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**EPA REGISTRATION DIVISION COMPANY NOTICE OF FILING FOR PESTICIDE PETITIONS PUBLISHED IN THE FEDERAL REGISTER**  **EPA Registration**  **Division contact: [**  **Jennifer Gaines --**  **703 305 -**  **5967] INSTRUCTIONS:**  **Please utilize this outline in preparing the pesticide petition. In cases where the outline element does not apply, please insert “NA**  **- Remove” and**  **maintain the outline. Please do not change the margins, font, or format in your pesticide petition. Simply re**  **place the instructions that appear in green**  **, i.e., “ [**  **insert company name**  **] ,” with the information specific to your action.**  **TEMPLATE:** Makhteshim Agan of North America, Inc. [Insert petition number] EPA has received a pesticide petition ( [insert petition number] ) from Makhteshim Agan of North America, Inc , 3120 Highwoods Blvd, Suite 100, Raleigh, NC 27604 request ing, pursuant to section 408(d) of the Federal Food, Drug, and Cosmetic Act (FFDCA), 21 U.S.C. 346a(d), to amend 40 CFR part 180 B y est ablishing a tolerance for residues of Fluensulfone equivalents (i.e., the sum of thiazole sulfonic acid ( TSA ) and butene sulfonic acid ( BSA ) expressed as total fluensulfone equivalents) in or on the raw agricultural commodity fruiting vegetables at 0.6 parts per million (ppm) and cucurbits at 1.0 parts per million (ppm) . EPA has determined that the petition contains data or information regarding the elements set forth in section 408 (d)(2) of FDDCA; however, EPA has not fully

evaluated the sufficiency of the submitted data at this time or whether the data supports granting of the petition. Additional data may be needed before EPA rules on the petition. A. Residue Chemistry 1. Plant metabolism. Fluensulfone is supported by a complete plant metabol ism data package based on the proposed uses on fruiting vegetables (crop group 8) and cucurbit vegetables (crop group 9). In all plant matrices, whether from a primary or rotational crop, a clear pattern was observed with TSA ( M
- 3625 ) and BSA ( M
- 3627 ) forming the majority

of the residues following the cleavage of fluensulfone. Neither compound has acute oral toxicity greater than parent fluensulfone or shows any genotoxic potential in a range of mutagenicity studies
. The residues definition for both monitoring and risk assessment should therefore be the sum of TSA and BSA , expressed as fluensulfone equivalents.2

2. Analytical method. Adequate anal yt ical methods for determining fluensulfone in/on appropriate raw agricultural commodities and processed commodities have been developed and validated, including LC

- MS/MS methods for use on tomato, pepper, melon, and cucumber. The anal yt ical procedures have been successfully validated in terms of specificity, linearity, precision, accuracy and LOQ
. The MRM study

demonstrates that the FDA multiresidue methods (MRMs) are not suitable for detection and enforcement of fluensulfone residues as s ulfonic acid metabolites in non

- fatty

matrices. 3. Magnitude of residues. Fluensulfone is proposed for use on field grown cucurbits and fruiting vegetables. To support these uses an extensive residues package has been generated at field trial sites in the USA and Canada in 2009

- 2010
. Fluensulfone, M

- 3 6 25 (TSA) and M

- 3 6 27 (BSA) were sought in all samples. No residues of fluensulfone were detected in an y samples. The LOQ for f luensulfone and the metabolites was 0.01 mg/kg. Adequate data are available to propose tolerances ( MRL s) and there is no unacceptable risk to consumers from the consumption of crops treated with formulations containing fluensulfone
. B. Toxicological Profile 1. Acute toxicity. The acute oral LD 50 is 671 mg/kg bw in rats. The acute dermal LD 50 of fluensulfone is >2000 mg/kg bw. The acute inhalation LD 50 in rats is >5.1 mg/L. Fluensulfone displayed no eye irritation in rabbits. Fluensulfone is not irritating to the skin and is a skin sensitizer. 2. Genotoxicty. A complete data package of in vitro and in vivo mutagenicity studies is available for fluensulfone. A full summary of the genotoxicity

database is provided in the OECD Dossier. On the basis of the robust in vitro and in vivo mutagenicity

data, it is concluded that fluensulfone does not possess any genotoxic potential. 3. Reproductive and developmental toxicity

. The reproductive toxicity of fluensulfone was evaluated in a 2

- gener ation reproduction study in rats. Developmental toxicity was assessed in rats and rabbits. Reproductive toxicity . A 2
- generation reproduction study in rats was conducted at dose levels of 0, 30, 250 and 1800 ppm (2.0, 16.2, and 122.0 mg/kg/day in males and 2.8, 23.0 and 169.1 mg/kg/day in females). Treatment with fluensulfone up to and including 1800 ppm, the highest tested dose level, showed no effects on reproductive function, including gonadal function, mating behavior, fertility , viability of offsp ring, breeding, conception, gestation and parturition. Parental s ys temic toxicity was evident however, with effects on body weight3

development throughout the study observed at 1800 ppm (the LOAEL); hence the NOAEL was set at 250 ppm (equivalent to approx imately 16.2 mg/kg/day

in males and 23.0 mg/kg /day

in females). A NOAEL for general toxicity in F1 and F2 pups was established at 250 ppm, based on reduced pup weight noted at 1800 ppm. Developmental toxicity . Fluensulfone was not teratogenic or fetotox ic either in rats or rabbits. A pre
- natal developmental study in rats included dose groups of 0, 7.7, 48.6, and 292.0 mg/kg/day . Maternal toxicity , manifested as decreased body weight gain and food consumption in rats, resulted in a lower body weight of female pups; the maternal and developmental NOAEL was set at 48.6 mg/kg/day
. A pre
- natal developmental study in rabbits included dose groups of 0, 2.5, 10 and 40 mg/kg/day . Similarly, as with the study in rats, treatment of rabbits at 40 mg/kg/day resul ted in slight maternal toxicity consisting of reduction in food consumption at the onset of the treatment and between day s 18 and 24, and reduced mean body weight gain at the beginning of the treatment only . As the lower fetal weights recorded at this dose level were within the range of the historical control data, the NOAEL for maternal and developmental toxicity

was considered to be 40 mg/kg/day , the highest dose tested. 4. Subchronic toxicity. Repeated dose, oral (dietary) toxicity studies with fluensulfone are available for rats, mice and dogs. The studies conducted include 28

- day and 90

- day

studies in the rat, mouse, and dog. In addition, a 1
- ye ar oral toxicity study in dogs and a 28
- day

der mal toxicity

study in rats w ere performed. The rat 28

- day

study was conducted at dose levels of 0, 125, 500, and 2000 ppm (0, 10.4, 42.5, and 152 mg/kg/day

in males and 0, 12.2, 37.2, and 165.9 mg/kg/day in females). The NOAEL was 125 ppm (10.4 and 12.2 mg/kg day in males and females respectivel y), based on results at the LOAEL of functional effects in the liver and kidney effects, which were considered adverse as a precaution but likely of no toxicological relevance. The mouse 28

- day

study was conducted at dose levels of 0, 100, 500, and 2000 ppm (0, 30.33, 101.31, and 374.5 mg/kg/day in males and 0, 41.32, 155.12, and 353.0 mg/kg/day in females). The NOAEL was 100 ppm (30.33 and 41.32 mg/kg/day in males and females respectivel y), based on results at th e LOAELof decreased food consumption and liver toxicity

(increased relative weight, histopathological findings). The dog 28

- day

study was conducted at dose levels of 0, 50, 200, and 900 ppm (1.9, 7.3, and 30.9 mg/kg/day

in males and 2.0, 7.9, and 29.7 mg/kg/day in females). The NOAEL was 200 ppm (7.3 and 7.9 mg/kg/day in males and females respectivel y), based on results at the LOAEL of slight changes in food consumption, body weight and organ weight (liver and th yroid) and on hepatic tissue enzyme acti vities. The rat subchronic 90

- day study was conducted at dose levels of 0, 60, 120, 500 and 2000 ppm (4.31, 8.26, 34.86, and 139.01 mg/kg/day in males and 4.85, 11.68, 53.10 and 148.73 mg/kg/day

in females). The NOAEL was 120 ppm (8.3 and 11.7 mg/kg/day in4

males and females respectively), based on results at the L OAEL of decreased body weight/body weight gain in males, increased water consumption in males and increased trigl ycerides in females. The mouse subchronic 90

- day study was conducted at dose l evels of 0, 60, 300, and 1500 ppm (11.06, 50.85, and 228.53 mg/kg/day in males and 18.33, 68.47 and 252.49 mg/kg/day

in females). The NOAEL was 60 ppm (11.06 and 18.33 mg/kg/day in males and females , respectivel y), based on results at the LOAEL of decreased food consumption in females and marginal effects in liver and hematological findings in males. The dog subchronic 90

- day study was conducted at dose levels of 0, 5, 50, and 500 ppm (0.2, 1.6 and 17.1 mg/kg/day in males and 0.2, 1.8 and 18.0 mg/kg/day in females). The NOAEL was 500 ppm (17.1 and 18.0 mg/kg/day in males and females, respectivel y), based on onl y slight and reversible liver effects at the top dose tested. The rat 28

- day

dermal study

was conducted at dose levels of 0, 80, 400, and 2000 mg/kg/day

in males and females. O nl y a minimal increase in the incidence of acanthosis/hy

perkeratosis was observed at the limit dose of 2000 mg/kg/day . However, because of the moderate degree rec orded in comparison to the vehicle control, the finding was considered adaptive and likely to be reversible after cessation of treatment and on this basis not adverse. The NOAEL was 2000 mg/kg/day , the highest dose tested , based on no sy stemic or adverse d ermal effects at the highest dose level tested. In all species the liver appears to be the main target organ, although often the observed effects were limited to adaptive changes (e.g. hepatocy te h yp ertroph y concomitant to increased weight, induction of m ainly phase II activities). Investigations on liver enzy me activities in all species revealed that fluensulfone administration does not result in significant induction of (activating) phase I c yt ochrome P450 subfamilies, but that the (conjugating) phase II enzy mes were induced. Frank hepatotoxicity was observed onl y at very high doses, and only

in mice. T he NOAEL for oral subchronic toxicity is 8.3 mg/kg bw/day b ased on decreased body weights in males (and supported by increased triglycerides in females at the same dietary dose) in the 90 day

rat study . The NOAEL for dermal subchronic toxicity is 2000 mg/kg bw/day , based on absence of adverse effects at the highest test dose in the rat 28

- day dermal toxicity

study
. 5. Chronic toxicity. The long

- term toxicity and carcinogenicity

potential of fluensulfone was evaluated in dogs (one ye ar study), rats (combined study for chronic toxicity and carcinogenicity), and mice (carcinogenicity). In a 1
- ye ar oral toxicity

study in dogs, fluensulfone was administered in the diet at 0, 5, 50 100 and 500 ppm (0.1, 1.5, 3.1, and 19 mg/kg/day in males and 0.1, 1.5, 3.3, and 16.2 mg/kg/day

in females) to purebred Beagle dogs for a period of 52 weeks with selected animals retained for an 8

- week recovery period. The NOAEL was considered to be 1005

ppm (3.1 mg/kg bw/day

in males and 3.3 mg/kg bw/day in females), based on decreased body weight and body

weight gains, decreased hemoglobin, MCH, MCHC and increased kidney weights at 500 ppm (16.0 and 16.2 mg/kg/day in males and females respectivel y) in the diet. A combined chronic dietary toxicity and carcinogenicity

study in rats was conducted with 0, 30, 200, and 1200 ppm dose groups (1.6, 11 and 66.3 mg/kg/day after 52 weeks and 1.4, 9.6 and 57.7 mg/kg/day after 104 weeks in males; 1.9, 13.1 and 75.2 mg/kg/day after 52 weeks and 1.7, 11.6 and 69.3 mg/kg/day after 104 weeks in females). Fluensulfone showed no carcinogenic potential in this study , and the NOAEL for lifespan treatment (2

- ye ars) was set at 30 ppm (1.4 mg/kg/day in males and 1.7 mg/kg/day in females) on the basis of chronic interstitial inflammation in the lungs of females, decreased body weight and body weight gain in males, and decreased hemoglobin concentration and hemoglobin concentration distributi on width in females receiving 200 ppm. A 78
- week dietary

carcinogenicity

study in mice was conducted with 0, 30, 200, and 1200 ppm dose groups (4.2, 27.6 and 152.3 mg/kg/day in males and 6.4, 39.0, and 188.4 in females). The overall NOEL in mice followin g lifespan treatment was set at 30 ppm (4.2 and 6.4 mg/kg/day

in males and females, respectivel y). In mice, treatment with fluensulfone for 78 weeks resulted in an increased incidence of alveolar/bronchiolar adenomas in females receiving 200 and 1200 ppm. Mechanistic studies were carried out to determine the relevance for humans of this finding. Tumors were found to be a species

- specific effect in mice due to activation of fluensulfone b y mouse lung Clara cells, leading to local cy

totoxicity , cell proliferation and finally formation of benign tumors. Rats have lower metabolic activity in the lungs compared to mice (below the threshold needed to cause lung tumors upon lifetime exposure) and activity in humans is orders of magnitude lower than rats. Fluensul fone was found to be extensively metabolized by

mouse lung microsomes, whereas no metabolic activity was seen in human lung microsomes. Inaccordance with the International Programme on Chemical Safety (I PCS) mode of action and human relevance framework , it is concluded that fluensulfone leads to species

- specific tumors via a non

- genotoxic threshold mode of action in the mouse lung, and that these tumors are not relevant to human hazard or risk. T he NOAEL for lifespan treatment was set at 1.4 mg/kg/day on the basis of decreased body weight and body

weight gain in males (supported by chronic interstitial inflammation in the lungs and decreased hemoglobin concentration and hemoglobin concentration distribution width in females ). 6. Neurotoxicity

. Acute and subchronic specific neurotoxicity studies (i.e. inclusive of neuropathology) were carried out, and functional observation batteries (FOBs) and motor activity assessments were included in the repeated dose/chronic studies with fluensulfone. The FOBs an d motor activity assessments conducted within the repeated dose/chronic toxicity studies revealed no effects. In an acute oral neurotoxicity study in rats, groups of 10 male and 10 female Wistar rats were administered single oral doses of 0 (control), 100 , 400 and 1200 mg/kg bw of fluensulfone by

oral gavage and observed for 14 day s. No test item

- related effects on6

absolute and relative brain weights were evident , and there were no findings in the nervous s ys tem during macroscopic and microscopic patholo gy examinations. The LOAEL for general toxicity is 100 mg/kg bw in males and females, based on the general sy stemic toxicity due to the bolus dose. The NOAELfor neurotoxicity is 100 mg/kg bw in males and females, based on reduced activity in the functio nal observation battery and decreased motor activity

at 400 mg/kg in absence of any neuropathological finding at any dose level. In a subchronic dietary

neurotoxicity

study , groups of 12 male and 12 female RccHan:WI ST (SPF) rats received fluensulfone in their diet at concentrations of 0 (control), 100, 500 and 2500 ppm (0, 6, 31, and 153 mg/kg/day in males and 0, 7, 34, and 162 mg/kg/day

in females) for at least 90 day s. Treatment
- related effects were confined to lower food consumption, body weight and bo dy

weight gain in males and females at 2500 ppm. These treatment

- related effects were attributed to sy stemic toxicity , and not to neurotoxicity
. No effects on functional parameters or neurohistopathology were observed. Therefore, the high dose level of 2500 ppm was the ‘no

- observed

- effect level’ (NOEL) for neurotoxicity associated with dietary exposure, equivalent to 153 mg/kg bw/day in males and 162 mg/kg bw/ day in females. The no

- observed

- adverse

- effect level (NOAE L) for s ys temic toxicity was 500 ppm equivalent to 31 mg/kg bw/day for males and 34 mg/kg bw/day for females. As developmental studies did not indicate that the offspring are more sensitive than the adult, and neuropathological effects were not observed in an y of the performed neurotoxicity

studies, a developmental neurotoxicity study was considered not necessary
. 7. Immunotoxicity
. Although immunotoxicity endpoints were already included in the 28

- day

dietary study in rats and mice, fluensulfone was tested also in mice in the 28

- day sheep red blood cell assay , to evaluate its immunotoxicity potential. In addition, the entire available data set was examined to check immunotoxicity

- related endpoints. Itis concluded that fluensulfone is not an immunotoxic substance. 8. Animal metabolism. Fluensulfone (labeled at the thiazole and the but e ne moieties of the molecule ) administered orall y to rats at nominal single doses of either 5 mg/kg or 500 mg/kg is rapidly metabolized. The recovery of radioactivity

was essentiall y complete for all groups of rats. The disposition and excretion of radiolabel for males and females were generally

s imilar. There was no indication that the metabolic elimination processes were saturated by the 100

- fold increase in dose level, as levels of radiolabel in urine, cage wash, feces, carcass, and gastro

- intestinal (GI tract) were similar. Urine was the majo r route of excretion and the only source of metabolites at ≥5% of the applied radiolabel. The cage wash contained relatively high levels of radiolabeled metabolites and anal ys is showed that those metabolites in cage wash and urine were similar. L ow amounts of thiazole sulfonic acid were found in feces, but no other fecal metabolites were ≥5% of the applied dose. Fluensulfone is not a significant residue in either urine or feces.7

In addition to investigating metabolism after a single dose, the tissue distribution was studied when the dosing of radioactivity was preceded b y 14 days administration of unlabelled material. The results indicate that distribution is comparable in both cases. 7. Metabolite toxicology
. The acute oral LD 50 of fluen sulfone metabolite M
- 3625 was greater than 2000 mg/kg ( le ss than that of the parent fluensulfone ). Metabolite M

- 3625 was tested for its genotoxic potential in a bacterial reverse gene mutation assay , an in vitro chromosome aberration assay in mammalian cells, and an in vivo micronucleus assay

in the bone marrow of rat. No genotoxic properties were identified. The acute oral LD 50 of fluensulfone metabolite M
- 362 7 (BSA) was greater than 2000 mg/kg bw ( less than that of the parent fluensulfone )
. Metabolite M

- 3627 was tested for its genotoxic potential in a bacterial reverse gene mutation assay , an in vitro chromosome aberration assay in mammalian cells, and an in vivo micronucleus assay

in the bone marrow of rat. No genotoxic properties were identified. 8. Endocrine disruption
. Evidence from the large available toxicological data set demonstrates that fluensulfone does not exert an y adverse effects on th yroid gland, reproductive s ys tem and related endocrine organs and adrenal glands. Therefore, it is concluded that fluensulfone does not possess an y endocrine disrupting potential. C. Aggregate Exposure 1. Dietary exposure. Acute and chronic dietary (food + water) exposures to fluensulfone have been estimated for the proposed uses on cucurbits and fruiting vegetables. Drinking water concentrations have been modeled, and the resulting parent

equivalent residues were included in the dietary exposure assessment. A Tier 1 acute dietary exposure assessment was conducted assuming tolerance

- level residues, 100% crop treated and default processing factors. For chronic dietary exposures, the assessment is partially

refined since it relies on average residues and, where available, empirical processing factors, but the results are still conservative due to the assumption of 100% crop treated. A summary

of the acute and chronic reference doses (RfDs) are given in the table below: Exposure Duration Reference Dose Basis Acute 0.033 mg/kg/d LOAEL of the acute neurotoxicity study with a safety factor of 300 Chronic 0.014 mg/kg/d NOAEL of the rat chronic toxicity study with a safety factor of 1008
Acute Dietary Exposure. An acute dietary exposure assessment was performed adjusting the parent

- equivalent estimated drinking water concentrations (EDWCs)
. Th e parent - equivalent EDWCs were assumed to be 150 ppb. Existing residue data on representative cucurbit and fruiting vegetable crop s were translated to all other crops in the cucurbit and fruiting vegetable crop groups using standard EPA procedures. Acute dietary

(food + water) e xposures to fluensulfone were calculated using DEEM
- FCID ve rsion 2.16 . The reported exposures correspond to the 95th percentile of the exposure distributions, as is appropriate for a Tier 1 acute dietary exposure as sessment. The 95th percentile acute dietary (food + water) exposures are less than the aRfD (0.33 mg/kg/d)
. Acute dietary exposures below 100% o f the aRfD are reasonabl y anticipated to result in no harm to exposed populations. For infants, the most highly exposed subpopulation, 95th percentile acute dietary exposures correspond to 9.2% of the aRfD
. For the general U.S. Population, 95th percentil e acute dietary exposures correspond to 3. 7 % of the aRfD
. Chronic Dietary Exposure
. A chronic dietary exposure assessment was performed using the parent

- equivalent estimated drinking water concentrations (EDWCs). Th e parent - equivalent EDWCs were assumed to be 77 ppb
. Existing residue data on representative cucurbit and fruiting vegetable crops were translated to all other crops in the cucurbit and fruiting vegetable crop groups using standard EPA procedures. Chronic dietary

e xposures to fluensulfone were calculated using DEEM

- FCID ve rsion 2.16. C hronic dietary exposures are less than the cRfD (0.014 mg/kg/d). Chronic dietary exposures below 100% of the cRfD are reasonably anticipated to result in no harm to exposed populations. For infants, the mos t highly exposed subpopulation, chronic dietary

exposures correspond to 39.6% of the cRfD. For the general U.S. Population, chronic dietary exposures correspond to 13.6% of the cRfD
. i. Food. Exposure to fluensulfone through food is included in the dietary assessment section above. For food alone, the 95 th percentile acute dietary exposures account for just 1. 9 % and 4. 6 % of the aRfD for the U.S. population and the most highly exposed subpopulation, respectivel y. For food alone, th e chronic dietary exposures account for just 2.0% and 4.5% of the cRfD for the U.S. population and the most highly exposed subpopulation, respectivel y . ii. Drinking water
. Exposure to fluensulfone through water is included in the dietary assessment section above. The estimated residues in water constitute the majority of total dietary

exposures . 2. Non

- dietary exposure
. Fluensulfone is currentl y not registered for use on any residential non

- food site. Therefore, residential exposure to fluensulfone residues will be through dietary

exposure only
.9

D. Cumulative Effects Fluensulfone is a member of a new chemical class of nematicides with a specific toxicological profile. It does not share a known toxicological mode of action with other pesticides
. Thus, no cumulative effects are foreseen
. E. Safety Determination 1. U.S. population. Using the conservative exposure assump tions described above and based on the completeness of the toxicity data, it can be concluded that total food and drinking water exposure to fluensulfone from all proposed crop uses will be 3.7 % of the aRfD and 13.6 % of the cRfD for the overall US populati on. 2. Infants and children
. Using the conservative exposure assumptions described above and based on the completeness of the toxicity data, it can be concluded that the total acute food and drinking water exposure to fluensulfone from all proposed crop uses will be 9.2% (all infants), 6.90% (children 1

- 2 y rs), 6.1% (children 3

- 5 y

rs), and 4.30% (6

- 12 y rs) of the aRfD. It can be concluded that the total chronic food and drinking wate r exposure to fluensulfone from all proposed crop uses will be 39.6% (all infants), 21.7% (children 1

- 2 y

rs), 20.3% (children 3

- 5 y rs), and 13.9% (children 6

- 12 y rs) of the cRfD. F. International Tolerances No Codex Maximum Residue Levels (MRLs) have been established for residues of fluensulfone on an y crops. There are no established tolerances for fluensulfone on an y crops in Canada and Mexico, however, this submission is part of a Global Joint Review application involving Canada and the United Stat es.