EPA REGISTRATION DIVISION COMPANY NOTICE OF FILING FOR PESTICIDE PETITIONS PUBLISHED IN THE FEDERAL REGISTER

EPA Registration Division contact: Venus Eagle, PM 1; 703

- 308

- 8045

Syngenta Crop Protection, LLC, P.O. Box 18300, Greensboro, NC 27419

- 8300

Petition N umber 5E8401

EPA has received a pesticide petition 5E8401 from Syngenta Crop Protection, LLC., P.O. Box 18300, Greensboro, NC 27419

- 8300 request ing, pursuant to section 408(d) of the Federal Food, Drug, a nd Cosmetic Act (FFDCA), 21 U.S.C. 346a(d), to amend 40 CFR part 180 by establishing a tolerance for residues of Thiamethoxam [{3

- [(2

- chloro

- 5

- thiazolyl)methyl]tetrahydro

- 5

- methyl

- N

- nitro

- 4 H

- 1,3,5

- oxadiazin

- 4

- imine} (CAS Reg. No. 153719

- 23

- 4) and i ts metabolite[ N

- (2

- chloro

- thiazol

- 5

- yl ) methyl]

- N ’

- methyl

- N ’

- nitro

- guanidine calculated as the stoichiometric equivalent of thiamethoxam in

or on the raw agricultural commodity banana at 0.04 parts per million (ppm) . EPA has determined that the petition contains data or information regarding the elements set forth in s ection 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 Chemistr y

1. Plant metabolism. The primary metabolic pathways of thiamethoxam in plants (corn, rice, pears and cucumbers) were similar to those described for animals, with certain extensions of the pathway in plants. Parent compound and CGA

- 322704 were the majo r residues in all crops. The metabolism of thiamethoxam in plants and animals is understood for the purposes of the proposed tolerances. Parent thiamethoxam and the metabolite, CGA

- 322704, are the residues of concern for tolerance setting purposes.

2. Analytical method. Syngenta Crop Protection, LLC has submitted practical analytical methodology for detecting and measuring levels of thiamethoxam in or on raw agricultural commodities. This method is based on crop specific cleanup procedures and determin ation by liquid chromatography with either UV or MS detections. The limit of detection (LOC) for each analyte of this method is 1.25 ng injected for samples analyzed by UV and 0.25ng injected for samples analyzed by MS, and the limit quantification (LOQ) is 0.005 ppm for milk and juices, and 0.01 ppm for all other substrates.

3. Magnitude of residues. One study (total of twelve crop

- field trials) were successfully conducted in Central and South America to support the registration of Thiamethoxam on banan as after treatment with four or five root zone drench applications of a suspension concentrate (SC) formulation. The nominal use pattern was a soil/root zone drench application at 180 days prior to harvest at a rate of 4 L product/ha (144 g ai/ha abamect in + 288 g ai/ha thiamethoxam) followed by thre e (or four) successive soil/root zone drench applications at a rate of 2 L2

product/ha (72 g ai/ha abamectin + 144 g ai/ha thiamethoxam) on a 60

- day retreatment interval (RTI). The initial application (4 L pro duct/ha) was intended to control the soil insects and nematodes present in previously untreated plantations and each of these sequential app l ications were made at a lower rate in order to maintain the level of control. However, it was determined that the higher initial rate wa s not commercially feasible. Banana samples were harvested 0 days after the last application (DALA). At four trial sites, additional RAC samples were collected (3, 7, 10, and 14 DALA) to generate residue decline data. Residues of abamectin, a mixture containing avermectin B1a (parent B1a + 8,9

- Z B1a) and avermectin B1b, and residues of thiamethoxam plus its metabolite CGA322704 were determined in or on banana whole fruit and banana pulp samples. Total abamectin residue levels fou nd in the whole banana fruit and banana pulp samples were below the LOQ level (<0.002 mg/kg). For the majority of the analyzed samples residues were Not Detectable (ND). Given that abamectin residues were not found in any samples in this study Syngenta d oes not intend to submit for an import tolerance for abamectin on banana. Total Thiamethoxam (Thiamethoxam + CGA322704) residue levels found in the whole banana fruit were in the range between 0.0158 and 0.0285 mg/kg and in the banana pulp were in the ran ge between 0.0158 and 0.0288 mg/kg The results of this study support the registration of the product for banana according to the GAP and provides adequate data to allow for tolerances to established for Thiamethoxam in bananas imported into the United Sta tes and Canada.

B. Toxicological Profile

1. Acute toxicity. The acute oral LD50 for thiamethoxam in the rat is 1563 mg/kg body weight. The acute dermal LD50 of thiamethoxam is >2000 mg/kg body weight. Thiamethoxam is non

- toxic at atmospheric concentra tions of 3.72 mg/l. Thiamethoxam is minimally irritating to the eye, non

- irritating to skin and is not a dermal sensitizer.

In an acute neurotoxicity study in rats (OPPTS 870.6200a), the NOAEL was 100 mg/kg/day with a NOAEL of 500 mg/kg/day based on droo ped palpebral closure, decrease in rectal temperature and locomotor activity and increase in forelimb grip strength (males only). At higher dose levels, mortality, abnormal body tone, ptosis, impaired respiration, tremors, longer latency to first step in the open field, crouched over posture, gait impairment, hypo

- arousal, decreased number of rears, uncoordinated landing during the righting reflex test, slight lacrimation (females only) and higher mean average input stimulus value in the auditory startle r esponse test (males only). ]

2. G enotoxicty. In gene mutation studies with S. typhimurium and e. coli (OPPTS 870.5100 and 870.5265), there was no evidence of gene mutation when tested up to 5000 ug/plate and there was no evidence of cytotoxicity.

In ge ne mutation study with chinese hamster V79 cells at HGPRT focus (OPPTS 8705300), there was no evidence of gene mutation when tested up to the solubility limit.3

In a CHO cell cytogenetics study (OPPTS 870.5375), there was no evidence of chromosomal aberr ations when tested up to cytotoxic or solubility limit concentrations. An in vivo mouse bonemarrow micronucleus study (OPPTS 870.5395) was negative when tested upto levels of toxicity in whole animals; however, no evidence of target cell cytoxicity was p resent. A UDS assay (OPPTS 870.5550) was negative when tested up to precipitating concentrations.

3. Reproductive and developmental toxicity. A prenatal development study in the rat (OPPTS 870.3700a) resulted in Maternal and Development NOAELs of 30 mg/k g/day and 200 mg/kg/day, respectively. The maternal LOAEL is 200 mg/kg/day based on decreased body weight, body weight gain and food consumption. The developmental LOAEL was 750 mg/kg/day based on decreased fetal body weight and an increased incidence of skeletal anomalies.

A prenatal development study in the rabbit (OPPTS 870.3700b) resulted in maternal and developmental LOAELs of 50 mg/kg/day. The maternal and developmental LOAEL is 150 mg/kg/day. The maternal LOAEL is based on maternal deaths, hemor rhagic discharge, decreased body weight and food intake during the dosing period. The developmental LOAEL is based on decreased fetal body weights, increased incidence of post

- implantation loss and a slight increase in the incidence of skeletal anomalies/ variations.

In a reproduction and fertility effects study in rats (OPPTS 870.3800) the Parental/systemic NOAEL is 1.84 (males), 202.06 (females) mg/kg/day; the reproductive NOAEL is 0.61 (males), 202.06 (females) mg/kg/day and the offspring NOAEL is 61.25 (males), 79.20 (females) mg/kg/day. The parental/systemic LOAEL is 61.25 (males), not determined (females) mg/kg/day based on increased incidence of hyaline change in renal tubules in F0 and F1 males. The reproductive LOAEL is 1.84 (males), not determin ed (females) mg/kg/day based on increased incidence and severity of tubular atrophy observed in testes of the F1 generation males. The offspring LOAEL is 158.32 (males), 202.06 (females) mg/kg/day based on reduced body weight gain during lactation period in all litters. Insert text.]

4. Subchronic toxicity. [ A 90 day oral toxicity study in rats (OPPTS 870.3100) resulted in a NOAEL of 1.74 (males), 92.5 (females) mg/kg/day. The LOAEL is 17.4 (male), 182.1 (female) mg/kg/day based on increased of hyaline change or renal tubules epithelium (males), fatty change in adrenal gland of females, liver changes in females, all at the LOAEL.

A 90 day oral toxicity in mice (OPPTS 870.3100) resulted in a NOAEL of 1.41 (males), 19.2 (females) mg/kg/day. The LOAEL was 14.3 (male), 231 (female) mg/kg/day based on increased incidence of hepatocellular hypertrophy. At higher dose levels: decrease in body weight and body weight gain, necrosis of individual hepatocytes, pigmentation of Kupffer cells, and lymphocytic infilt ration of the liver in both sexes; slight hematologic effects and decreased absolute and r elative kidney weights in males; and ovarian atrophy, decreased ovary and spleen weights and increased liver weights in females.4

In an oral toxicity in dogs (OPPTS 8 70.3150), the NOAEL is 8.23 (males), 9.27 (females) mg/kg/day. The LOAEL is 32.0 (male), 33.9 (female) mg/kg/day based on slightly prolonged prothrombin times and decreased plasma albumin and A/G ration (both sexes; decreased calcium levels and ovary weig hts and delayed maturation in the ovaries (female); decreased cholesterol and phospholipid levels, testis weights, spermatogenesis, and spermatic giant cells in testes (male)

In a 28 day dermal study in rats (OPPTS 870.3200) the NOAEL was 250 (male), 60 ( female) mg/kg/day. The LOAEL was 1000 (male), 250 (female) mg/kg/day based on increased plasma glucose, triglyceride levels, and alkaline phosphatase activity and inflammatory cell infiltration in the liver and necrosis if single hepatocyts in females and hyaline change in renal tubules and a very slight reduction in body weight in males. At higher dose levels in females, chronic tubular lesions in the kidneys and inflammatory cell infiltration in the adrenal cortex were observed. In a subchronic neurot oxicity screening study in rats (OPPTS 870.6200b) the NOAEL was 95.4 (males), 216.4 (female) mg/kg/day, both at the highest dose tested. The LOAEL was not determined. No treatment related observations at any dose level. LOAEL was not achieved. May not have been tested at sufficient high dose levels; however, a new study is not required because of the weight of evidence from other toxicity studies indicates no evidence of concern. ]

5. Chronic toxicity. In a chronic toxicity study in dogs (OPPTS 870.410 0) the NOAEL was 4.05 (male), 4.49 (female) mg/kg/day. The LOAEL was 21.0 (male), 24.6 (female) mg/kg/day based on increase in creatinine in both sexes, transient decrease in food consumption in females, and occasional increase in urea levels, decrease i n ALT, and atrophy of seminiferous tubules in males.

In a mouse carcinogenicity study (OPPTS 870.4200) the NOAEL was 2.63 (male), 3.68 (female) mg/kg/day. The LOAEL was 63.8 (male), 87.6 (female) mg/kg/day based on hepatocyte hypertrophy, single cell nec rosis, inflammatory cell infiltration, pigment disposition, foci of cellular alteration, hyperplasia of Kupffer cells and increased mitotic activity, also an increase in the incidence of hepatocellular adenoma (both sexes). At higher doses, there was an in crease in the incidence of hepatocellular adenocarcinoma (both sexes) and the number of animals with multiple tumors, evidence of carcinogenicity.

In a combined carcinogenicity study in rats (OPPTS 870.4300) the NOAEL was 21.0 (male), 50.3 (female) mg/kg /day. The LOAEL was 63.0 (male), 255 (female) mg/kg/day based on the increased incidence of lymphocytic infiltration of the renal pelvis and chronic nephropathy in males in decreased body weight gain, slight increase in the severity of hemosiderosis of t he spleen, foci of cellular alteration in liver and chronic tubular lesions in kidney in females. No evidence of carcinogenicity.

In a hepatic cell proliferation study in mice, the NOAEL was 16 (male), 20 (female) mg/kg/day. The LOAEL was 72 (male), 87 (female) mg/kg/day based on proliferative5

activity of hepatocytes. At higher dose levels, increases in absolute and relative liver weights , speckled liver, hepatocellular glycogenesis/fatty change, hepatocellular necrosis, apoptosis and pigmentation were observed.

In a 28 day feeding study to assess replicative DNA synthesis in the male rat, the NOAEL was 711 mg/kg/day. The LOAEL was not established. Immunohistochemical staining of the liver sections from control and high dose animals for proliferating cell nuclear antigen gave no indication for a treatment related increase in the fraction of DNA synthesizing hepatocytes in S

- phase. CGA

- 293343 did not stimulate hepatocyte cell proliferation in male rats.

In a special study to assess liver biochemistry in the mouse, the NOAEL was 17 (male), 20 (female) mg/kg/day. The LOAEL was 74 (male), 92 (female) mg/kg/day based on marginal to slight increases in absolute and relative liver weights, a slight increase in the microsomal protein content of the livers, moderate increases in the cytochrome P450 content, slight to moderate increases in the activity of several microsomal enzymes, slight to moderate induction of cytstolic glutathione S

- transfer activity. Treatment did not affect peroxisomal fatty acid β

- oxi dation.

6. Animal metabolism. The metabolism of thiamethoxam in rats and livestock animals is adequately understood. The residues of concern have been determined to be parent thiamethoxam and its metabolite [ N

- (2

- chloro

- thiazol

- 5

- ylmethyl)

- N ’

- methyl

- N ’

- nitro

- guanidine] expressed as thiamethoxam.

7. Metabolite toxicology

. For most risk assessment purposes, residues of the metabolite corrected for molecular weight are cons idered to be toxicologically equivalent to parent thiamethoxam. However, EPA has d etermined that the metabolite should not be included in the cancer risk assessment.

8. Endocrine disruption

. There are no specific studies requested by the Endocrine Disruptor Screening Program (EDSP) at this time because endocrine effects have been well characterized in an acceptable 2

- generation reproduction study with a clear NOAEL and LOAEL, and the chronic reference dose (cRfD) selected for thiamethoxam risk assessments is considered protective of the observed endocrine effects.

C. Aggregate Exposur e

1. Dietary exposure. Tier I acute and Tier III chronic aggregate risk assessments were performed for thiamethoxam using the Dietary Exposure Evaluation Model (DEEM

- FCID TM Version 4.02, Evaluation Copy) from Exponent; consumption data was from the USDA N HANES “What We Eat in America” survey, 2005

- 2010. These assessments included all current and pending uses as well as a proposed new banana import use. The Tier I acute assessments incorporated established or proposed tolerances (40CFR180.565) for the com bined residues of thiamethoxam (CGA293343) and its metabolite (CGA322704) in or on a variety of raw agricultural commodities including meat and milk; percent of crop treated values were conservatively estimated to be 100%6

for all uses in the acute assessme nts. The Tier III chronic assessments incorporated field trial residue values where thiamethoxam was applied at the maximum intended use rate and samples were harvested at the minimum pre

- harvest interval (PHI) to obtain the maximum expected residues. Es timated percent crop treated (%CT) values were incorporated into the Tier III chronic assessments based upon economic, pest, and competitive pressures. Drinking water estimates were incorporated directly into the acute and chronic dietary exposure assessm ents using the highest estimated drinking water concentrations (EDWCs) for surface and ground water.

i. Food. Acute Exposure . The thiamethoxam acute food risk assessments were performed for all population subgroups using an acute reference dose of 0.3 45 mg/kg

- bw/day based upon a developmental neurotoxicity study in rats with a no observed adverse effect level (NOAEL) of 34.5 mg/kg/day and an uncertainty factor of 100X to account for intra

- and inter

- species variations. No additional FQPA safety factor was applied. For the purpose of the acute aggregate risk assessments, the exposure values were expressed in terms of margin of exposure (MOE), which was calculated by dividing the NOAEL by the exposure for each population subgroup. In addition, exposure was expressed as a percent of the acute reference dose (%aRfD). At the 95th percentile, acute (food only) exposure to the U.S. population resulted in a MOE of 1,900 (5.2% of the aRfD of 0.345 mg/kg

- bw/day). The most exposed sub

- population was children ( 1

- 2 years old) with a MOE of 861 (11.4% of the aRfD of 0.345 mg/kg

- bw/day). Since the Benchmark MOE for this assessment was 100 and since the EPA generally has no concern for exposures above the Benchmark MOE or below 100% of the aRfD, Syngenta believes t hat there is a reasonable certainty that no harm will result from dietary (food only) exposure to residues arising from all current, pending, and proposed uses of thiamethoxam.

Chronic Exposure. The thiamethoxam chronic dietary food risk assessments were performed for all population subgroups using a chronic reference dose of 0.012 mg/kg

- bw/day based upon a two generation reproduction study in rats with a no observed adverse effect level (NOAEL) of 1.2 mg/kg/day and an uncertainty factor of 100X to

accoun t for intra

- and inter

- species variations. No additional FQPA safety factor was applied. For the purpose of aggregate risk assessment, the exposure values were expressed in terms of margin of exposure (MOE), which was calculated by dividing the NOAEL by the exposure for each population subgroup. In addition, exposure was expressed as a percent of the chronic reference dose (%cRfD). Chronic (food only) exposure to the U.S. population resulted in a MOE of 1,536 (6.5% of the cRfD of 0.012 mg/kg

- bw/day). T he most exposed sub

- population was children (1

- 2 years old) with a MOE of 517 (19.3% of the cRfD of 0.012 mg/kg

- bw/day). Since the Benchmark MOE for this assessment was 100 and since the EPA generally has no concern for exposures above the Benchmark MOE o r below 100% of the cRfD, Syngenta believes that there is a reasonable certainty that no harm will result from dietary (food only) exposure to residues arising from all current, pending, and proposed uses of thiamethoxam.

Cancer . A quantitative risk asse ssment using a cancer endpoint was not performed.7

ii. Drinking water

. The Estimated Drinking Water Concentrations (EDWCs) of thiamethoxam were determined using SCI

- GROW (v2.3) and Modified Tier 1 Rice Model, which estimate pesticide concentration in grou ndwater and surface water (aquatic uses), respectively. The modeling was conducted to identify the highest EDWCs of parent thiamethoxam from all current and pending uses of thiamethoxam in addition to proposed importation of banana treated with thiamethox am. For ground water, the currently registered Thiamethoxam Lawn and Landscape 0.22G use on turf ( 0.267 lb a.i./A/year) provided the highest EDWC of 4 .14 ppb (acute and chronic). The Modified Tier 1 model estimated acute and chronic surface water drinking water concentrations of 169.8 and 28.6 ppb, respectively. These surface water EDWCs resulted from the pending Endigo ® ZCX use on dry

- seeded rice (0.173 lb a.i./A) followed by 2 foliar applications (0.086 lb a.i./A/application). No percent cropped area adju stments were made to the surface water EDWCs.

Acute Exposure from Drinking Water

. The acute surface water EDWC of 169.8 ppb was input directly into the DEEM

- FCIDTM software as “water, direct and indirect, all sources” to model the acute drinking water exp osures. Exposure contributions at the 95 th percentile of exposures were determined by taking the difference between the aggregate (food + drinking water) exposures and the food (alone) exposures for each population subgroup. Acute drinking water exposure U.S. population resulted in a MOE of 5,723 (1.7% of the acute RfD of 0.345 mg/kg

- bw/day). The most exposed sub

- population was all infants with a MOE of 2,228 (4.5% of the acute RfD of 0.345 mg/kg/day). Since the benchmark MOE for this assessment was 100 and since EPA generally has no concern for exposures below 100% of the acute RfD, Syngenta believes that there is a reasonable certainty that no harm will result from acute drinking water exposure to residues arising from the current uses for thiamethoxam

. Chronic Exposure from Drinking Water

. The chronic surface water exposure value of 28.6 ppb was used as a DEEM

- FCIDTM input to determine chronic exposure from drinking water. The chronic surface water EDWC of 28.6 ppb was input directly into the DEEM

- FC IDTM software as “water, direct and indirect, all sources” to model the chronic drinking water exposures. Chronic drinking water exposure to the U.S. population resulted in a MOE of 2,077 (4.8% of the chronic RfD of 0.012 mg/kg

- bw/day). Chronic drinking w ater exposure to the most exposed sub

- population (all infants) resulted in a MOE of 556 (18.0% of the chronic RfD of 0.012 mg/kg

- bw/day). Since the Benchmark MOE for this assessment was 100 and since EPA generally has no concern for exposures below 100% o f the chronic RfD, Syngenta believes that there is a reasonable certainty that no harm will result from chronic drinking water exposure to residues arising from the current uses for thiamethoxam.

2. Non

- dietary exposure

. Residential exposure risk assess ments were performed for use of thiamethoxam formulated as Meridian 0.33G, Thiamethoxam 0.22G, Meridian 25WG, Thiamethoxam 0.40/Lambda

- cyhalothrin 0.16 ME Concentrate, Thiamethoxam 0.01/Lambda

- cyhalothrin 0.004 ME RTU, Optigard ZT, Optigard Flex, Tandem, o r Derby. Optigard ZT, Optigard Flex, Tandem, and Derby are labeled for professional use8

only; therefore no residential handler exposure assessments are required for these products. Homeowner application of Meridian 0.33G, Thiamethoxam 0.22G, Meridian 25W G, Thiamethoxam 0.40/Lambda

- cyhalothrin 0.16 ME Concentrate, or Thiamethoxam 0.01/Lambda

- cyhalothrin 0.004 ME RTU is allowed; therefore residential handler exposure assessments are required. The following endpoints were used: a 1.2 mg/kg/day NOAEL for adu lts (dermal and inhalation, all durations) from a two generation oral reproduction study in rats; a 60 mg/kg/day NOAEL for children 1

- 6 years (dermal, short

- term) from a 28

- day dermal study in rats; a 8.23 mg/kg/day NOAEL for children 1

- 6 years (oral, shor t

- term) (incidental oral, all durations) from a 90

- day oral tox study in dogs. Residential handler exposure risk from thiamethoxam was acceptable (MOE = 1,316) for adults (19+ years) treating gardens and trees with a backpack sprayer. Post

- application ex posure risk for adult gardeners (19+ years) re

- entering thiamethoxam

treated gardens and trees was acceptable (MOE = 850). Post

- application exposure risk for youth gardeners (6

- 11 years) re

- entering thiamethoxam

- treated gardens and trees was acceptable (M OE = 1,200). Post

- application exposure risk for adults (19+ years) re

entering thiamethoxam

- treated turf was acceptable (MOE = 582). Post

- application exposure risk for youth golfers (6

- 11 years) re

- entering thiamethoxam

- treated golf courses was acceptabl e (MOE = 5,416). Post

- application dermal plus non

- dietary oral hand

- to

- mouth exposure risk was acceptable for children (1

- 6 years) re

- entering thiamethoxam

- treated residential turf grass (short

- term MOE = 277). Post

- application dermal plus non

- dietary or al hand

- to

- mouth exposure risk was acceptable for children (1

- 6 years) re

- entering thiamethoxam

- treated indoor hard or carpeted surfaces areas (short

term MOE = 402). Since the MOEs for children (1

- 6 years), youths (6

- 11 years), and adults (19+ years) wer e above the Benchmark MOE of 100, residential exposure risks for thiamethoxam do not exceed the EPA’s Level of Concern.

D. Cumulative Effect

. Cumulative Exposure to Substances with a Common Mechanism of Toxicity. Section 408(b)(2)(D)(v) of FFDCA require s that, when considering whether to establish, modify, or revoke a tolerance, the Agency consider “available information” concerning the cumulative effects of a particular pesticide’s residues and “other substances that have a common mechanism of toxicity” . Unlike other pesticides for which EPA has followed a cumulative risk approach based on a common mechanism of toxicity, EPA has not made a common mechanism of toxicity finding as to thiamethoxam and any other substances and thiamethoxam does not appear t o produce a toxic metabolite produced by other substances. For the purposes of this tolerance action, the EPA has not assumed that thiamethoxam has a common mechanism of toxicity with other substances.

E. Safety Determination

1. U.S. population. The acute dietary exposure analysis (food plus water) showed that exposure from all current, pending, and proposed uses of thiamethoxam would result in a MOE of 1,426 (6.9% of the aRfD of 0.345 mg/kg

- bw/day) for the general U.S. population, which exceeds the Benchmark MOE of 100. For the short

- term aggregate9

exposure analysis the corresponding food, water and residential MOEs were aggregated using the inverse MOE approach. The short

- term aggregate (food, drinking water, and residential) MOE was 511 for adult s (20

- 49 years old), which exceeds the Benchmark MOE of 100. The chronic dietary exposure analysis (food plus water) showed that exposure from all current, pending, and proposed uses of thiamethoxam resulted in a MOE of 883 (11.3% of the cRfD of 0.012 mg/kg

- bw/day) for the general U.S. population, which also exceeds the Benchmark MOE of 100. Based on the completeness and reliability of the toxicity data supporting these petitions, Syngenta believes that there is a reasonable certainty that no harm will re sult from aggregate exposure to residues arising from all current, pending, and proposed uses of thiamethoxam, including anticipated dietary exposure from food, water, and all other types of non

- occupational
exposures.

2. Infants and children

. The acute dietary exposure analysis (food plus water) showed that exposure from all current, pending, and proposed uses of thiamethoxam would result in a MOE of 634 (15.5% of the aRfD of 0.345 mg/kg

- bw/day) for the most sensitive population subgroup, all infants, w hich exceeds the Benchmark MOE of 100. For the short

- term aggregate exposure analysis the corresponding food, water and residential MOEs were aggregated using the inverse MOE approach. The short

- term aggregate (food, drinking water, and residential) MOE was 251 for children (1

- 2 years), which exceeds the Benchmark MOE of 100. The chronic aggregate dietary (food plus water) exposure analysis showed that exposure from all current, pending, and proposed uses of thiamethoxam would result in a MOE of 283 (35. 4% of the cRfD of 0.012 mg/kg

- bw/day) for the most sensitive population subgroup, infants <1 year old, which exceeds the Benchmark MOE of 100. Based on the completeness and reliability of the toxicity data supporting these petitions, Syngenta believes tha t there is a reasonable certainty that no harm will result to infants and children from aggregate exposure to residues arising from all current, pending, and proposed uses of thiamethoxam, including anticipated dietary exposure from food, water, and all ot her types of non

- occupational
exposures.

F. International Tolerances

. In 2011 the Codex Alimentarius Commission established Maximum Residue Limits (MRLs) for thiamethoxam in various agricultural commodities including artichokes, bananas, barley, berries, Brassica vegetables (head), cacao beans, celery, citrus, coffee, fruiting vegetables, cucurbits, leafy vegetables, legumes, maize, oilseeds, papayas, pecans, peppers (chili, dried) , pineapples, pome fruits, popcorn, pulses, root and tuber vegetables, stone fruits, sweet corn, tea (green, black; fermented and dried), wheat, and various meat, milk, and egg commodities.