3-(tetrahydro-3-furylmethyl)guanidinium dihydrogen phosphate) was identified as a 

degradation product of dinotefuran in photodegradation in soil (MRID 45640109), photodegradation in water 

(MRID 45640106, 45640105) and anaerobic soil metabolism (MRID 45891616) studies. Although the phosphorus 

is not an elemental constituent of parent dinotefuran, DN phosphate was formed as a salt of orthophosphate and 1-

methyl- 3-(tetrahydro-3-furylmethyl)guanidinium. Because the DN phosphate salt will dissociate in soil and aquatic 

environments to form (1-methyl-3-(tetrahydro-3-furylmethyl)guanidinium) and phosphoric acid, it is not expected to 

alter the environmental fate or toxicity of the organic moiety of DN phosphate (1-methyl-3-(tetrahydro-3-

furylmethyl)guanidinium). 

Environmental fate properties for dinotefuran are shown in Table 5.

Table 5. Environmental Fate Properties for Dinotefuran 

Parameter Value Reference/ Comments 

Hydrolysis Half-life stable MRID# 45640102 (s) 

MRID# 45640102 (a) 

Photodegradation in Water Half-life 1.8 days MRID# 45640105 (s) 

Aerobic Soil Metabolism Half-life 38, 17, 78, 89, 63, 100, 87.7, 

 and 15.9 days 

MRID# 45640111 (s) 

MRID# 45640112(s) 

O N

H

O

N

H

CH3

NH

N

H

H2N

CH3

ClH

O

H

N NH

HN

OH

COOH

COOH

2

H N N

O

HN

CH3

COOH

COOH

N

H

H2N

N

CH3

NO2
7

Table 5. Environmental Fate Properties for Dinotefuran 

Parameter Value Reference/ Comments 

MRID# 46751101(a) 

MRID# 45640112(a) 

MRID# 46711201 (s) 

Anaerobic Soil Metabolism Half-life 65 days MRID# 45891616 (s) 

Aerobic Aquatic metabolism Half-life 79.3 days 

 76.0 days 

25.7 – 27.3 silt loam 

66.6 – 50.2 sand 

MRID # 45640117 (s) 

MRID # 48680002 (s) 

Batch Equilibrium Texture Kd Koc

Loam 1.01 42 

Sandy Loam 0.71 45 

Clay Loam 1.22 42 

Loamy Sand 0.12 6 

Silt Loam 0.22 22 

MRID# 45640114 (a) 

Terrestrial Field Dissipation CA (SL) t1/2 = 65.2 days 

MNG (degradate) was detected in 

0-15 cm soil at 31.5% @ 45 days 

after 2nd application. 

GA (SL) t1/2 = 19.4 days 

MNG was detected in 0-15 cm soil 

at 5.3% max. mean concentration 

after 7 and 30 days after the 2nd

application. 

NY (SL) t1/2 = 55.9 days 

MNG was detected in 0-15 cm soil 

at 6.6% @ 45 and 120 days after 

the second application.

Applied 2X @ 0.268 lb a.i/A @ 

14-day interval to bare soil. 

MRID# 45640118 (a) 

Accumulation in Fish, max. BCF NA Waived (KOW = 0.28) 

* (a) = acceptable study that fulfills guideline requirement; (s) = supplemental study; NA=Not Available; 

N/A=Not Applicable 

Based upon the results of an additional aerobic and anaerobic aquatic metabolism study (MRID 

48680002; supplemental study) the major transformation product in an aquatic environment such 

as a rice paddy would be DN. At the termination of this study, 77 to 86 percent of the applied 

radioactivity was identified as dinotefuran or DN; no other degradation products (except CO2) 

were identified. Of these degradates important transformation products in the environmental fate 

studies of dinotefuran appear to be MNG and DN. The aqueous photolysis study had identified 

UF, DN-2-OH+DN-3-OH, MG hydrogen chloride, and BCDN succinate as major transformation 

products, only two (UF, DN-2-OH+DN-3-OH) of these degradates were identified as residues of 

concern. 
8

For the proposed rice use, the relevant environmental fate properties are those associated within 

the aquatic environment. With an aqueous photolysis half-life of 1.8 days, aqueous photolysis 

could be important in clear and shallow bodies of water; however, in rice paddies, deep ponds or 

rivers or flowing bodies of water, it is more likely to dissipate via dissolution, and subsequently 

via metabolism. Based upon this it is assumed that aqueous photolysis would not contribute 

significantly to the degradation of dinotefuran; thus the formation of these photodegradates 

would be expected to be minor (see Table 4). The residues of concern for the drinking water 

assessment for the proposed rice use were dinotefuran and DN (DP397490). 

The previous aerobic aquatic and anaerobic aquatic metabolism study (48681616) was 

determined to be supplemental, in part, because the sediment was determined to be anaerobic 

during the aerobic portion of the study. In another aerobic and anaerobic metabolism study 

(MRID 48680002), the half-lives of parent dinotefuran were similar for each soil (i.e., textural 

class: silt loams~25 days and sand >50 days) (Table 6). The major degradate in the aquatic 

dissipation studies was DN, which was still increasing at the end of the study, so half-lives for 

DN could not be determined. Half-lives (and rate constants), for modeling, were determined for 

the decline of the parent plus DN (based upon % applied radioactivity), for aerobic aquatic (352 

and 685 days) and anaerobic aquatic (188, 468, 510 days) metabolism for the combined 

dinotefuran plus DN residues. 

Table 6. Summary of half-life and degradation rates for Dinotefuran and Dinotefuran + DN in total 

system of Aerobic and Anaerobic Metabolism to address OCSPP No. Guideline Studies 835.4300 and 

835.4400. (Tables 2 and 3 in DP397490) 

MRID 

(condition) 

Soil in 

Soil/Water 

System 

Dinotefuran Dinotefuran + DN 

48680002 

Half-life1 

(day) 

Rate 

(1/day) 

Half-life1 

(day) 

Rate 

 (1/day) 

(Aerobic) Silt loam 25.7 0.027 685 0.00101 

(Aerobic) Sand 66.6 0.0104 352 0.00197 

(Anaerobic) Silt loam 27.3 0.0254 468 0.00148 

(Anaerobic) Sand 50.2 0.0138 509 0.00136 

45891616 

Silt loam 66.842

 0.01037 188 0.0037 

(Anaerobic) 

1 Kinetics model: Single First-Order (SFO) using regression in data analysis of Microsoft Excel 2007 

2 Half-life value in D354339 is 65 days. 3

 90-percent upper bound means of aerobic and anaerobic aquatic degradation rates for Dinotefuran + DN is 1031.9 

days (0.000167 days-1) and 579.3 days (0.00119 days-1), respectively. 

In the soil, dinotefuran appears to be relatively persistent to metabolism, both in aerobic (half-life 

= 63-100 days) and anaerobic soil (half-life = 65 days) conditions. It appears that under 

metabolic conditions, dinotefuran degrades to MNG and subsequently to NG. Dinotefuran is 
9

stable to hydrolysis in a range of pH values of 4 to 9. It is considered to be mobile to highly6,7

mobile (Koc = 6 to 45) in various soil types. It is also very highly soluble (39,830 ppm). Since 

dinotefuran may persist in soils, it may have a high potential to leach to subsurface. 

Furthermore, it can migrate to adjacent bodies of water through spray drift and in runoff events, 

probably dissolved in the water column. 

The batch equilibrium - adsorption/desorption studies conducted on the parent and major 

degradates MNG and DN-phosphate, indicate that the parent dinotefuran, and MNG are very 

highly mobile (Koc<50), while DN is slightly to highly mobile. Koc values for dinotefuran 

ranged from 6 to 45 for eight soils tested (four from Japan and four domestic). Koc values for 

MNG ranged from 8 to 31 for five domestic and foreign soils. The study on DN-phosphate 

yielded a wide range of Koc values (between 58 and 2502). Therefore, parent dinotefuran is more 

mobile then the transformation product DN. 

Environmental fate properties for DN (in its stable form, DN-phosphate) DN-phosphate8

 are 

shown in Table 7. Potential routes of dissipation include photodegradation, microbial-mediated 

metabolism, leaching, and runoff. N-phosphate is stable to abiotic hydrolysis at pH 4, 7, and 9). 

Photodegradation is slow (t1/2= 53.4 to stable days) in water at pH 5, 7, and 9. It is moderately 

persistent (t1/2= 114 days) in soil and aquatic environments. DN-phosphate has low soil:water 

partitioning coefficients (Kd < 3; Koc 58-413) in loam and sandy loam textured soils. Higher 

soil:water partitioning coefficients (Kd: 7 - 72; Koc: 270-2502) were found in clay textured soils. 

These data suggest the extent leaching or runoff of DN-phosphate is dependent on soil properties 

such as texture and organic carbon content. 

Environmental fate data for the other degradation products are presented in the new chemical 

chapter (D285633, June 30, 2004). 

 

6 FAO. 2000. Appendix 2. Parameters of pesticides that influence processes in the soil. In FAO Information 

Division Editorial Group (Ed.), Pesticide Disposal Series 8. Assessing Soil Contamination. A Reference Manual.

Rome: Food & Agriculture Organization of the United Nations (FAO). 

7 USEPA. 2006. Standard Soil Mobility Classification Guidance. Memorandum From S. Bradbury to 

Environmental Fate and Effects Division. January 23, 2004. Environmental Fate and Effects Division. Office of 

Pesticide Programs. United States Environmental Protection Agency. 

8

 DN phosphate (1-methyl-3-(tetrahydro-3-furylmethyl)guanidinium dihydrogen phosphate) was identified as a 

degradation product of dinotefuran in photodegradation in soil (MRID 45640109), photodegradation in water 

(MRID 45640106, 45640105) and anaerobic soil metabolism (MRID 45891616) studies. Although the phosphorus 

is not an elemental constituent of parent dinotefuran, DN phosphate was formed as a salt of orthophosphate and 1-

methyl- 3-(tetrahydro-3-furylmethyl)guanidinium. Because the DN phosphate salt will dissociate in soil and aquatic 

environments to form (1-methyl-3-(tetrahydro-3-furylmethyl)guanidinium) and phosphoric acid, it is not expected to 

alter the environmental fate or toxicity of the organic moiety of DN phosphate (1-methyl-3-(tetrahydro-3-

furylmethyl)guanidinium). 
10

Table 7. Physicochemical and Environmental Fate Properties for Dinotefuran Degradation Product DNPhosphate

Parameter Value Reference/ Comments 

Selected Physical Chemical Parameters 

Water Solubility (20oC) 619,400 mg/L MRID# 45640112 

MRID# 45639702, 45639706, 

45639707 (USEPA Pesticide 

Fact Sheet, 2004) 

Hydrolysis Half-life 

DN-Phosphate pH 4-9 (50o

C) 

stable MRID# 45640104 (s) 

Photodegradation in Water Half-life 

pH 5 

pH7 

pH9 

53.4 days 

Stable (533.2 days) 

Stable 

MRID# 45640108 (s) 

Aerobic Soil Metabolism Half-life 

DN 

114 days MRID# 45640117 (USEPA 

Pesticide Fact Sheet, 2004) 

Aerobic Aquatic metabolism t1/2 114 days MRID# 45640117 (USEPA 

Pesticide Fact Sheet, 2004) 

Mobility in Soils 

DN-Phosphate 

Texture Kd KOC

Loam (US) 2.08 87 

Sandy Loam (US) 2.07 58 

Clay Loam (US) 72.54 2502 

Sandy Loam (Swiss) 2.93 413 

Clay (German) 7.11 270 

MRID# 45640113 (s) 

* (a) = acceptable study that fulfills guideline requirement; (s) = supplemental study; NA=Not Available; 

N/A=Not Applicable 

EXPOSURE MODELING 

Aquatic Exposure 

For dinotefuran use on rice, applications may lead to direct surface water contamination as a 

result of direct spraying of a flooded rice paddy, spray drift or indirect contamination through 

discharge of the paddy water containing dinotefuran sorbed to suspended soil particles and 

dissolved dinotefuran. For this assessment and the associated Drinking Water Assessment 

(DP397490), EECs for dinotefuran and relevant degradates for surface water were obtained 

using the Tier 1 Rice model v.1.09

 and the modified Tier 1 Rice Model (after D354339, 

Meléndez, 20093). The modified Tier 1 Rice Model v.1.0 assumes that only aerobic and 

anaerobic aquatic metabolism processes occur in the rice paddy, during the holding period. 

 

9 http://www.epa.gov/oppefed1/models/water/rice_tier_i.htm
11

Analysis Plan 

Tier 1 Rice Model 

The EFED Tier 1 Rice Model (v1.0, May 8, 2007)10 was used to estimate aquatic exposures for 

applications directly to water (flooded field/paddy). The Tier I Rice Model4 v1.0 (eq. 1) is a 

simple equilibrium partitioning equation that calculates a single, screening-level concentration in 

paddy water and released tail water based on a compound’s application rate and soil mobility. 

 d

ai

w K

m C

0.00105 0.00013

'

  eq. 1

 Cwo = Cw = water concentration [μg/L] 

mai' = mass applied per unit area [kg/ha] 

Kd = water-sediment partitioning coefficient [L/kg] 

Koc = organic carbon partitioning coefficient [L/kg] 

Equation 2 includes the soil property and paddy geometry information to derive eq 1. The 

provisionally modified Tier I Rice Model (eq. 3) includes time, the aerobic degradation rate, and 

the anaerobic degradation rate as inputs in order to estimate a single, screening-level 

concentration in paddy water or tail water at a given time after application. 

  w sed sed b d

ai

w d d K

m C

 3

2

10

10 '

    eq.2

and, if appropriate: 

Kd 01KOC  0.

where: 

 Cw = water concentration [μg/L] 

mai' = mass applied per unit area [kg/ha] 

Kd = water-sediment partitioning coefficient [L/kg] 

KOC = organic carbon partitioning coefficient [L/kg] 

dw = water column depth = 0.10 m 

dsed = sediment depth = 0.01 m 

θsed = porosity of sediment = 0.509 

ρb = bulk density of sediment = 1300 kg/m3

 

10 USEPA 2007. Guidance for Tier I Estimation of Aqueous Pesticide Concentrations in Rice Paddies. Memo from 

S. Bradbury to Environmental Fate and Effects Division; May 8, 2007. U.S. Environmental Protection Agency, 

Office of Prevention, Pesticides and Toxic Substances, Office of Pesticide Programs, Environmental Fate and 

Effects Division, Washington, DC. Available at http://www.epa.gov/oppefed1/models/water/index.htm#rice 

(accessed September 27, 2010). 
12

Provisional Modified Rice Model (Jones, 2006). 

       t

d d K

d k d k d K k

w w

w sed sed b d

w sed sed sed b d

C C e 















 

   



  3

3 1 2 2

10

10

0

 

 

 eq. 3

where, 

t = interval since last application (d) 

k1 = aerobic aqueous metabolism rate constant (1/days) 

k2 = anaerobic aqueous metabolism rate constant (1/days) 

The Tier I Rice Model was calibrated to generate estimates that are similar to or greater than 

dissolved concentrations measured within rice paddies and in discharged paddy water. The 

calibration involved determination of the sediment interaction depth by calibrating the model to 

maximum residues measured in paddy water in dissipation studies. The model does not account 

for volatilization, dilution, foliar interception, or other dissipation processes. The model was not 

evaluated or calibrated for concentrations measured in sediment. 

Detailed descriptions and documentation for the Tier I Rice model can be found on the Office of 

Pesticide Program’s models website.11 

Selecting Input Parameters

The input parameters used in this assessment were selected from the environmental fate data 

submitted to support dinotefuran registration in accordance with US EPA-OPP EFED water 

model parameter guidance.12 The input values used in the Tier I rice model are provided in 

Table 2. The maximum application rate for dinotefuran for rice is 0.131 lb a.i./A (7.5 oz. to 10.5 

oz. product per acre) as an aerial spray. Two applications per season are allowed. Application 

rates should not exceed more than a total of 0.262 lb a.i./A per season for aerial applications. 

The rates for this assessment and the Section 18 (D354339; Meléndez, 2009) are the same. 

The only fate data required for the Tier 1 Rice Model (eq.1) is Kd. The average dinotefuran Kd is 

0.656 mL/g (0.656 L/kg) (Table 5. D354339; Meléndez, J.L. 2009). The modified Tier 1 Rice 

model (eq. 3) also requires k1 the aerobic aqueous metabolism rate constant (1/days) and 

k2 the anaerobic aqueous metabolism rate constant (1/days). These values were determined from 

the 90 percent upper bound to the aerobic aquatic and anaerobic aquatic metabolism half-lives 

(Table 7). DN has an average Kd of 21.2 L/kg, thus, it has greater sorption potential than the 

parent (D394848 MRID 45640013). 

 

11 http://www.epa.gov/oppefed1/models/water/index.htm 12 Guidance for Selecting Input Parameters in Modeling the Environmental Fate and Transport of Pesticides, 

Version 2.1, October 22, 2009. 
13

Surface Water Exposure Estimates 

Modeling Data

Table 8 summarizes the surface water EECs for dinotefuran and relevant degradate (DN). The 

surface water EDWCs were obtained using the provisionally modified Tier 1 Rice Model v.1.0 

for the use of dinotefuran on rice. The peak concentration is 269 μg/L and the longer term 

concentration (≈average) would depend upon retention time (10 to 30 days). 

Table 8. Tier 1 Surface water EECs (μg/L) for the use of dinotefuran on rice, based upon total toxic residues 

(dinotefuran + DN). 

Peak1 Retention Time 

10 day 30 day 60 day 100 day 150 day 

Dinotefuran + DN 269 257 253 248 240 198 

1

 At time = 0 peak concentration represents only parent dinotefuran. 

Monitoring Data 

Dinotefuran data is not available within the National Water-Quality Assessment Program 

(NAWQA) database. 

Terrestrial 

Terrestrial exposure estimates for avian and mammalian risk assessments were derived using the 

T-REX model (version 1.3.1, December 22, 2006). The EEC values used for terrestrial animal 

exposure are derived from the Kenaga nomograph, as modified by Fletcher et al. (1994), 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). Risk quotients are based on the most sensitive LC50 and NOAEC for birds and LD50 for 

mammals. 

We derive terrestrial EECs for dinotefuran using the maximum proposed single and annual 

application rates (i.e., 2 applications of 0.131 lb a.i./acre made 7 days apart). The default 35-day 

foliar half-life value was used for modeling EECs on terrestrial food items. Table 9 illustrates 

expected terrestrial EECs for rice use. 
14

Table 9. Estimated terrestrial exposure for uses of dinotefuran on rice using T-REX

Use Pattern Rice 

Application Rate 0.131 lb a.i./A/application, two applications 

Dietary-Based EECs (mg a.i./L) 

Short Grass: 

Tall Grass: 

Broadleaf plants: 

Fruits, pods, seeds:

Arthropods: 

11.76 

5.39 

6.62 

0.74 

4.61 

ENVIRONMENTAL EFFECTS 

Assessment of risk is based on the most sensitive species tested for terrestrial and aquatic 

organisms. The acute and chronic toxicity values for the most sensitive aquatic animals and 

plants tested are presented in Table 10, Table 11, and Table 12. The most sensitive terrestrial 

animal acute and chronic toxicity values are presented in Table 13 and Table 14. These 

endpoints are based on those presented in the most recent assessment conducted for dinotefuran 

(USEPA 2012, D390191). The complete available ecotoxicity dataset can be found within the 

USEPA 2012 assessment (D390191). 

Aquatic Animals (Acute/Chronic) 

The data submitted by the registrant show that dinotefuran (technical MTI-446) is practically 

nontoxic on an acute basis to freshwater and estuarine/marine fish (96-hour LC50 > 99 mg a.i./L) 

and saltwater mollusks (eastern oyster 96-hr EC50 > 141 mg a.i./L; MRID 45639711); no 

sublethal effects were noted in these studies. The degradate of dinotefuran (DN phosphate) is 

also considered practically non-toxic to the freshwater invertebrate (D. magna 48-hour LC50 > 

110.6 mg a.i./L; MRID 45639710); however, in the same acute study, on the basis of 10% 

immobility in the highest concentration tested a NOAEC of 10 mg a.i./L was determined. 

However, on an chronic basis, dinotefuran appears to be highly toxic to the estuarine/marine 

invertebrates (mysid shrimp LC50 = 0.79 mg a.i./L; MRID 45639713). 

Chronic toxicity testing on freshwater fish (rainbow trout; MRID 45639719) and invertebrates 

(D. magna; MRID 45639718) showed no treatment related effects and NOAECs of > 6.36 mg 

a.i./L and > 95.3 mg a.i./L, respectively. A chronic toxicity test on the estuarine/marine 

invertebrate Americamysis bahia (MRID 48680006) indicates that dinotefuran is very highly 

toxic to estuarine/marine invertebrates on the basis of reproductive and survival endpoints. 
15

Table 10. Acute effect concentrations (LC50/EC50) for aquatic animals following exposure to dinotefuran and DN.

Species Measurement 

Endpoint 

Time LC50/EC50 MRID / 

OCSPP GLN# 

Rainbow Trout 

Oncorhynchus mykiss

Mortality/Intoxication 

(TGAI: 97.26 %) 

96hr 

(limit 

test) 

LC50 > 99.5 mg a.i./L 

NOAEC ≥ 99.5 mg a.i./L 

Endpoint(s) affected: None. 

(Sub)lethal effects: None. 

45639714 

Acceptable / 

Practically nontoxic1

Sheepshead minnow 

Cyprinodon 

variegatus

Mortality/Intoxication 

(TGAI: 99.2 %) 

96hr 

(limit 

test) 

LC50 > 109 mg a.i./L 

NOAEC ≥ 109 mg a.i./L 

Endpoint(s) affected: None. 

(Sub)lethal effects: 

None. 

45639717

Supplemental

/Practically 

non-toxic1

Waterflea 

Daphnia magna

Mortality/Immobility 

(Test substance: DN 

phosphate, metabolite 

of dinotefuran) 

48 hr LC50 > 110.6 mg a.i./L 

NOEAC: 10 mg a.i./L 

LOAEC: 110.6 mg a.i./L 

Endpoint(s) affected: After 48 hours, 

there was 10% immobility in the 

110.6 mg a.i./L treatment group 

which was the basis for a NOAEC of 

10 mg a.i./L. The control and other 

treatment groups had 0% immobility. 

45639710 

(Acceptable/ 

Practically nontoxic1

) 

850.1010 

Mysid 

Americamysis bahia 

Mortality (TGAI: 

99.2%) 

96 hr LC50: 0.79 mg a.i./L 

NOAEC: 0.49 mg a.i./L 

LOAEC: 1.0 mg a.i./L 

Endpoint(s) affected: Mortality, 

sublethal effects 

(Sub)lethal effects: At 96 hours, 

mortality was 5% in the control and 

5, 5, 0, 5, 75, and 100% for the test 

concentrations, respectively. Erratic 

swimming and loss of equilibrium 

were observed in surviving mysids 

from the 1.0 and 2.0 mg a.i./L 

treatment levels during the test. 

Lethargic mysids were observed in 

the 1.0 mg a.i./L treatment level.

45639713

(Acceptable/ 

Highly toxic1

) 

850.1035 

1

Based on EC50 (mg/L): < 0.1 very highly toxic; 0.1-1 highly toxic; >1-10 moderately toxic; >10-100 slightly toxic; 

>100 practically nontoxic 
16

Table 11. Chronic effect concentrations (LC50/EC50) for aquatic animals following exposure to dinotefuran

Species Measurement 

Endpoint 

Time NOEL/LOEL MRID / 

OCSPP GLN# 

Rainbow Trout 

Oncorhynchus mykiss

Endpoints 

considered: 

Fertilization / 

hatching success, 

time to hatch, time 

to swim up, posthatch survival, 

terminal length, wet 

or dry weights 

Early 

life 

stage 

(94 

days) 

(limit 

test) 

94-d NOAEC > 6.36 mg a.i./L 

94-d LOAEC ≥ 6.36 mg a.i./L 

Endpoint(s) affected: None. 

(Sub)lethal effects: None. 

45639719

Acceptable1

Waterflea 

Daphnia magna 

Endpoints 

considered: 

Mortality, 

reproductive effects 

(number of offspring 

per surviving adult), 

terminal length. 

21-day 

chronic 

toxicity 

LC50/EC50 > 95.3 mg a.i./L 

NOAEC > 95.3 mg a.i./L 

LOAEC ≥ 95.3 mg a.i./L 

Endpoint(s) affected: None. 

(Sub)lethal effects: None. 

45639718

Acceptable1 

Mysid 

Americamysis bahia 

F0 Dry Weight, 

Length and 

Mortality; 

Number of Live 

Offspring; 

Time to first brood; 

35 days F0 Female Dry Weight: 

NOEL = <0.044 mg a.i./L 

LOEL = 0.044 mg a.i./L 

F0 Male Length: 

NOEL = <0.044 mg a.i./L 

LOEL = 0.044 mg a.i./L 

F0 Mortality (Post Pairing2

): 

NOEL = 0.044 mg a.i./L 

LOEL = 0.089 mg a.i./L 

Number of Live Offspring: 

NOEL = 0.089 mg a.i./L 

LOEL = 0.21 mg a.i./L 

Time to First Brood: 

NOEL = 0.21 mg a.i./L 

 

48680006

(Acceptable/ 

Very highly 

toxic1

) 

850.1350 

1

Based on EC50 (mg/L): < 0.1 very highly toxic; 0.1-1 highly toxic; >1-10 moderately toxic; >10-100 slightly toxic; 

>100 practically nontoxic 

2

Based on the number of F0 organisms that were kept for the reproduction phase of the study. 

Aquatic Plants 

Toxicity testing on aquatic vascular plants (L. gibba; MRID 45639731) showed no treatment 

related effects yielding 7-day EC50 and NOAEC values of > 110 mg a.i./L and ≥ 110 mg a.i./L, 

respectively. Non-vascular plant (P. subcapitata) acute toxicity testing on two degradates MNG 

(MRID 45639733) and DN (DN-phosphate; MRID 45639734) also showed no treatment related 

effects and thus 96-hour EC50 and NOAEC values of > 98.7/ ≥98.7 mg a.i./L and > 100.4 / 

≥100.4 mg a.i./L, respectively. However, testing with the TGAI (MTI-446, dinotefuran) 

indicated a significant effect on cell density for P. subcapitata at the two highest test 

concentrations yielding a 96-hour NOAEC of 25 mg a.i./L; the EC50 for cell density, biomass, 

and growth rate endpoints, however, is >97.6 mg a.i./L (the highest concentration tested). 
17

Table 12. Effect concentrations (EC50/NOAEC) for aquatic plants following exposure to dinotefuran and some of its 

metabolites

Species Measurement 

Endpoint 

Time EC50/NOAEC MRID / 

OCSPP GLN# 

Vascular 

Duckweed 

Lemna gibba

Dry weight, 

growth rate, 

biomass 

(TGAI: 99.2 

7-

day 

All endpoints: 

EC50 >110 mg a.i./L 

NOAEC =110 mg a.i./L 

Endpoints affected: None 

(Sub)lethal effects: Compared to the 

control, frond dry wt decreased by 21.5, 

2.9, 12.9, 2.3, and 4.3%, biomass 

decreased by 11.2, 3, 17.5, 12.5, and 

8.4%, growth rate decreased by 4.8, 2.3, 

6.9, 4.7, and 3.2%.

45639731 

(Supplemental1) 

850.4400 

Non-vascular 

Green Algae 

Pseudokirchneriella 

subcapitata 

(a.k.a. Selenastrum 

capricornutum) 

Cell density, 

biomass, growth 

rate (TGAI: 

97.26%) 

96 hr EC50 > 97.6 mg a.i./L 

EC05: 21 mg a.i./L 

NOAEC: 25 mg a.i./L 

Endpoint(s) affected: Cell density. 

(Sub)lethal effects: 

Cell density significantly reduced in the 

two highest test concentrations, thus the 

determination of NOAEC of 25 mg a.i./L. 

The 96-hr %inhibition of growth rate was 

1.5, 0, 0.5, 1.6, and 2.0%; of AUG curve 

was 12, -3.2, -1.1, 5.9, and 3.6% for test 

concentrations, respectively. Shape of 

cells was unaffected.

45639732 

(Acceptable) 

850.5400 

Green Algae 

Pseudokirchneriella 

subcapitata 

(a.k.a. Selenastrum 

capricornutum) 

Metabolite 

MNG 

96 hr EC50 > 98.7 mg a.i./L 

NOAEC = 98.7 mg a.i./L 

Endpoints affected: None. 

(Sub)lethal effects: Compared to the 

control, 96-hr %inhibition for cell density 

was 34, -8, and 23%, for growth rate was 

20, -1.7, and 8.3%, for biomass was 30, -

9.8, and 14%

45639733 

(Supplemental2) 

850.5400 

Green Algae 

Pseudokirchneriella 

subcapitata 

(a.k.a. Selenastrum 

capricornutum) 

Metabolite DN 

(DN-Phosphate) 

96 hr EC50 > 100.4 mg a.i./L 

NOAEC =100.4 mg a.i./L 

Endpoints affected: None. 

(Sub)lethal effects: Compared to the 

control, 96-hr %inhibition for cell density 

was 31, -6, and 1%, for growth rate was 

7, 0, and 2%, for biomass was 15, 2, and 

4%

45639734 

(Supplemental2

) 

850.5400 

1

 The study is scientifically sound, but does not satisfy guideline requirements for a tier II acute toxicity study with 

aquatic vascular plants because there were an insufficient number of plants per replicate, test concentrations were 

not analytically determined, and replicate data were only provided for frond number. 

2

 As there is no study guideline for testing with a degradate, the study is classified as supplemental. 
18

Terrestrial Toxicity Summary (Acute/Chronic) 

Birds

Dinotefuran was tested on various species of birds (Japanese quail, northern bobwhite quail, and 

mallard duck for acute oral and dietary studies; and, bobwhite quail and mallard duck for chronic 

reproduction studies). The parent compound is practically nontoxic to Japanese quail (LD50 > 

2,000 mg a.i./kg-bw; MRID 45639720) and bobwhite quail (LD50 > 2,250 mg a.i./kg-bw; MRID 

47353601) on an acute oral basis and to mallard duck (LC50 > 5,000 mg a.i./kg-diet; whereby the 

mean test item intake13 is 997.9 mg a.i./kg-diet per day; MRID 45639722) and Japanese quail 

(LC50 > 5,000 mg a.i./kg-diet; whereby the mean test item intake is 1301 mg a.i./kg-diet per day; 

MRID 45639721) on a subacute dietary basis. However, sublethal effects (lethargy up to 3 hours 

after administration of the test compound) were observed in the highest test concentration (2,000 

mg a.i./kg-bw) of the acute oral Japanese quail study leading to a NOAEL determination of 

1,000 mg a.i./kg-bw. Sublethal effects were not noted in the bobwhite quail acute oral, mallard 

duck or Japanese quail acute dietary studies. Although there appeared to be no significant 

treatment-related effects on bobwhite quail (MRID 45639724) reproductive parameters, chronic 

testing on mallard duck (NOAEC = 2,150 mg a.i./kg-diet; MRID 45639723) showed significant 

reductions in the percentages of number of hatchlings/eggs laid, eggs set, and 14-day old 

survivors. 

Mammals

Dinotefuran is slightly to practically nontoxic on an acute oral (female LD50 = 2000 mg/kg-bw; 

MRID 45639823) or acute inhalation (LC50 > 0.71 mg a.i./L; MRID 47814506) basis to 

mammals (laboratory rat). Chronic studies indicated effects on rats and rabbits. A 2-generation 

reproduction study for MTI-446 (dinotefuran) technical on the rat indicated a reproductive 

NOAEL of 3,000 mg/kg-diet (MRID 45639913) based on decreased uterine weights and 

microscopic alterations in the uterus and estrous cyclicity in Fo and F1 females, slight increases in 

abnormal sperm morphology in Fo and F1 males, and slight decreases in testicular sperm count in 

Fo males and sperm mortality in F1 males. The developmental toxicity NOAEL for MTI-446 

(dinotefuran) technical on rabbits is ≥ 300 mg/kg-bw/day, while the maternal toxicity NOAEL is 

52 mg/kg-bw/day based on decreased body weight gain, decreased food consumption, and gross 

necropsy findings (pale discoloration of the liver and gray white plaques in the stomach). The 

rabbit study is included here to represent the most sensitive NOAEL and to illustrate that 

sublethal effects as a result of chronic exposure to dinotefuran occur in multiple mammalian 

species. The degradates MNG and DN were not tested on birds or mammals. 

Terrestrial Invertebrates

Dinotefuran technical, MTI-446, (MRID 45639725) is highly toxic to bees on an acute contact

basis (48-hr LD50 = 0.047 g a.i./bee) and on an acute oral basis (48-hr LD50 = 0.023 g 

a.i./bee). Similarly, the dinotefuran formulation, MTI-446 20%WG (MRID 45639726, with 

control; MRID 45639727, without negative but with solvent control) is also highly toxic to bees 

on an acute contact (48-hr LD50 = 0.061 g a.i./bee and 0.024 g a.i./bee, respectively) and on an 

acute oral basis (48-hour LD50 = 0.032 g a.i./bee and 0.0076 g a.i./bee, respectively). The 

 

13 The test item intake (TII) was calculated based on food consumption and the nominal test item concentration in 

the diet. For the dietary studies, these values were calculated by the study author. 
19

RT25 (residual time to cause 25% mortality) derived from the exposure to residues on alfalfa 

study (MRID 45639728) with the formulation MTI-446 20% WG indicated that bees were most 

sensitive to the 8 hour aged residue (RT25 = 4.8 hours) and least sensitive to treatment when 

exposed to 48 hour aged residue (RT25 = 90 hours). When translocated from pollen and nectar to 

bee hives, residues of dinotefuran can be detected in stored honey inside hives at least 85 days 

after application (honeybee field study, MRID 48120501), which suggests the occurrence of 

long-term chronic exposure inside the hive and has potential concerns for overwintering success. 

In addition, exposure to dinotefuran formulation MTI-446 20% SG applications (of varying 

exposure periods) led to survivorship and reproductive effects on non-Apis terrestrial 

invertebrates including parasitoid wasp (Aphidius rhopalosiphi, MRID 45640121), predaceous 

bug (Orius laevigatus, MRID 45640122), and predatory mite (an arachnid, Typhlodromus pyri, 

MRID 45640120) indicating LC50 values of 6.89x10-5 lb a.i./A, 1.19x10-5 lb a.i./A, and 0.027 lb 

a.i./A, respectively. It is important to note that with the lowest non-definitive chronic endpoint 

NOAEC (<1.21 x 10-6 lb a.i./A) reported for the predaceous bug study, it is unknown as to how 

much lower the application would need to be to elicit no response in terrestrial invertebrates. For 

additional comparative analyses including a comparison of dinotefuran and imidacloprid 

toxicities to insects refer to USDA Forest Service risk assessment (Durkin 2009; MRID 

47814402). For further details on the toxicity studies see the USEPA 2012 assessment 

(D390191).

Table 13. Acute effect concentrations (LD50/LC50) for terrestrial organisms following exposure to dinotefuran.

Species Measurement 

Endpoint 

Time LD50/LC50 MRID / OCSPP 

GLN# 

Birds 

Japanese quail 

Coturnix japonica 

Oral Toxicity 

(TGAI: 

97.26%) 

14 day LD50 > 2000 mg a.i./kg-bw 

NOAEL: 1000 mg a.i./kg-bw 

No mortality observed. All ♂ & ♀

birds showed somnolence up to 3 hours 

after gavage in 2000 mg a.i./kg-bw 

level which was the basis for a NOAEL 

of 1000 mg a.i./kg-bw; otherwise, none 

45639720 

(Supplemental/ 

Practically nontoxic3

) 

850.2100 

Mammals 

Rat 

Rattus norvegicus 

Oral Toxicity 14 day ♂ LD50 = 2,804 mg/kg-bw 

♀ LD50 = 2,000 mg/kg-bw 

Endpoint(s) affected: Morbidity. 

45639823

(Acceptable/ 

Toxicity 

category III) 

870.1100 

Rat Acute 

Inhalation 

Toxicity (TEP: 

Dinotefuran 

35SL; 35.3%) 

Limit test 

4 hours 

(exposure) 

14 day 

(observation) 

LC50 > 2.02 mg form/L 

LC50 > 0.71 mg a.i./L 

(Sub)lethal effects: None. 

47814506 

(Acceptable / 

Toxicity 

category IV) 

870.1300 

Invertebrates

Honey bee 

Apis mellifera 

Acute Oral 

(EUP, MTI-446 

48 hour LD50 = 0.0076 μg a.i./bee 45639727 

(Supplemental2

; 
20

Table 13. Acute effect concentrations (LD50/LC50) for terrestrial organisms following exposure to dinotefuran.

Species Measurement 

Endpoint 

Time LD50/LC50 MRID / OCSPP 

GLN# 

20% WG: 

21.4%) 

Endpoint(s) affected: Mortality. 

(Sub)lethal effects: By 48 hours, 13, 3, 

17, 43, 97, and 90% mortality was 

observed in the test treatments, 

respectively. Solvent control mortality 

was 20%. However, a concurrent 

dimethoate test had 13% mortality in 

the solvent control. At 4 hours, there 

were stumbling and/or knockdown bees 

observed in every treatment and 

control group, except for the 0.00056 

μg a.i./bee 

*An important note is that the control 

mortality exceeded 10% (an OECD 

requirement), but not the 20% 

guideline limit set for an acute contact 

study).

highly toxic1

) 

850.3020 

Honey bee 

Apis mellifera

Acute Contact 

(EUP, MTI-446 

20% WG: 

21.4%) 

48 hour LD50 = 0.024 μg a.i./bee 

Endpoint(s) affected: Mortality. 

(Sub)lethal effects: By 48 hours, 3, 3, 7, 

43, 63, and 87% mortality was 

observed in the test treatments, 

respectively. Solvent control mortality 

was 0%. At 4 hours, there were 

stumbling and knockdown bees in the 

0.036 and 0.08 μg a.i./bee groups. 

45639727 

(Acceptable / 

Highly toxic1

) 

850.3020 

Parasitoid wasp4 

Aphidius 

rhopalosiphi

(Hymenoptera, 

Braconidae) 

(EUP: MTI-446 

20% SG) 

13-day, 

survival 

(exposure 

phase: 2 day 

exposure; 11 

day obs) and 

separate 

repro study 

(fecundity 

phase: 1 day 

exposure; 10 

day obs) 

13-d LC50: 77.2 mg a.i./ha 

(6.89x10-5 lbs a.i./A) 

(95% CI: 59.4 – 102.6 mg a.i./ha; 5.30 

x 10-5 – 9.16x10-5 lbs a.i./A) 

NOAEC: 7 mg a.i./ha 

(6.25x10-6 lbs a.i./A) 

Endpoints considered: Mortality and 

reproductive effects (parasitism) 

Endpoint(s) affected: Mortality, 

parasitism success. 

(Sub)lethal effects: Corrected mortality 

(using Schneider-Orelli’s fomula5

) was 

-7, -2, 9, 50, and 74% in the test 

treatments, respectively. Significant 

mortality obs in the two highest 

concentrations. Negative control 

mortality was 10%. 

45640121 

Supplemental2
21

Table 13. Acute effect concentrations (LD50/LC50) for terrestrial organisms following exposure to dinotefuran.

Species Measurement 

Endpoint 

Time LD50/LC50 MRID / OCSPP 

GLN# 

Percent reduction in parasitism success 

(#of aphid mummies per ♀) was -1 and 

67% for the two concentrations tested 

(7 and 20 mg a.i./ha). Significant 

reduction in parasitism obs in 20 mg 

a.i./ha group. Control parasitization 

success was 8.4 aphid mummies per ♀

per 22 hour parasitization period. 

Predaceous bug 4 

Orius laevigatus 

(Hemiptera, 

Anthocoridae) 

(EUP: MTI-446 

20% SG) 

21 day (9 

day 

exposure; 12 

day obs), 

survival (9 

days) and 

reproduction 

(12 days) 

study 

21-d LC50: 13.3 mg a.i./ha 

(1.19x10-5 lbs a.i./A) 

(95% CI: 7.0 - 25.1 mg a.i./ha; 

 6.25x10-6 – 2.24x10-5 lbs a.i./A) 

NOAEC <1.36 mg a.i./ha 

(1.21x10-6 lbs a.i./A) 

Probit slope: 2.11 

LOAEC: 8.8 mg a.i./ha 

Endpoints considered: Mortality and 

reproductive effects (oviposition, egg 

hatch success) 

Endpoint(s) affected: Mortality. 

(Sub)lethal effects: Corrected mortality 

(using Schneider-Orelli’s fomula5

) was 

15, 1, 13, 43, and 49% in the test 

treatments, respectively. Significant 

mortality obs in the lowest and two 

highest concentrations. Negative 

control mortality was 16%. 

Percent reduction in mean #of eggs 

produced per day per ♀ was 4 and -2% 

and percent inhibition for egg hatch 

were 0 and -1% for the two 

concentrations tested (2.72 and 5 mg 

a.i./ha). Fecundity was not significantly 

affected by treatment. Reproductive 

success was 6.9 eggs per ♀ per day and 

average egg hatch success was 92%. 

45640122 

Supplemental2
22

Table 13. Acute effect concentrations (LD50/LC50) for terrestrial organisms following exposure to dinotefuran.

Species Measurement 

Endpoint 

Time LD50/LC50 MRID / OCSPP 

GLN# 

Predaceous mite4 

Typhlodromus 

pyri

(Acari: 

Phytoseiidae) 

(EUP: MTI-446 

20% SG) 

14 day (7 

day 

exposure; 7 

day obs), 

survival (7 

days) and 

reproduction 

(7 days) 

study 

14-d LC50: 30.1 g a.i./ha 

(0.027 lbs a.i./A) 

(95% CI: 26.7- 34.2 g a.i./ha; 

0.024 – 0.030 lbs a.i./A) 

NOAEC <15 g a.i./ha 

(0.013 lbs a.i./A) 

Endpoints considered: Mortality and 

reproductive effects (# of eggs and 

oviposition) 

Endpoint(s) affected: Mortality, 

fecundity. 

(Sub)lethal effects: Corrected mortality 

(using Schneider-Orelli’s fomula5

) was 

39, 32, 79, 47, and 96% in the test 

treatments, respectively. Significant 

mortality obs in all test concentrations. 

Negative control mortality was 10%. 

Percent reduction in mean #of eggs 

produced per day per ♀ was 41 and 

51% for the two concentrations tested 

(15 and 20 g a.i./ha). Fecundity was 

significantly reduced in the 20 g a.i./ha 

treatment. Reproductive success was 9 

eggs per ♀ per day. 

45640120 

Supplemental2

1

 Based on acute contact LD50 (μg a.i./bee) <2 highly toxic; 2-10.99 moderately toxic; ≥11 practically non-toxic 2

 The study is a non-guideline study and does not fulfill an OPP guideline requirement. 

3

Acute Oral (avian/mammal): Based on LD50 (mg/kg) <10 very highly toxic; 10-50 highly toxic; 51-500 moderately 

toxic; 501-2000 slightly toxic; >2000 practically nontoxic 

4

 The test species is not a US EPA-recommended species for toxicity testing with terrestrial invertebrates; SEP guidelines do not 

exist for this species. 

5

 Schneider-Orelli’s formula: Corrected % = (%mortality in treated - %mortality in control) / (100-%mortality in control) *100 
23

Table 14. Chronic effect concentrations (NOAEC/LOAEC) for terrestrial animals (birds/mammals) following 

exposure to dinotefuran 

Species Measurement 

Endpoint 

Time NOAEC/ 

LOAEC 

MRID / OCSPP 

GLN# 

Birds 

Mallard duck 

Anas 

platyrhynchos 

1-generation 

reproduction; 

dietary study 

(TGAI: 99.3%) 

20 

weeks 

NOAEC: 2150 mg a.i./kg-diet 

LOAEC: 5270 mg a.i./kg-diet 

Endpoint(s) affected: number of 

hatchlings/eggs laid and set, 14-day old 

survivors/eggs set 

(Sub)lethal effects: One incidental mortality 

in control. Incidental injuries due to penwear. Reproductive effects resulted in 

endpoint determination.

45639723 

(Acceptable) 

850.2300 

Mammals 

Rat 

Rattus norvegicus 

2-Generation 

Reproduction; 

dietary study 

(TGAI: 98.9%) 

 Repro. NOAEL = 3,000 mg/kg-diet 

(241-269 mg/kg-bw/day ♂; 

267-292.6 mg/kg-bw/day ♀) 

Repro. LOAEL = 10,000 mg/kg-diet 

(822.1-934.7 mg/kg-bw/day ♂; 

907-1004.8 mg/kg-bw/day ♀) 

Endpoint(s) affected/Sublethal effects: 

Decreased uterine weights, microscopic 

alteration in uterus and vagina of Fo ♀; 

decreased numbers of primordial follicles 

in F1 ♀, altered estrous cyclicity in Fo ♀; 

slight increases in abnormal sperm 

morphology in Fo and F1 ♂, and slight 

decreases in testicular sperm count in Fo ♂

and sperm mortality in F1 ♂.

45639913 

(definitive test) 

45639914 (rangefinding test) 

(Acceptable) 

870.3800 

Rabbit 

New Zealand 

white 

Prenatal 

development; 

gavage study 

(TGAI: 92.9%) 

Average weight 

of pregnant 

females across all 

doses: 3.485 kg 

(3485 g) 

 Maternal NOAEL = 52 mg/kg-bw/day 

Maternal LOAEL = 125 mg/kg-bw/day 

Endpoint(s) affected: None. No statistically 

significant effects on developmental 

endpoints 

Sublethal effects: Maternal toxicity was 

evident at doses of 125 and 300 mg/kgbw/day. Decreased bw gain (80% of 

controls) in ♀ in the 125 mg/kg-bw/day 

group at gestation days 6-18 and transient 

decrease in food consumption (84-90% of 

controls) after initiation (gestation days 6-

10). Other findings include: liver 

discoloration, stomach plaque, transient 

neurological signs 

45654208 

(definitive test) 

45639911 (range 

finding test) 

45639912 (range 

finding test) 

(Acceptable) 

870.3700 
24

Terrestrial Plants

Terrestrial plant testing (Tier I seedling emergence OCSPP 850.4100, MRID 45639729, and 

vegetative vigor OCSPP 850.4150, MRID 45639730) on ten species indicated no effects as a 

result of a single application of LX1414-01 MTI-446 20% SG (20% dinotefuran) Lot # 01i-6252 

at a rate of 0.54 lb a.i./A. For some plants, considered endpoints exhibited reductions relative to 

the controls which were < 25% which indicates that further testing (i.e., Tier II) is not needed. 

The 14-day EC25 and NOAEL for both studies were >0.54 lb a.i./A and 0.54 lb a.i./A, 

respectively. 

RISK CHARACTERIZATION 

Aquatic Organisms 

The high solubility of Dinotefuran and DN in water (39,830 mg/L and 619,400 mg/L 

respectively), moderate persistence in the water column and soil (t1/2 = 76-79.3 days under 

aerobic aquatic conditions; t1/2 = 15-100 days in aerobic and anaerobic soils) and high mobility 

(Koc of 6-45) suggests that dinotefuran is expected to dissolve in the water column. 

Concentrations in pore water are assumed to be equivalent to those in the water column in the 

rice paddy, as well as in the receiving body (i.e., a moving stream or a stagnant pond). Based on 

the currently available aquatic ecotoxicity studies, the proposed dinotefuran use on rice exceeds 

the level of concern for estuarine/marine invertebrates on both an acute and chronic exposure 

scenarios (see Table 15). 

Table 15. RQs for Aquatic Organisms Exposed to Dinotefuran from the Proposed New Use on Rice

Taxa EECs1

 

(μg a.i./L) 

Acute Endpoint 

(LC50 in μg 

a.i./L) 

Chronic 

Endpoint 

(NOAEC in μg 

a.i./L) 

Acute RQ4 Chronic 

RQ4 

Animals 

Freshwater Fish 

269 

99100 6360 0.003 0.04 

Freshwater Invertebrate 1106003 10000 0.002 0.03 

Estuarine/Marine 

Invertebrate 790 44 0.34 6.11 

Plants 

Taxa EECs1

 

(μg a.i./L) 

Non-listed 

Species 

Endpoint 

(EC50 in μg 

a.i./L) 

Listed Species 

Endpoint 

(NOAEC in μg 

a.i./L) 

Non-listed 

Species RQ4 

Listed 

Species RQ4 

Vascular Aquatic Plants 

269 

1100003 110000 0.002 0.002 

Non-vascular Aquatic 

Plants 976003 25000 0.003 0.01 
25

1

Concentrations are based on Tier I Rice Model outputs 

2

The available acute freshwater invertebrate toxicity data for dinotefuran (Daphnid only) provides only nondefinitive toxicity values for the LC50, so this was used as an estimate for the LC50.. 3

The available aquatic plant toxicity data provides only non-definitive LC50 endpoints, so these were used as an 

estimate for the LC50. 4

Values in bold are LOC exceedances (LOC: 0.05, acute listed species; 0.1, acute restricted use; 0.5 acute; 1, 

chronic).

Terrestrial Animals 

Risk quotients (RQs) were calculated based on mammalian and avian toxicity endpoints in Table 

13 and EECs presented in Table 9. The values calculated in Appendix A reflect upper bound 

Kenaga values. No exceedances of the Agency’s Levels of Concern (LOCs) were observed for 

either acute or chronic risk to terrestrial animals for any of the proposed new uses. 

Based on the available invertebrate toxicity data, dinotefuran is very highly toxic to terrestrial 

insects and invertebrates. These organisms may be impacted from the proposed of the 

dinotefuran new use on rice, however because the proposed dinotefuran application timing 

would be post flowering, pollinator (e.g. pollen harvesting insects) exposures in the field should 

be minimized. Invertebrates resident in the field or visiting the field for food, shelter, resting 

etcetera would be considered at risk. There is also a potential for off-site exposure from spray 

drift to pose a concern for terrestrial insects and invertebrates from spray drift. 

Terrestrial Plants 

The available terrestrial plant toxicity data show little to no toxicity of dinotefuran to plants (14-

day EC25 and NOAEL for both vegetative vigor and seedling emergence studies were >0.54 lbs 

a.i./A). Based on the proposed single application rate and the annual maximum a.i./A (0.131 lbs 

a.i./A and 0.262 lbs a.i./A respectively), exceedances of the Agency’s Levels of Concern (LOCs) 

for listed or non-listed plants are not expected for the proposed new rice use. 

Endangered Species

Since dinotefuran is toxic to honeybees, it is assumed that it may also be toxic to listed terrestrial 

invertebrates (those that are federally listed as endangered or threatened). In addition, should 

invertebrate prey populations decline to a point where they would negatively impact predator 

populations, then dinotefuran applications could have indirect effects on various insectivorous 

taxa including mammals and birds, or plants that are pollinated by invertebrates. In other words, 

any listed species that relies on terrestrial invertebrates during its life-cycle may potentially be at 

risk. 

Incidents

Data on ecological incidents can be obtained through three incident databases: 1) the Ecological 

Incident Information System v. 2.1.1 (EIIS) maintained by EFED; 2) the Avian Incident 

Monitoring System (AIMS) maintained by the American Bird Conservancy; and, 3) the Incident 

Data System (IDS), a component of the PRISM database maintained by ITRMD. 
26

No incidents have been reported (i.e., no records were found) in which dinotefuran has been 

associated with some type of environmental effect; this is the case for all three incident databases 

searched, which were last run for the recent problem formulation for Registration Review 

(D389547, December 13, 2011). The absence of documented incidents does not necessarily 

mean that such incidents did not occur. 

II. Summary 

With the exception of concerns for risks to terrestrial invertebrates (e.g., pollinators), there are 

generally no risks of concern for exposures to terrestrial organisms or plants. However, based on 

the proposed rice use, EPA’s level of concern is exceeded for listed aquatic estuarine/marine 

invertebrates. These concerns for aquatic invertebrates are primarily focused on the production 

areas of the Gulf of Mexico region due to their proximity to the estuarine and marine 

environment and water management practices in this region. 

 

 
27

Appendix A. T-REX Model Inputs/Results 

Table A-1. Upper Bound Kenaga, Acute Avian Dose-Based Risk Quotients 

Size Class 

(grams) 

Adjusted 

LD50 

EECs and RQs 

Short Grass Tall Grass Broadleaf Plants Fruits/Pods/Seeds Arthropods Granivore 

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

20 1440.86 13.40 0.01 6.14 0.00 7.54 0.01 0.84 0.00 5.25 0.00 0.19 0.00 

100 1834.29 7.64 0.00 3.50 0.00 4.30 0.00 0.48 0.00 2.99 0.00 0.11 0.00 

1000 2591.00 3.42 0.00 1.57 0.00 1.92 0.00 0.21 0.00 1.34 0.00 0.05 0.00 

Table A-2. Upper Bound Kenaga, Chronic Avian Dietary Based Risk Quotients1 

NOAEC (ppm) 

EECs and RQs 

Short Grass Tall Grass Broadleaf Plants Fruits/Pods/Seeds Arthropods 

EEC RQ EEC RQ EEC RQ EEC RQ EEC RQ 

2150 11.76 0.01 5.39 0.00 6.62 0.00 0.74 0.00 4.61 0.00 1

An LC50 could not be determined from the available dietary studies. 

Table A-3. Upper Bound Kenaga, Acute Mammalian Dose-Based Risk Quotients 

Size Class 

(grams) 

Adjusted 

LD50 

EECs and RQs 

Short Grass Tall Grass Broadleaf Plants Fruits/Pods/Seeds Arthropods Granivore 

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

15 4395.66 11.21 0.00 5.14 0.00 6.31 0.00 0.70 0.00 4.39222 0.001 0.1558 4E-05 

35 3556.56 7.75 0.00 3.55 0.00 4.36 0.00 0.48 0.00 3.03561 0.0009 0.1076 3E-05 

1000 1538.32 1.80 0.00 0.82 0.00 1.01 0.00 0.11 0.00 0.70382 0.0005 0.025 2E-05 

Table A-4. Upper Bound Kenaga, Chronic Mammalian Dietary Based Risk Quotients1 

NOAEC (ppm) 

EECs and RQs 

Short Grass Tall Grass Broadleaf Plants Fruits/Pods/Seeds/Large Insects Arthropods 

EEC RQ EEC RQ EEC RQ EEC RQ EEC RQ 

4820 11.76 0.00 5.39 0.00 6.62 0.00 0.74 0.00 4.61 0.00 1

An LC50 could not be determined from the available dietary studies. 

Table A-5. Upper Bound Kenaga, Chronic Mammalian Dose-Based Risk Quotients 

Size Class 

(grams) Adjusted NOAEL 

EECs and RQs 

Short Grass Tall Grass Broadleaf Plants Fruits/Pods/Seeds Arthropods Granivore 

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

15 529.68 11.21 0.02 5.14 0.01 6.31 0.01 0.70 0.00 4.39 0.01 0.16 0.00 

35 428.57 7.75 0.02 3.55 0.01 4.36 0.01 0.48 0.00 3.04 0.01 0.11 0.00 

1000 185.37 1.80 0.01 0.82 0.00 1.01 0.01 0.11 0.00 0.70 0.00 0.02 0.00 

DP Barcode Summary
28

DP Barcode Authors Title Date 

285633 Dutta, S. and J.L. Ellis Revised Section 3 Environmental Risk Assessment for 

the Registration of Dinotefuran on Leafy Vegetable, 

Turfgrasses, Ornamentals and Residential Use. 

06/30/04 

D304957 Dutta, S. and J.L. Ellis FIFRA Section 3, Environmental Risk Assessment for 

the New Use Registration of Dinotefuran on Cotton, 

Potato, Head and stem Brassica, Fruiting Vegetables, 

Cucurbits, Grapes, Ornamental Plants and Flower Beds, 

Lawn, Shrubs and Additional Residential Uses. 

08/09/04 

324854 Patrick FIFRA Section 3, Environmental Risk Assessment for 

Increasing the Use Rates for the Registration of 

Dinotefuran on Head and Stem Brassica, Cucurbits, 

Fruiting Vegetables, Grapes, Leafy Vegetables, and 

Potatoes. 

10/16/06 

332829 Federoff, N.E. and F.A. 

Khan 

Section 18 Request for Use of Dinotefuran in Texas on 

Leafy Brassica to Control Whitefly. 

10/31/06 

355010 Meléndez, J. and N.E. 

Federoff 

Section 18 Request for Use of Dinotefuran in Texas on 

Rice to Control Rice Stink Bug. 

10/28/08 

358860 Meléndez, J. and A. 

Solliday 

Incremental Environmental Risk Assessment for IR-4 

for the Registration of Dinotefuran Use on Leafy 

Brassica (Subgroup 5B) 

06/15/09 

378125 Crk, T. and R. Parker FIFRA Section 3 New Use, Environmental Risk 

Assessment for the Registration of Dinotefuran for 

Forestry Uses (Christmas Trees, Trees in Plantations, 

Reforestation Nurseries, Forests, and Woodland Areas) 

05/03/11 

388997+ Crk, T. and R. Parker Section 18 Request for Use of Dinotefuran in VA, WV, 

DE, MD, NC, PA, and NJ on Stone Fruit and Pome 

Fruit to Control Brown Marmorated Stink Bug 

06/16/11 

390191 Crk, T. and R. Parker FIFRA Section 3 New Uses (IR-4 Petition), 

Environmental Risk Assessment for the Registration of 

Dinotefuran for bulb and green onion subgroups (3-

07A&B), low growing berry (13-07H, except 

strawberry), small fruit and vine climbing (berry) 

subgroup (13-07F, except fuzzy kiwifruit), tuberous and 

corm vegetables subgroup (1C), watercress, and peach. 

02/14/12 

389547 Crk, T., R. Parker, J. 

Hetrick, D. Spatz 

Registration Review: Problem Formulation for 

Environmental Fate, Ecological Risk, Endangered 

Species, and Drinking Water Exposure Assessments for 

Dinotefuran 

12/12/11 

283465 Dutta, S. and J.L. Ellis EFED’s Data Evaluation Records for the Registration 

Action of the Proposed Use of Dinotefuran on Leafy 

Vegetable, Turf grasses, and Residential uses 

05/13/04 

 

290192 Dutta, S. Tier I Estimated Drinking Water Concentrations of 

Dinotefuran (MTI-446) and its major transformation 

products for use in Human Health Risk Assessment 

01/21/04 

304958 Dutta, S. Tier I Estimated Drinking Water Concentrations of 

Dinotefuran (MTI-446) and its major transformation 

products for use in Human Health Risk Assessment 

06/07/04 

324853 Meléndez, J.L. Tier I Estimated Drinking Water Concentrations of 

Dinotefuran (MTI-446) and Its Transformation Products 

of Concern for Use in Human Health Risk Assessment 

09/18/06 

324854 Meléndez, J.L. Tier I Estimated Drinking Water Concentrations of 

Dinotefuran (MTI-446) and Its Transformation Products 

09/18/06 
29

DP Barcode Summary

DP Barcode Authors Title Date 

of Concern for Use in Human Health Risk Assessment 

354339 Meléndez, J.L. Tier I Estimated Drinking Water Concentrations of 

Dinotefuran (MTI-446) and It’s Transformation 

Products of Concern MNG, DN, UF and DN-2-OH + 

DN-3-OH, for Use in Human Health Risk Assessment: 

Section 18 Emergency Exemption for the Use of the 

Chemical on Rice in Texas 

04/09/09 

357111 Meléndez, J.L. Tier I Estimated Drinking Water Concentrations of 

Dinotefuran and its Transformation Products of Concern 

MNG, DN, UF and DN-2-OH + DN-3-OH, for Use in 

Human Health Risk Assessment, Proposed New (IR-4) 

Use of the Chemical on Leafy Brassica Greens and 

Turnip Greens 

01/23/2009 

378125 Parker, R. Dinotefuran Drinking Water Assessment for the 

Additional Registration of Forestry Uses 

02/01/11 

384148 Parker, R. Dinotefuran Drinking Water Assessment for the 

Additional Registration of Forestry Uses 

02/03/11 

394848 Parker, R. Tier I Human Health Drinking Water Assessment of 

Dinotefuran and its Transformation Products of Concern 

(MNG, DN, UF and DN-2-OH + DN-3-OH) in Support 

of Proposed IR-4 New Uses (Onion, Bulb and Green; 

Berry and Small Fruit; Tuberous and Corm Vegetables; 

Peach; and Watercress) 

12/12/11 

334846 Steeger, T. Review of Proposed Bee Study Protocol for Dinotefuran 03/09/07 

397490 Wolf, J.K. Tier 1 Drinking Water Concentrations for Dinotefuran 

for Section 3 new use on 

Rice. 

08/07/12