Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 1961 1.226 0.5419 0.2224 0.1144 0.08266 0.02234 1962 0.2795 0.08307 0.05479 0.02814 0.02331 0.007364 1963 1.29 0.3988 0.1313 0.05476 0.03762 0.01108 1964 0.7698 0.2925 0.1295 0.08957 0.06589 0.02062 1965 0.8199 0.3542 0.09111 0.04263 0.0393 0.01316 1966 0.9534 0.2749 0.08134 0.0524 0.04011 0.01241 1967 0.5376 0.1777 0.1098 0.06812 0.05435 0.01709 1968 0.2626 0.08816 0.05465 0.02997 0.02208 0.007846 1969 0.793 0.2222 0.06204 0.04446 0.0331 0.01034 1970 0.5533 0.1895 0.07268 0.05353 0.04755 0.01566 1971 0.5631 0.2252 0.09425 0.05425 0.04655 0.01441 1972 0.1783 0.07947 0.05469 0.02486 0.01809 0.00693 1973 0.359 0.1188 0.05413 0.03113 0.03114 0.01187 1974 0.2453 0.09148 0.0546 0.03222 0.0285 0.01044 1975 1.963 0.5468 0.1709 0.08791 0.06441 0.01897 1976 0.6558 0.3085 0.1194 0.07679 0.06374 0.01891 1977 0.7099 0.2023 0.08756 0.0485 0.03896 0.0132 1978 0.3376 0.1514 0.07174 0.0301 0.02289 0.009309 1979 1.774 0.7277 0.2936 0.1442 0.1029 0.02968 1980 0.1773 0.07812 0.05483 0.02386 0.01644 0.005911 1981 0.7052 0.223 0.09086 0.03682 0.02992 0.01008 1982 1.041 0.3565 0.1905 0.1038 0.07313 0.02066 1983 0.6226 0.1741 0.0554 0.03716 0.02755 0.009677 1984 0.5998 0.1962 0.07937 0.05025 0.03676 0.01381 1985 1.079 0.3445 0.1131 0.08942 0.06773 0.01999 1986 0.841 0.2369 0.09571 0.04585 0.03531 0.01199 1987 0.178 0.07902 0.05456 0.02846 0.01996 0.007121 1988 0.7274 0.247 0.09384 0.05461 0.04235 0.01465 1989 0.363 0.1662 0.08456 0.0358 0.02902 0.01167 1990 0.2886 0.08093 0.05454 0.02163 0.02147 0.008993 Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly  B 37 0.1 1.2836 0.52759 0.18854 0.102377 0.07259 0.020656 Average of yearly averages: 0.0135393666666667  B 38 Pore Water Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 1961 0.0291 0.02842 0.0259 0.01946 0.01498 0.004353 1962 0.00514 0.004974 0.00372 0.003105 0.002906 0.00139 1963 0.01752 0.01711 0.01437 0.008269 0.005987 0.002038 1964 0.01741 0.01693 0.01543 0.01338 0.01098 0.004183 1965 0.01714 0.01675 0.01341 0.009093 0.007224 0.002879 1966 0.01577 0.01542 0.01232 0.008067 0.006612 0.002652 1967 0.01459 0.01421 0.0119 0.01058 0.009627 0.003717 1968 0.005172 0.005026 0.004051 0.003375 0.003 0.00173 1969 0.01123 0.01097 0.008554 0.005789 0.005011 0.001945 1970 0.01309 0.01272 0.009928 0.008609 0.007604 0.003292 1971 0.01566 0.01521 0.01244 0.008331 0.007417 0.002894 1972 0.004488 0.004355 0.003724 0.002667 0.002169 0.001289 1973 0.00803 0.007828 0.006974 0.005038 0.004481 0.00249 1974 0.007007 0.006867 0.005942 0.004918 0.004232 0.002267 1975 0.02813 0.02738 0.02346 0.0148 0.01129 0.003956 1976 0.01466 0.01433 0.01291 0.01083 0.01064 0.003964 1977 0.01287 0.01249 0.009498 0.00681 0.005971 0.002708 1978 0.007882 0.007648 0.005939 0.00363 0.002886 0.001925 1979 0.04219 0.04129 0.0358 0.02438 0.01871 0.006341 1980 0.004598 0.004438 0.0038 0.002448 0.001799 0.001054 1981 0.007944 0.007816 0.007568 0.004819 0.004242 0.00194 1982 0.02652 0.02609 0.02386 0.01662 0.01257 0.00403 1983 0.009021 0.008775 0.006835 0.004589 0.003903 0.001814 1984 0.01167 0.01139 0.008983 0.007198 0.005865 0.003053 1985 0.02354 0.02286 0.01778 0.01384 0.0118 0.004164 1986 0.01375 0.01333 0.0101 0.006364 0.005269 0.002352 1987 0.004563 0.004438 0.003687 0.003218 0.002571 0.001444 1988 0.01253 0.01218 0.009413 0.007764 0.006885 0.002919 1989 0.008801 0.008617 0.007535 0.004806 0.004178 0.002539 1990 0.004951 0.004848 0.004095 0.003063 0.002628 0.001943 Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly 0.1 0.027969 0.027251 0.02382 0.016438 0.012493 0.0041811 Average of yearly averages: 0.0027755 Sediment Levels Year Peak 96 hr 21 Day 60 Day 90 Day Yearly  B 39 1961 165 161 147 110 84.91 24.68 1962 29.14 28.2 21.09 17.6 16.48 7.882 1963 99.31 96.99 81.49 46.88 33.94 11.55 1964 98.68 95.99 87.49 75.86 62.25 23.71 1965 97.19 94.93 76.04 51.55 40.95 16.32 1966 89.37 87.43 69.86 45.73 37.49 15.04 1967 82.73 80.53 67.48 59.98 54.58 21.07 1968 29.32 28.49 22.96 19.13 17 9.81 1969 63.68 62.18 48.49 32.82 28.4 11.02 1970 74.22 72.1 56.28 48.8 43.11 18.66 1971 88.78 86.21 70.52 47.23 42.04 16.41 1972 25.44 24.69 21.11 15.12 12.3 7.31 1973 45.52 44.38 39.54 28.56 25.4 14.11 1974 39.72 38.93 33.68 27.88 23.99 12.85 1975 159 155 133 83.87 64 22.43 1976 83.11 81.23 73.19 61.42 60.3 22.47 1977 72.97 70.8 53.84 38.6 33.85 15.35 1978 44.68 43.35 33.67 20.58 16.36 10.91 1979 239 234 203 138 106 35.95 1980 26.07 25.16 21.54 13.88 10.2 5.975 1981 45.04 44.31 42.9 27.32 24.05 11 1982 150 148 135 94.2 71.28 22.84 1983 51.14 49.74 38.75 26.01 22.13 10.28 1984 66.15 64.56 50.92 40.8 33.25 17.3 1985 133 130 101 78.46 66.88 23.6 1986 77.94 75.55 57.24 36.08 29.87 13.34 1987 25.87 25.16 20.9 18.24 14.58 8.187 1988 71.02 69.04 53.36 44.01 39.03 16.55 1989 49.89 48.85 42.71 27.24 23.68 14.39 1990 28.07 27.48 23.21 17.37 14.9 11.01 Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly 0.1 158.1 154.3 134.8 93.167 70.84 23.699 Average of yearly averages: 15.7334666666667 North Carolina Cotton stored as CypermethrinNC_ new. out Chemical: Cypermethrin PRZM environment: NCcottonC. txt modified Friday, 6 December 2002 at 08: 14: 40  B 40 EXAMS environment: pond298. exv modified Thuday, 29 August 2002 at 11: 33: 30 Metfile: w13722. dvf modified Wedday, 3 July 2002 at 04: 05: 50 Water segment concentrations ( ppb)

Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 1961 0.7829 0.2425 0.102 0.06825 0.05392 0.01556 1962 1.123 0.3416 0.193 0.093 0.0679 0.02133 1963 0.4646 0.1363 0.06221 0.03189 0.02309 0.01192 1964 0.8147 0.2578 0.1027 0.07208 0.06236 0.02159 1965 1.087 0.3661 0.1297 0.08817 0.06477 0.01962 1966 0.9823 0.2828 0.1184 0.06464 0.0495 0.01525 1967 0.8511 0.2427 0.1061 0.0698 0.05526 0.01702 1968 1.376 0.4384 0.1517 0.07802 0.06104 0.02002 1969 1.21 0.4544 0.1621 0.09553 0.07375 0.02257 1970 1.175 0.3574 0.1532 0.0905 0.06618 0.01962 1971 0.7139 0.2596 0.1107 0.08362 0.06585 0.02022 1972 1.216 0.3852 0.1841 0.1017 0.07569 0.0224 1973 0.893 0.3103 0.1305 0.08329 0.06214 0.01843 1974 0.7254 0.2767 0.1034 0.06187 0.04992 0.01549 1975 2.018 0.9594 0.2575 0.1178 0.08568 0.0243 1976 0.7583 0.2149 0.06548 0.03302 0.03049 0.01162 1977 0.5815 0.1882 0.07972 0.05069 0.04471 0.01528 1978 2.25 0.6295 0.1754 0.08368 0.05959 0.018 1979 1.405 0.3984 0.1668 0.08516 0.06783 0.02081 1980 0.5809 0.1628 0.0688 0.03844 0.03463 0.01207 1981 1.092 0.3141 0.1237 0.08648 0.06831 0.02104 1982 0.3715 0.1085 0.05525 0.03841 0.02845 0.01129 1983 0.2582 0.07973 0.05498 0.02415 0.01791 0.009862 1984 1.985 0.8272 0.2946 0.1373 0.09784 0.02821 1985 2.022 0.5825 0.1573 0.09978 0.07393 0.02175 1986 0.7714 0.2769 0.11 0.08862 0.06646 0.01934 1987 0.9977 0.2836 0.1015 0.05343 0.0462 0.01524 1988 0.5768 0.1771 0.08303 0.05078 0.04612 0.01572 1989 1.176 0.3721 0.1288 0.09119 0.06951 0.02164 1990 0.3421 0.1163 0.06489 0.03195 0.02269 0.01051 Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly  B 41 0.1 2.0147 0.6248 0.19211 0.101508 0.075514 0.022553 Average of yearly averages: 0.0179240666666667 Inputs generated by pe4. pl  8 August 2003 Data used for this run:

Output File: CypermethrinNC_ new Metfile: w13722. dvf PRZM scenario: NCcottonC. txt EXAMS environment file: pond298. exv Chemical Name: Cypermethrin Description Variable Name Value Units Comments Molecular weight mwt 416.3 g/ mol Henry's Law Const. henry 3.4e 7 atm m^ 3/ mol Vapor Pressure vapr 2.5e 9 torr Solubility sol 0.04 mg/ L Kd Kd mg/ L Koc Koc 141700 mg/ L Photolysis half life kdp 36.2 days Half life Aerobic Aquatic Metabolism kbacw 11.3 days Halfife Anaerobic Aquatic Metabolism kbacs 19.3 days Halfife Aerobic Soil Metabolism asm 62 days Halfife Hydrolysis: pH 5 0 days Half life Hydrolysis: pH 7 0 days Half life Hydrolysis: pH 9 1.9 days Half life Method: CAM 2 integer See PRZM manual Incorporation Depth: DEPI 0 cm Application Rate: TAPP 0.112 kg/ ha Application Efficiency: APPEFF 0.95 fraction Spray Drift DRFT .039 fraction of application rate applied to pond Application Date Date 1 7 dd/ mm or dd/ mmm or dd mm or dd mmm Interval 1 interval 3 days Set to 0 or delete line for single app.

Interval 2 interval 3 days Set to 0 or delete line for single app.

Interval 3 interval 3 days Set to 0 or delete line for single app.

Interval 4 interval 3 days Set to 0 or delete line for single app.

Interval 5 interval 3 days Set to 0 or delete line for single app.

Record 17: FILTRA IPSCND 3 UPTKF Record 18: PLVKRT  B 42 PLDKRT .13 FEXTRC 0.5 Flag for Index Res. Run IR Pond Flag for runoff calc. RUNOFF none none, monthly or total( average of entire run)

Write Benthic Porewater File? benthic 1 Write Benthic Sediment File? benthicsed 1  B 43 Pore Water Levels Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 1961 0.01876 0.0183 0.01594 0.01209 0.009726 0.003203 1962 0.02464 0.02421 0.02246 0.01609 0.01268 0.004845 1963 0.007875 0.007813 0.007134 0.005915 0.004872 0.002889 1964 0.01569 0.01545 0.0141 0.01209 0.01178 0.005392 1965 0.02282 0.02226 0.01806 0.01457 0.01197 0.004524 1966 0.0197 0.0192 0.01624 0.01111 0.008782 0.003382 1967 0.01713 0.01669 0.01409 0.01146 0.009762 0.003876 1968 0.02208 0.02165 0.018 0.01285 0.01085 0.004547 1969 0.03042 0.02973 0.02557 0.01748 0.01447 0.005446 1970 0.02093 0.02039 0.01762 0.01543 0.01248 0.004455 1971 0.01815 0.01772 0.01586 0.01331 0.01223 0.004589 1972 0.02823 0.02764 0.02289 0.01795 0.0147 0.005083 1973 0.02154 0.02106 0.01826 0.01437 0.01156 0.004081 1974 0.01995 0.01946 0.01571 0.01125 0.009192 0.003591 1975 0.04467 0.04365 0.0355 0.02154 0.01638 0.005312 1976 0.01135 0.01115 0.009681 0.007534 0.00656 0.002763 1977 0.01342 0.01307 0.01035 0.00919 0.007934 0.003608 1978 0.02998 0.02931 0.02311 0.01409 0.01061 0.003832 1979 0.0274 0.02678 0.02262 0.01563 0.01284 0.004748 1980 0.01081 0.01058 0.008538 0.006821 0.005754 0.0027 1981 0.01967 0.01923 0.01723 0.01295 0.01215 0.0048 1982 0.008075 0.007864 0.007291 0.005305 0.004422 0.002586 1983 0.005045 0.005017 0.004849 0.004331 0.003709 0.002301 1984 0.04902 0.04781 0.04 0.02559 0.01938 0.006527 1985 0.02996 0.02923 0.02362 0.01758 0.01391 0.004809 1986 0.02077 0.02026 0.0182 0.01496 0.01209 0.004274 1987 0.0167 0.01631 0.01545 0.01125 0.009337 0.00349 1988 0.01442 0.01416 0.01255 0.009416 0.008187 0.003732 1989 0.02261 0.02212 0.01788 0.01519 0.01307 0.004926 1990 0.006863 0.006767 0.006015 0.004777 0.003923 0.002356 Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly 0.1 0.030376 0.029688 0.025375 0.017913 0.014677 0.005384 Average of yearly averages: 0.0040889 Sediment Levels Year Peak 96 hr 21 Day 60 Day 90 Day Yearly  B 44 1961 106 104 90.33 68.56 55.14 18.16 1962 140 137 127 91.23 71.86 27.47 1963 44.64 44.29 40.44 33.53 27.62 16.38 1964 88.96 87.59 79.95 68.55 66.78 30.57 1965 129 126 102 82.58 67.84 25.64 1966 112 109 92.08 62.98 49.79 19.17 1967 97.1 94.62 79.85 64.95 55.34 21.97 1968 125 123 102 72.85 61.53 25.78 1969 172 169 145 99.12 82.04 30.87 1970 119 116 99.91 87.48 70.72 25.25 1971 103 100 89.91 75.46 69.34 26.01 1972 160 157 130 102 83.34 28.82 1973 122 119 104 81.46 65.54 23.13 1974 113 110 89.06 63.78 52.11 20.36 1975 253 247 201 122 92.85 30.11 1976 64.36 63.2 54.88 42.71 37.19 15.66 1977 76.06 74.09 58.69 52.1 44.98 20.45 1978 170 166 131 79.85 60.15 21.72 1979 155 152 128 88.62 72.78 26.92 1980 61.29 59.96 48.4 38.66 32.62 15.3 1981 112 109 97.66 73.42 68.9 27.21 1982 45.78 44.58 41.33 30.08 25.07 14.66 1983 28.6 28.44 27.49 24.55 21.02 13.04 1984 278 271 227 145 110 37 1985 170 166 134 99.68 78.88 27.26 1986 118 115 103 84.82 68.57 24.23 1987 94.65 92.47 87.58 63.8 52.93 19.78 1988 81.72 80.28 71.14 53.38 46.41 21.16 1989 128 125 101 86.12 74.1 27.93 1990 38.91 38.36 34.1 27.08 22.24 13.35 Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly 0.1 171.8 168.7 143.9 101.768 83.21 30.524 Average of yearly averages: 23.1786666666667 Texas Cotton Surface Water Levels stored as CypermethrinTX_ new. out Chemical: Cypermethrin  B 45 PRZM environment: TXcottonC. txt modified Friday, 6 December 2002 at 08: 25: 18 EXAMS environment: pond298. exv modified Thuday, 29 August 2002 at 11: 33: 30 Metfile: w13958. dvf modified Wedday, 3 July 2002 at 04: 06: 24 Water segment concentrations ( ppb)

Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 1961 0.6156 0.1983 0.08781 0.03552 0.02836 0.007487 1962 0.4891 0.1116 0.04363 0.02398 0.01833 0.005078 1963 0.1703 0.06588 0.0435 0.01636 0.01112 0.002922 1964 0.1706 0.06616 0.04377 0.01675 0.01358 0.004304 1965 0.2287 0.06618 0.04375 0.01705 0.014 0.004543 1966 0.2397 0.06609 0.04366 0.02512 0.0182 0.004839 1967 0.1705 0.06612 0.04386 0.01799 0.01512 0.004825 1968 0.3529 0.1348 0.06078 0.02374 0.01738 0.004999 1969 0.2323 0.06588 0.0435 0.02336 0.01658 0.004618 1970 0.1706 0.06628 0.04383 0.01662 0.0121 0.003507 1971 0.3063 0.104 0.04355 0.02596 0.01807 0.004815 1972 0.1708 0.06659 0.04579 0.01783 0.01218 0.00355 1973 0.3332 0.1285 0.05836 0.02268 0.01923 0.006616 1974 0.494 0.119 0.04376 0.02982 0.02185 0.006387 1975 0.1805 0.09172 0.04972 0.02065 0.01532 0.004637 1976 0.2577 0.09046 0.05447 0.0213 0.01772 0.005298 1977 0.1704 0.06604 0.04362 0.01646 0.01202 0.003359 1978 0.217 0.06585 0.04348 0.02048 0.01508 0.004343 1979 1.11 0.2589 0.1066 0.05246 0.0363 0.009494 1980 0.1701 0.06554 0.04323 0.01625 0.01193 0.003362 1981 0.2103 0.08754 0.04931 0.01875 0.01536 0.004892 1982 0.1703 0.06582 0.04346 0.01633 0.01103 0.00304 1983 0.3609 0.1082 0.05489 0.02249 0.01589 0.004327 1984 0.1704 0.06601 0.0436 0.01647 0.01118 0.003906 1985 0.1974 0.07084 0.04547 0.01726 0.01284 0.004376 1986 0.2175 0.06589 0.04351 0.01641 0.01392 0.00484 1987 0.3724 0.08637 0.04798 0.01919 0.01761 0.005054 1988 0.1706 0.06631 0.04392 0.01701 0.01147 0.00301 1989 0.1705 0.06606 0.04366 0.01809 0.01244 0.00336 1990 0.2164 0.0998 0.05133 0.01994 0.01356 0.004222 Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly  B 46 0.1 0.49351 0.13417 0.060538 0.029434 0.021588 0.0065931 Average of yearly averages: 0.004667 Inputs generated by pe4. pl  8 August 2003 Data used for this run:

Output File: CypermethrinTX_ new Metfile: w13958. dvf PRZM scenario: TXcottonC. txt EXAMS environment file: pond298. exv Chemical Name: Cypermethrin Description Variable Name Value Units Comments Molecular weight mwt 416.3 g/ mol Henry's Law Const. henry 3.4e 7 atm m^ 3/ mol Vapor Pressure vapr 2.5e 9 torr Solubility sol 0.04 mg/ L Kd Kd mg/ L Koc Koc 141700 mg/ L Photolysis half life kdp 36.2 days Half life Aerobic Aquatic Metabolism kbacw 11.3 days Halfife Anaerobic Aquatic Metabolism kbacs 19.3 days Halfife Aerobic Soil Metabolism asm 62 days Halfife Hydrolysis: pH 9 1.9 days Half life Method: CAM 2 integer See PRZM manual Incorporation Depth: DEPI 0 cm Application Rate: TAPP 0.112 kg/ ha Application Efficiency: APPEFF 0.95 fraction Spray Drift DRFT .039 fraction of application rate applied to pond Application Date Date 1 7 dd/ mm or dd/ mmm or dd mm or dd mmm Interval 1 interval 3 days Set to 0 or delete line for single app.

Interval 2 interval 3 days Set to 0 or delete line for single app.

Interval 3 interval 3 days Set to 0 or delete line for single app.

Interval 4 interval 3 days Set to 0 or delete line for single app.

Interval 5 interval 3 days Set to 0 or delete line for single app.

Record 17: FILTRA IPSCND 1 UPTKF Record 18: PLVKRT PLDKRT .13 FEXTRC 0.5  B 47 Flag for Index Res. Run IR Pond Flag for runoff calc. RUNOFF none none, monthly or total( average of entire run)

Write Benthic Porewater File? benthic 1 Write Benthic Sediment File? benthicsed 1  B 48 Pore Water Levels Year Peak 96 hr 21 Day 60 Day 90 Day Yearly 1961 0.01119 0.01078 0.008992 0.005252 0.004434 0.001335 1962 0.005421 0.005166 0.003975 0.002469 0.002288 0.0008119 1963 0.003179 0.003056 0.002475 0.001438 0.001027 0.000334 1964 0.003292 0.003169 0.002587 0.001558 0.001385 0.0006677 1965 0.003279 0.00316 0.002574 0.001612 0.001413 0.000783 1966 0.00515 0.004945 0.00386 0.002903 0.002437 0.0008033 1967 0.003262 0.003142 0.002558 0.001743 0.00176 0.0008056 1968 0.006208 0.006078 0.005233 0.002962 0.002342 0.0008904 1969 0.003776 0.003633 0.002949 0.002329 0.002035 0.0007132 1970 0.003314 0.003194 0.002607 0.001557 0.001253 0.0005053 1971 0.006321 0.006094 0.004598 0.003134 0.002462 0.0007371 1972 0.003581 0.003471 0.002917 0.001837 0.001341 0.0005213 1973 0.00564 0.00549 0.00481 0.003403 0.002702 0.001236 1974 0.007482 0.007202 0.005413 0.003813 0.003271 0.001213 1975 0.004475 0.004321 0.003569 0.002223 0.001882 0.0008138 1976 0.005325 0.005155 0.004156 0.002616 0.002404 0.0009618 1977 0.003228 0.003108 0.002525 0.001485 0.001162 0.0004752 1978 0.003639 0.003485 0.002635 0.002116 0.001745 0.000624 1979 0.01734 0.01672 0.01388 0.008231 0.006116 0.001774 1980 0.003074 0.002943 0.002369 0.00138 0.001083 0.0004292 1981 0.004017 0.003862 0.003315 0.001945 0.001824 0.000791 1982 0.003164 0.003038 0.002459 0.001429 0.001016 0.000359 1983 0.005875 0.005637 0.004192 0.002627 0.001987 0.0006448 1984 0.003217 0.003097 0.002516 0.001485 0.001158 0.00058 1985 0.003543 0.003421 0.002835 0.001685 0.001353 0.0007293 1986 0.003183 0.003059 0.002479 0.001778 0.001621 0.0008269 1987 0.004292 0.004149 0.003289 0.002033 0.002172 0.0008989 1988 0.003313 0.003193 0.002601 0.00159 0.00114 0.0003619 1989 0.003242 0.003121 0.002538 0.001638 0.001313 0.0004159 1990 0.005033 0.004855 0.003661 0.002167 0.00156 0.0006245 Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly 0.1 0.0073659 0.0070912 0.005395 0.003772 0.0032141 0.0012337 Average of yearly averages: 0.000755566666666667 Sediment Levels Year Peak 96 hr 21 Day 60 Day 90 Day Yearly  C 1 1961 63.41 61.11 50.97 29.77 25.13 7.568 1962 30.73 29.29 22.53 13.99 12.97 4.603 1963 18.02 17.32 14.03 8.152 5.823 1.893 1964 18.66 17.97 14.66 8.832 7.852 3.785 1965 18.59 17.91 14.59 9.138 8.012 4.439 1966 29.19 28.03 21.88 16.46 13.81 4.554 1967 18.49 17.81 14.5 9.882 9.978 4.567 1968 35.19 34.45 29.67 16.79 13.28 5.048 1969 21.41 20.59 16.72 13.2 11.54 4.043 1970 18.79 18.11 14.78 8.828 7.106 2.865 1971 35.83 34.55 26.07 17.76 13.96 4.179 1972 20.3 19.68 16.54 10.41 7.605 2.955 1973 31.97 31.12 27.27 19.29 15.32 7.007 1974 42.41 40.83 30.69 21.62 18.54 6.876 1975 25.37 24.49 20.23 12.6 10.67 4.613 1976 30.19 29.22 23.56 14.83 13.63 5.453 1977 18.3 17.62 14.31 8.416 6.589 2.694 1978 20.63 19.76 14.94 12 9.894 3.537 1979 98.29 94.78 78.71 46.66 34.67 10.06 1980 17.43 16.68 13.43 7.824 6.141 2.433 1981 22.77 21.9 18.79 11.03 10.34 4.484 1982 17.93 17.22 13.94 8.098 5.758 2.035 1983 33.31 31.96 23.76 14.89 11.26 3.655 1984 18.24 17.56 14.26 8.418 6.563 3.288 1985 20.08 19.39 16.07 9.55 7.671 4.134 1986 18.04 17.34 14.05 10.08 9.188 4.688 1987 24.33 23.52 18.64 11.52 12.32 5.096 1988 18.78 18.1 14.74 9.014 6.465 2.051 1989 18.38 17.69 14.39 9.283 7.444 2.358 1990 28.53 27.52 20.75 12.29 8.844 3.54 Sorted results Prob. Peak 96 hr 21 Day 60 Day 90 Day Yearly .1 41.752 40.202 30.588 21.387 18.218 6.9939 Average of yearly averages: 4.28336666666667 APPENDIX C. TerrPlant Model   Input, Results, Output No plant toxicity data were submitted, therefore, TerrPlant was not run for this assessment.  C 2  D 1 APPENDIX D. T REX Model ( T REX Version 1.12, December 7, 2004)   Input, Results, Output The model output from T REX for cypermethrin is provided in the attached Microsoft Excel spreadsheets:

° Cypermethrin_ T REX_ cotton_ v1.12. xls ° Cypermethrin_ T REX_ lettuce_ v1.12. xls ° Cypermethrin_ T REX_ pecans_ v1.12. xls ° Cypermethrin_ T REX_ rape_ v1.12. xls 1. Introduction This spreadsheet based model calculates the decay of a chemical applied to foliar surfaces for single or multiple applications. It uses the same principle as the batch code models FATE and TERREEC for calculating terrestrial estimates exposure ( TEEC) concentrations on plant surfaces following application. A first order decay assumption is used to determine the concentration at each day after initial application based on the concentration resulting from the initial and additional applications. The decay is calculated by from the first order rate equation:

CT = Cie kT or in log form:

ln ( CT/ Ci) = kT Where:

CT = concentration at time T = day zero.

Ci = concentration, in parts per million ( PPM) present initially ( on day zero) on the surfaces. Ci is calculated based on Kenaga and Fletcher by multiplying the Ci based on the Kenega nomogram ( Hoerger and Kenaga, ( 1972) as modified Fletcher ( 1994). For maximum concentration the application rate, in pounds active ingredient per acre, is multiplied by 240 for Short Grass, 110 for Tall Grass, and 135 for Broad leafed plants/ small insects and 15 for fruits/ pods/ lg insects. Additional applications are converted from pounds active ingredient per acre to PPM on the plant surface and the additional mass added to the mass of the chemical still present on the surfaces on the day of application.

k = If the foliar dissipation data submitted to EFED are found scientifically valid and statistically robust for a specific pesticide, the 90% upper confidence limit of the mean half lives should be used. When scientifically valid, statistically robust data are not available TETT recommends the using a default half life value of 35 days. The use of the 35 day half life is based on the highest reported value ( 36.9 days) reported by Willis and McDowell ( Pesticide persistence on foliage, Environ. Contam. Toxicol, 100: 23 73, 1987).  D 2 T = time, in days, since the start of the simulation. The initial application is on day 0. The simulation is designed to run for 365 days.

The program calculates concentration on each type of surface on a daily interval for one year. The maximum concentration during the year are calculated for both maximum and mean residues. The inputs used to calculate the amount of the chemical present are in highlighted in light blue on the spread sheet. Outputs are in yellow. The inputs required are:

Application Rate: The maximum label application rate ( in pounds ai/ acre)

Half life: The degradation half life for the dominate process( in days)

Frequency of Application: The interval between repeated applications, from the label ( in days)

Maximum # Application per year: From the label The calculated concentrations are used to calculate Avian and Mammalian RQ values. The maximum calculated concentration is divided by user input values for acute and chronic endpoints to give RQs for each type of plant surface.

2. Avian Species For calculating dose based RQs in birds, the maximum and mean Kenaga residue values are adjusted for avian class and food consumption based on the following scaling factor ( USEPA, 1993):

FI ( g/ d) = 0.648 ( g bw)^ 0.651 For the 3 avian weight classes considered ( 20, 100 and 1000 g), this results in % body weight consumption of:

Weight( g) FI wet FI % bw consumed 20 4.555599463 22.77799731 114 100 12.98897874 64.94489369 65 1000 58.15338588 290.7669294 29  D 3 A. Dose Based Acute RQs Dose based acute RQs are then calculated using the formula:

RQ = adjusted EEC/ LD50 or NOAEL where the adjusted EEC is considered to be the daily dose weighted for % body weight consumed of a given food source.

B. Dietary Based RQs For dietary based RQs, two values are given for each food group. First, the consumption weighted RQ for each weight class ( 20, 100, and 1000g birds) is displayed and calculated using the equation:

RQ = EEC/(( LC50 or NOAEC)/(% bw consumed))

In the second method, no adjustment is made for consumption differences among the weight classes. This RQ is calculated:

RQ = EEC/ LC50 or NOAEC 3. Mammalian Species A. Dose Based RQs For calculating dose based RQs in mammals, the maximum and mean Kenaga values are adjusted for mammalian class and food consumption ( 0.95, 0.66 and 0.15 body weight for herbivores and insectivores and 0.21, 0.15, and 0.03 body wt. for granivores). Dose based acute and chronic RQs are then calculated by dividing the adjusted EECs ( daily dose) by the LD50 or NOAEL.

B. Dietary Based RQs Dietary based RQs are calculated using the equation:

RQ = EEC/(( LC50 or NOAEC)/(% bw consumed))

4. Graph  D 4 A graph of concentration on each plant surface vs time is plotted and a concentration of concern line can be added at a user specified level. The concentration of concern ( e. g., avian LC50, mammalian NOAEL) label should be entered in the cell underneath the value. The graph automatically plots a line at this concentration and the label is extracted from that cell. The graph is plotted for the first 100 days post application. Graphs displaying acute and chronic LOCs for both birds and mammals are displayed in the " Graph" worksheet. These graphs may be useful as a visual aid to communicate risk in your assessment and can be copy/ pasted into your document. To help with scaling issues on the y axis, you may want to delete one of the endpoints.

5. New Version Notes A new look is used in this update in an effort to decrease confusion and increase transparency in the risk assessment process. This version of T REX ( v1.12) incorporates the ability to calculate EECs and RQs for maximum and mean residues. Mean residues are calculated exactly as the maximum residues are, except the corresponding Kenaga values are: 85 for Short Grass, 36 for Tall Grass, and 45 for Broad leafed plants/ small insects and 7 for fruits/ pods/ lg insects.

6. References Fletcher, J. S., J. E. Nellesson and T. G. Pfleeger. 1994. Literature review and evaluation of the EPA food chain ( Kenaga) nomogram, an instrument for estimating pesticide residues on plants. Environ. Tox. and Chem. 13( 9): 1383 1391.

Hoerger, F. and E. E. Kenaga. 1972. Pesticide residues on plants: correlation of representative dada as a basis for estimation of their magnitude in the environment. IN: F. Coulston and F. Corte, eds., Environmental Quality and Safety: Chemistry, Toxicology and Technology. Vol 1. Georg Theime Publishers, Stuttgart, Germany. pp. 9 28.

USEPA. 1993. Wildlife Exposure Factors Handbook. Volume I of II. EPA/ 600/ R 93/ 187a. Office of Research and Development, Washington, D. C. 20460. Willis and McDowell. 1987. Pesticide persistence on foliage. Environ. Contam. Toxicol. 100: 23 73.  E 1 Acute and Chronic RQs are based on the Upper Bound Kenaga Residues.

Chemical Name: The maximum single day residue estimation is used for Use both the acute and reproduction RQs. Formulation Application Rate 0.1 lbs a. i./ acre Half life 60 days Application Interval 3 days Maximum # Apps./ Year 6 Length of Simulation 1 year Concentration of Concern 150.00 ( ppm) Name of Concentration of Concern 2000 Note: To provide risk management with the maximum possible information,

20000 it is recommended that both the dose based and concentration based RQs be calculated when data are available 50 247 Note: To provide risk management with the maximum possible information,

0 it is recommended that both the dose based and concentration based 7.5 RQs be calculated when data are available 150 Kenaga Values Short Grass 132.28 Tall Grass 60.63 Broadleaf plants/ sm Insects 74.41 Fruits/ pods/ seeds/ lg insects 8.27 Avian Results Avian Body % body wgt Adjusted Class Weight consumed LD50 Small 20 114 1416 Mid 100 65 1803 Large 1000 29 2546 small mid large 20 g 100 g 1000 g Short Grass 151 86 38 Tall Grass 69 39 18 Broadleaf plants/ sm Insects 85 48 22 Fruits/ pods/ lg insects 9 5 2 20 g 100 g 1000 g Short Grass 0.11 0.05 0.02 Tall Grass 0.05 0.02 0.01 Broadleaf plants/ sm insects 0.06 0.03 0.01 Fruits/ pods/ lg insects 0.01 0.00 0.00 Acute Chronic Short Grass 0.01 2.65 Tall Grass 0.00 1.21 Broadleaf plants/ sm Insects 0.00 1.49 Fruits/ pods/ lg insects 0.00 0.17 Dose based RQs ( daily dose/ LD50) Avian Acute RQs RQs Upper Bound Kenaga Residues For RQ Calculation Avian Classes and Body Weights EEC equivalent dose ( mg/ kg bw) EECs ( ppm) NOAEL ( mg/ kg bw) NOAEC ( mg/ kg diet) Mammals LD50 ( mg/ kg bw) Cypermethrin Cotton Bobwhite quail LC50 ( mg/ kg diet) Mammal chronic NOAEC Bobwhite quail LD50 ( mg/ kg bw) Endpoints Bobwhite quail NOAEL ( mg/ kg bw)

LC50 ( mg/ kg diet) Avian Bobwhite quail NOAEC ( mg/ kg diet)

Dietary based RQs ( EEC/ LC50 or NOAEC) T REX Output for Cypermethrin Application to Cotton  E 2 T REX Output for Cypermethrin Application to Lettuce  E 3 Acute and Chronic RQs are based on the Upper Bound Kenaga Residues.

Chemical Name: The maximum single day residue estimation is used for Use both the acute and reproduction RQs. Formulation Application Rate 0.1 lbs a. i./ acre Half life 60 days Application Interval 7 days Maximum # Apps./ Year 0.6 Length of Simulation 1 year Concentration of Concern 150.00 ( ppm) Name of Concentration of Concern 2000 Note: To provide risk management with the maximum possible information,

20000 it is recommended that both the dose based and concentration based RQs be calculated when data are available 50 247 Note: To provide risk management with the maximum possible information,

0 it is recommended that both the dose based and concentration based 7.5 RQs be calculated when data are available 150 Kenaga Values Short Grass 24.00 Tall Grass 11.00 Broadleaf plants/ sm Insects 13.50 Fruits/ pods/ seeds/ lg insects 1.50 Avian Results Avian Body % body wgt Adjusted Class Weight consumed LD50 Small 20 114 1416 Mid 100 65 1803 Large 1000 29 2546 small mid large 20 g 100 g 1000 g Short Grass 27 16 7 Tall Grass 13 7 3 Broadleaf plants/ sm Insects 15 9 4 Fruits/ pods/ lg insects 2 1 0 20 g 100 g 1000 g Short Grass 0.02 0.01 0.00 Tall Grass 0.01 0.00 0.00 Broadleaf plants/ sm insects 0.01 0.00 0.00 Fruits/ pods/ lg insects 0.00 0.00 0.00 Acute Chronic Short Grass 0.00 0.48 Tall Grass 0.00 0.22 Broadleaf plants/ sm Insects 0.00 0.27 Fruits/ pods/ lg insects 0.00 0.03 Dose based RQs ( daily dose/ LD50) Avian Acute RQs RQs Upper Bound Kenaga Residues For RQ Calculation Avian Classes and Body Weights EEC equivalent dose ( mg/ kg bw) EECs ( ppm) NOAEL ( mg/ kg bw) NOAEC ( mg/ kg diet) Mammals LD50 ( mg/ kg bw) Cypermethrin Lettuce Bobwhite quail LC50 ( mg/ kg diet) Mammal chronic NOAEC Bobwhite quail LD50 ( mg/ kg bw) Endpoints Bobwhite quail NOAEL ( mg/ kg bw)

LC50 ( mg/ kg diet) Avian Bobwhite quail NOAEC ( mg/ kg diet)

Dietary based RQs ( EEC/ LC50 or NOAEC)

T REX Output for Cypermethrin Application to Canola  E 4 Acute and Chronic RQs are based on the Upper Bound Kenaga Residues.

Chemical Name: The maximum single day residue estimation is used for Use both the acute and reproduction RQs. Formulation Application Rate 0.1 lbs a. i./ acre Half life 60 days Application Interval 4 days Maximum # Apps./ Year 0.4 Length of Simulation 1 year Concentration of Concern 150.00 ( ppm) Name of Concentration of Concern 2000 Note: To provide risk management with the maximum possible information,

20000 it is recommended that both the dose based and concentration based RQs be calculated when data are available 50 247 Note: To provide risk management with the maximum possible information,

0 it is recommended that both the dose based and concentration based 7.5 RQs be calculated when data are available 150 Kenaga Values Short Grass 24.00 Tall Grass 11.00 Broadleaf plants/ sm Insects 13.50 Fruits/ pods/ seeds/ lg insects 1.50 Avian Results Avian Body % body wgt Adjusted Class Weight consumed LD50 Small 20 114 1416 Mid 100 65 1803 Large 1000 29 2546 small mid large 20 g 100 g 1000 g Short Grass 27 16 7 Tall Grass 13 7 3 Broadleaf plants/ sm Insects 15 9 4 Fruits/ pods/ lg insects 2 1 0 20 g 100 g 1000 g Short Grass 0.02 0.01 0.00 Tall Grass 0.01 0.00 0.00 Broadleaf plants/ sm insects 0.01 0.00 0.00 Fruits/ pods/ lg insects 0.00 0.00 0.00 Acute Chronic Short Grass 0.00 0.48 Tall Grass 0.00 0.22 Broadleaf plants/ sm Insects 0.00 0.27 Fruits/ pods/ lg insects 0.00 0.03 Dose based RQs ( daily dose/ LD50) Avian Acute RQs RQs Upper Bound Kenaga Residues For RQ Calculation Avian Classes and Body Weights EEC equivalent dose ( mg/ kg bw) EECs ( ppm) NOAEL ( mg/ kg bw) NOAEC ( mg/ kg diet) Mammals LD50 ( mg/ kg bw) Cypermethrin Canola Bobwhite quail LC50 ( mg/ kg diet) Mammal chronic NOAEC Bobwhite quail LD50 ( mg/ kg bw) Endpoints Bobwhite quail NOAEL ( mg/ kg bw)

LC50 ( mg/ kg diet) Avian Bobwhite quail NOAEC ( mg/ kg diet)

Dietary based RQs ( EEC/ LC50 or NOAEC)  E 5 T REX Output for Cypermethrin Application to Pecans  E 6 Acute and Chronic RQs are based on the Upper Bound Kenaga Residues.

Chemical Name: The maximum single day residue estimation is used for Use both the acute and reproduction RQs. Formulation Application Rate 0.1 lbs a. i./ acre Half life 60 days Application Interval 5 days Maximum # Apps./ Year 0.6 Length of Simulation 1 year Concentration of Concern 150.00 ( ppm) Name of Concentration of Concern 2000 Note: To provide risk management with the maximum possible information,

20000 it is recommended that both the dose based and concentration based RQs be calculated when data are available 50 247 Note: To provide risk management with the maximum possible information,

0 it is recommended that both the dose based and concentration based 7.5 RQs be calculated when data are available 150 Kenaga Values Short Grass 24.00 Tall Grass 11.00 Broadleaf plants/ sm Insects 13.50 Fruits/ pods/ seeds/ lg insects 1.50 Avian Results Avian Body % body wgt Adjusted Class Weight consumed LD50 Small 20 114 1416 Mid 100 65 1803 Large 1000 29 2546 small mid large 20 g 100 g 1000 g Short Grass 27 16 7 Tall Grass 13 7 3 Broadleaf plants/ sm Insects 15 9 4 Fruits/ pods/ lg insects 2 1 0 20 g 100 g 1000 g Short Grass 0.02 0.01 0.00 Tall Grass 0.01 0.00 0.00 Broadleaf plants/ sm insects 0.01 0.00 0.00 Fruits/ pods/ lg insects 0.00 0.00 0.00 Acute Chronic Short Grass 0.00 0.48 Tall Grass 0.00 0.22 Broadleaf plants/ sm Insects 0.00 0.27 Fruits/ pods/ lg insects 0.00 0.03 Dose based RQs ( daily dose/ LD50) Avian Acute RQs RQs Upper Bound Kenaga Residues For RQ Calculation Avian Classes and Body Weights EEC equivalent dose ( mg/ kg bw) EECs ( ppm) NOAEL ( mg/ kg bw) NOAEC ( mg/ kg diet) Mammals LD50 ( mg/ kg bw) Cypermethrin pecans Bobwhite quail LC50 ( mg/ kg diet) Mammal chronic NOAEC Bobwhite quail LD50 ( mg/ kg bw) Endpoints Bobwhite quail NOAEL ( mg/ kg bw)

LC50 ( mg/ kg diet) Avian Bobwhite quail NOAEC ( mg/ kg diet)

Dietary based RQs ( EEC/ LC50 or NOAEC) APPENDIX E. Ecological Effects Data I. Categories of Acute Toxicity  E 7 In general, categories of acute toxicity ranging from " practically nontoxic" to " very highly toxic" have been established for aquatic organisms ( based on LC50 values), terrestrial organisms ( based on LD50 values), avian species ( based on LC50 values), and non target insects ( based on LD50 values for honey bees) ( EPA 2001).

Categories of acute toxicity for aquatic organisms can be classified according to the toxicity reference value ( LC50) given by a study:

LC50 ( ppm) Toxicity Category < 0.1 Very highly toxic 0.1  1 Highly toxic > 1  10 Moderately toxic > 10  100 Slightly toxic > 100 Practically nontoxic Categories of acute toxicity for mammalian species can be classified according to the toxicity reference value ( LD50) given by a study:

LD50 ( mg a. i./ kg) Toxicity Category < 10 Very highly toxic 10  50 Highly toxic 51  500 Moderately toxic 501  2000 Slightly toxic > 2000 Practically nontoxic  E 8 For avian species, categories of acute toxicity for can also be classified according to the toxicity reference value ( LC50) given by a study:

LC50 ( ppm) Toxicity Category < 50 Very highly toxic 50  500 Highly toxic 501  1000 Moderately toxic 1001  5000 Slightly toxic > 5000 Practically nontoxic The following toxicity category descriptions were developed by Atkins ( 1981) and have been used by EFED to characterize honey bee acute contact toxicity values ( EPA, 2001):

LD50 (: g a. i./ bee) Toxicity Category < 2 Highly toxic 2 < 11 Moderately toxic > 11 Practically nontoxic II. Toxicity to Freshwater Aquatic Animals a. Freshwater Fish, Acute Two freshwater fish toxicity studies using the TGAI are required to establish the acute toxicity of cypermethrin to fish. The preferred test species are bluegill sunfish ( a warmwater fish) and rainbow trout ( a coldwater fish). Acute toxicity studies using cypermethrin TGAI have been submitted for rainbow trout ( 7 studies), bluegill sunfish ( 4 studies), brown trout ( 1 study), carp ( 1 study), and rudd ( 1 study); results are summarized in Table E 1a. The 96 hour LC50 values reported in these studies range from 0.39 : g a. i./ L in rainbow trout ( MRID 44546027; Acceptable) to 4.5 : g a. i./ L in bluegill sunfish ( MRID 44546030; Acceptable), indicating that cypermethrin TGAI is very highly toxic to freshwater fish. Taking the most conservative approach, EFED will use the lowest 96 hour LC50 of 0.39 : g a. i./ L in rainbow trout to evaluate acute toxic exposure to freshwater fish. The guideline ( § 72 1) is fulfilled.

In addition to lethality endpoints, sublethal effects of acute cypermethrin ( TGAI) exposure were assessed in studies in rainbow trout ( 3 studies) and bluegill sunfish ( 3 studies). The sublethal signs of toxicity reported were rapid and erratic swimming, partial/ complete loss of equilibrium, jaw spasms, gulping respiration, lethargy, and darkened pigmentation. The NOAEC values for sublethal effects ranged from < 0.00068 : g a. i./ L in rainbow trout ( Acc. No.  E 9 241598, Acceptable) to 2.1 : g a. i./ L in bluegill sunfish ( MRID 44546030; Acceptable). For two studies, the NOAEC value for sublethal effects was several orders of magnitude lower than the LC50 value; in rainbow trout, the NOAEC and LC50 values were 0.00068 : g a. i./ L and 0.8 : g a. i./ L, respectively ( Acc No. 241598; Acceptable), and in bluegill sunfish, the NOAEC and LC50 values were < 0.0022 : g a. i./ L and 2.2 : g a. i./ L, respectively ( MRID 241598; Supplemental). Thus, sublethal effects can occur at exposure levels far below the concentrations that cause lethality.

Studies assessing the acute toxicity of three cypermethrin formulations in rainbow trout were submitted; results are summarized in Table E 1b. The formulations tested were WL 43467 40% EC ( 40% a. i.), GFU 061 (% a. i. not reported), and GFU 070 ( 25.1% a. i.). The 96 hour LC50 values were reported for GFU 061 and GFU 070 are 4.7 : g formulation/ L ( MRID 65813; Supplemental) and 13.0 : g formulation/ L ( MRID 88947; Acceptable), respectively, indicating that these cypermethrin formulations are very highly toxic to freshwater fish. Sublethal effects reported include loss of equilibrium, quiescence, darkening pigmentation and coughing. Based on these results, cypermethrin TGAI and the cypermethrin formations tested appear to have a degree of toxicity to freshwater fish on an acute basis. Results of the study using WL 43467 40% EC show that toxicity of cypermethrin is decreased in unfiltered pond water ( for both lethality and sublethal effects), compare to microfiltered pond water from which suspended solids have been removed ( MRID 89036; Supplemental). The authors suggest that the reduced toxicity in unfiltered pond water is due to adsorption of cypermethrin to suspended solids, resulting in decreased concentrations of cypermethrin in water.

Acute toxicity studies in freshwater fish were also submitted for the cypermethrin degradate 3 phenoxy benzoic acid in rainbow trout ( MRID 89037; Acceptable) and bluegill sunfish ( MRID 89038; Acceptable). Results yield 96 hour LC50 values of 13.3 and 36.3 mg degradate/ L in rainbow trout and bluegill sunfish, respectively ( Table E 1c). Based on these 96 hour LC50 values, 3 phenoxy benzoic acid is categorized as slightly toxic to freshwater fish on an acute basis. Thus, the 3 phenoxy benzoic acid degradate is much less toxic than cypermethrin TGAI to freshwater fish.  E 10 Table E 1a: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Freshwater Fish Species % a. i. LC50 Toxicity Category Identification Number Study Classification Technical Grade Cypermethrin Salmo gairdneri ( rainbow trout)

. 92.9 Flow through test conditions. Concentrations tested: 0.00068, 0.001, 0.0015, 0.0033, 0.0047, 0.01, 0.047, 0.10, and 0.47 µ g a. i./ L ( no controls indicated).

The first symptoms noted at all concentrations were rapid swimming with frequent thrashing of the body. In all cases this was followed by exaggerated and involuntary jaw spasms. After death all fish were seen to have pronounced spinal curvature and blackening of the dorsal area.

24 hr LC50 = 5.3 ppb a. i. (: g a. i./ L)

48 hr LC50 = 2.0 ppb a. i. (: g a. i./ L)

96 hr LC50 = 0.8 ppb a. i. (: g a. i./ L) Very highly toxic Accession No. 241598 ( Hill et al. 1976) Acceptable Salmo gairdneri ( rainbow trout) 91.5 Flow through test conditions. Concentrations ( nominal) tested: 0, 0 ( DMSO solvent), 0.32, 0.56, 0.75, 1.0 1.8, 2.4, 3.2 and 4.2 µ g a. i./ L. Mean measured concentrations: 0.14, 0.25, 0.43, 0.55, 1.08, 1.49, 1.95, and 3.35 µ g a. i./ L.

24 hr LC50 = 1.73 ppb a. i. (: g a. i./ L)

48 hr LC50 = 1.00 ppb a. i. (: g a. i./ L)

96 hr LC50 = 0.92 ppb a. i. (: g a. i./ L) ( 95% C. I. = 0.81 1.05) Very highly toxic MRID 62792 ( ICI 1980); same study reported in unclassified MRID 92027011 ( Treacy 1990) Acceptable Table E 1a: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Freshwater Fish Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 11 Oncorhynchus mykiss ( rainbow trout; formerly Salmo gairdneri) 98.4 Flow through test conditions. Concentrations ( nominal) tested: 0, 0 ( acetone solvent control), 0.31, 0.52, 0.87, 1.5, and 2.4 µ g a. i./ L. Mean measured concentrations: 0.25, 0.42, 0.71, 1.1, and 2.0 µ g a. i./ L.

Sublethal signs of test material toxicity were limited to partial/ complete loss of equilibrium, which was observed in the four highest concentration treatments.

96 hr LC50 = 1.1 ppb a. i. (: g a. i./ L) ( 95% C. I. = 1.0  1.3)

NOAEC ( sublethal effects) = 0.25 ppb a. i. (: g a. i./ L) Very highly toxic MRID 44546028 ( Sousa, 1998) Acceptable Lepomis macrochirus ( bluegill sunfish) 98.4 Flow through test conditions. Concentrations ( nominal) tested: 0, 0 ( acetone solvent control), 1.4, 2.4, 4.0, 6.6, and 11 µ g ai/ L. Mean measured concentrations: 1.3, 2.1, 3.1, 4.7, 8.1 µ g a. i./ L.

Fish exposed at the three highest concentration treatment levels demonstrated signs of toxicity which included partial/ complete loss of equilibrium, lethargy, and erratic swimming behavior.

96 hr LC50 = 4.5 ppb ai (: g a. i./ L) ( 95% C. I.: 4.0  5.3 ppb ai)

NOAEC ( sublethal effects) = 2.1 ppb ai (: g a. i./ L) Very highly toxic MRID 44546030 ( Sousa, 1998) Acceptable Table E 1a: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Freshwater Fish Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 12 Lepomis macrochirus ( bluegill sunfish) 91.5 Flow through test conditions. Concentrations ( nominal or measured unspecified) tested: 0.35, 0.71, 1.44, 1.93, 2.38, and 3.17 ( no units; ppb a. i. are assumed, given the units reported for NOAEC).

96 hr LC50 = 1.78 units assumed to be ppb a. i. (: g a. i./ L) ( 95% C. I. = 1.63 1.95) ( based on mean measured concentrations). Very highly toxic MRID 65812 ( ICI 1980) Acceptable Lepomis macrochirus ( bluegill sunfish) 92.9 Flow through test conditions.

Concentrations tested ( nominal or measured unspecified): 0.0022, 0.0047, 0.01, 0.022, 0.047, and 0.1 mg a. i./ L At all concentrations, fish were seen to swim with greater rapidity of movement. Other toxic symptoms included jaw spasms and the tendency to swim with the head up and the tail down.

24 hr LC50 value = 7.2 ppb a. i. (: g a. i./ L)

48 hr LC50 value = 3.7 ppb a. i. (: g a. i./ L)

96 hr. LC50 = 2.2 ppb a. i. (: g a. i./ L)

Note: LC50 values given in this study were not determined by probit analysis. Very highly toxic Accession No. 241598 ( Hill et al., 1973) Supplemental Technical Cypermethrin ( FMC 45806) Table E 1a: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Freshwater Fish Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 13 Oncorhynchus mykiss ( Rainbow trout ) 91.5 Flow through test conditions. Concentrations ( nominal) tested: 0, 0 ( DMF solvent control), 0.39, 0.65, 1.08, 1.80, and 3.00 µ g a. i./ L. Mean measured concentrations:

0.219, 0.366, 0.719, 1.35, and 2.24 µ g a. i./ L 96 hour LC50 = 0.90 µ g a. i./ L ( based on mean measured concentration) ( 95% C. I.: 0.72 1.35). Very highly toxic MRID 41968209 ( Vaishnav and Yurk, 1990) Acceptable Cypermethrin S ( Fury Technical) ( FMC 56701)

Oncorhynchus mykiss ( rainbow trout) 88.2 Flow through test conditions. Concentrations ( nominal) tested: 0, 0 ( DMF solvent control), 0.70, 1.17, 1.94, 3.24, and 5.40 µ g a. i./ L. Mean measured concentrations: 0.47, 0.82, 1.65, 2.77, and 5.27 µ g a. i./ L.

96 hour LC50 = 0.69 µ g a. i./ L ( based on mean measured concentration)( 95% C. I. = 0.60 0.82).

NOAEC could not be determined due to mortality at all concentrations. Very highly toxic MRID 41968208 ( Overman et al., 1990) Acceptable Table E 1a: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Freshwater Fish Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 14 14C labeled Beta cypermethrin Oncorhynchus mykiss ( rainbow trout) tech > 95% Radio chemical purity. Flowthrough test conditions. Concentrations ( nominal) tested: 0, 0 ( acetone solvent control), 0.13, 0.22, 0.36, 0.60, and 1.0 µ g a. i./ L ( 17% radiolabeled material and 83% unlabeled material). Mean measured concentrations: 0.11, 0.16, 0.27, 0.42, and 0.8 µ g a. i./ L.

Signs of test material toxicity observed at all but the lowestconcentration included partial/ complete loss of equilibrium, gulping respiration, erratic swimming, surfacing, darkened pigmentation, and lethargy.

96 hour LC50 = 0.39 ppb a. i. ( µ g a. i./ L) ( 95% C. I.: 0.27 0.80)

NOAEC ( sublethal effects) = 0.11 ppb a. i. ( µ g a. i./ L) Very highly toxic MRID No. 44546027 ( Sousa, 1998) Acceptable Table E 1a: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Freshwater Fish Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 15 Lepomis macrochirus ( bluegill) tech > 95% Radio chemical Purity. Flowthrough test conditions. Concentrations ( nominal) tested: 0, 0 ( acetone solvent control), 1.3, 2.1, 3.5, 5.9, and 9.8 µ g ai/ L ( 0.87% radiolabeled material and 99.13% unlabeled material). Mean measured concentrations: 0.61, 1.0, 1.6, 2.4, 4.4 µ g a. i./ L.

Signs of test material toxicity observed at all but the lowest concentration included partial or complete loss of equilibrium and lethargy.

96 hour LC50 = 1.2 ppb ai ( µ g a. i./ L) ( 95% C. I.: 1.0 1.3)

NOAEC ( sublethal effects) = 0.61 ppb ai. ( µ g a. i./ L) Very highly toxic MRID No. 44546029 ( Sousa, 1998) Acceptable Table E 1b: Acute Toxicity of Cypermethrin Formulations to Freshwater Fish Species % a. i. LC50 Toxicity Category Identification Number Study Classification WL 43467 ( 40% EC) Table E 1b: Acute Toxicity of Cypermethrin Formulations to Freshwater Fish Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 16 Salmo gairdneri ( rainbow trout) 40 96 hr exposure period; static or flow through not indicated. Trout were exposed to 2 and 5 µ g/ L nominal concentrations in microfiltered water or pond water. 1.7 and 4.9 µ g/ L measured in microfiltered water. 1.2 and 4.0 µ g/ L measured in pond water.

After 3 hrs. in the 1.7 and 4.9 µ g/ L WL 43467 microfiltered water, fish showed signs of loss of balance, tail drop, and erratic swimming; fish appeared normal after 24 hr. At 1.7 µ g/ L WL 43467, one fish was found dead after 48 hr. At 4.9 µ g/ L WL 43467, all fish ( 6) were dead after 24 hr exposure.

There were no signs of toxicity and no mortalities in fish exposed to 1.2 or 4.9 µ g/ L WL 43467 in pond water during the 96 hr. exposure period.

The authors conclude that the observed reductions of toxicity and lethal effect of WL 43467 to the fish in pond water was due to the absorption of the compound onto suspended solids, thereby becoming less bio available to the fish. NA MRID 89036 ( Reiff et al., 1978) Supplemental Table E 1b: Acute Toxicity of Cypermethrin Formulations to Freshwater Fish Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 17 Formulation GFU 061 Salmo gairdneri ( Rainbow trout) 22.0 cis: trans ratio = 54: 46. Flowthrough test conditions. Concentrations ( nominal) tested: 0, 1.0, 2.4, 3.2 5.6, 7.5, 10.0, 15.5, 21.0, 24.0 µ g GFU/ L. Mean measured concentrations: 0.60, 1.53, 1.90, 4.27, 6.02, 8.07, 13.1, 16.5, and 16.6 µ g GFU/ L.

24 hour LC50 = 18.3 µ g GFU/ L ( 95% C. I. = 14.3 23.4)

48 hour LC50 = 6.3 µ g GFU/ L ( 95% C. I. = 5.7 6.9)

96 hour LC50 = 4.7 µ g GFU/ L ( 95% C. I. = 4.1 5.4)

NOAEC ( lethality) = 1.53 µ g GFU/ L Very highly toxic MRID 65813 ( Hill et al., 1980) Supplemental Formulation GFU 070 Table E 1b: Acute Toxicity of Cypermethrin Formulations to Freshwater Fish Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 18 Salmo gairdneri ( Rainbow trout) 25.1 Flow through test conditions. Concentrations ( nominal) tested: 1.8 3.2, 5.6, 10, 18, 32, and 56 µ g./ L as GFU 070. Mean measured concentrations: 1.15, 2.24, 4.75, 7.69, 18.0, 34.9, and 64.7 µ g/ L No mortalities observed at the three lowest treatment levels ( 1.15, 2.24, and 4.75 µ g/ L mean measured concentrations). General toxic symptoms noted were loss of equilibrium, quiescence, surfacing, darkening in color, and coughing.

96 hour LC50 = 13.0 µ g GFU 070/ L ( based upon mean measured concentrations) ( 95% C. I.: 10.9 15.3) Very highly toxic MRID 88947 ( Hill, 1981) Acceptable Table E 1c: Acute Toxicity of Cypermethrin Degradates to Freshwater Fish Species % a. i. LC50 Toxicity Category Identification Number Study Classification Cypermethrin Degradation Product 3 phenoxybenzoic Acid Table E 1c: Acute Toxicity of Cypermethrin Degradates to Freshwater Fish Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 19 Salmo gairdneri ( Rainbow trout) 99.0 Concentrations tested: 0, 0 ( DMSO solvent control), 3.5, 5.5, 10.0, 17.7, 33.7, and 56.7 ppm 3 phenoxy benzoic acid ( mg/ L)

96 hr static acute LC50 = 13.3 ppm 3 phenoxy benzoic acid/ L ( mg/ L ) ( 95% C. L. = 11.2 and 15.8)

96 hr NOAEL = 5.5 ppm 3 phenoxy benzoic acid / L ( mg/ L) Slightly toxic MRID 89037 ( Hill and Young, 1981) Acceptable Lepomis macrochirus ( bluegill) 99.0 Concentrations tested: 0, 0 ( DMSO solvent control), 5.7, 9.3, 16.8, 28.8, 44.6, and 52.7 ppm 3 phenoxy benzoic acid ( mg/ L)

96 hr static acute LC50 = 36.3 ppm 3 phenoxy benzoic acid ( mg/ L) ( 95% C. L. = 33.3 and 39.5) Slightly toxic MRID 89038 ( Hill et. al, 1981) Acceptable b. Freshwater Fish, Chronic A freshwater fish early life stage test using the TGAI is required for cypermethrin because end use products could contaminate surface water through drift or runoff events and, may be transported to water from the intended use site. An early life stage study in fathead minnow was submitted by the registrant to establish the chronic toxicity of cypermethrin to freshwater fish ( MRID 89039; Acceptable); data are summarized in Table E 2. Results of this 30 day exposure study show that survival was significantly reduced compare to controls at 0.33 : g a. i./ L, yielding a 30 day NOAEC value for survival of 0.14 : g a. i./ L. No treatment related effects were observed for hatchability or growth. The NOAEC value for survival of 0.14 : g a. i./ L will be used to assess the risk of chronic exposure of freshwater fish to cypermethrin TGAI. The guideline ( § 72 4) is fulfilled.

No chronic toxicity studies of cypermethrin formulations or cypermethrin degradates in freshwater fish were submitted.  E 20 Table E 2: Chronic Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Freshwater Fish Species % a. i. Toxicity Value Identification Number Study Classification Technical Grade Cypermethrin Pimephales promelas ( fathead minnow) 91.5 30 day chronic toxicity test to early life stage fathead minnows under flow through conditions.

Concentrations ( nominal) tested: 0, 0 ( unidentified solvent control), 0.031, 0.062, 0.12, 0.25, and 0.50 : g a. i./ L. Mean measured concentrations: 0.048, 0.045, 0.063, 0.14, and 0.33 µ g a. i./ L.

Survival significantly different from controls at 0.33 µ g a. i./ L.

Survival LOAEC = 0.33 µ g a. i./ L Survival NOAEC = 0.14 µ g a. i./ L MRID 89039 ( Jaber and Hawk 1981) Acceptable c. Freshwater Invertebrates, Acute A freshwater aquatic invertebrate toxicity study using the TGAI is required to establish the toxicity of cypermethrin to freshwater invertebrates. The preferred test species is the water flea ( Daphnia magna). Four acute toxicity studies using cypermethrin TGAI have been submitted for water flea; results are summarized in Table E 3a. Acute toxicity values range from the 48 hour LC50 value of 0.42 : g a. i./ L ( MRID 44546031; Acceptable) to the 24 hour EC50 value ( for immobility) of 2.0 : g a. i./ L ( Acc. No. 42444601; Supplemental). Based on these results, cypermethrin TGAI is categorized as very highly toxic on an acute basis. EFED will take the most conservative approach and use the lowest LC50 values reported, the 48 hour LC50 value of 0.42 : g a. i./ L,, to assess acute risk to freshwater invertebrates. The guideline ( § 72 2) is fulfilled.

In addition to lethality endpoints, sublethal effects of acute cypermethrin ( TGAI) exposure were described in two studies in the waterflea. Sublethal signs of toxicity reported include lethargy and lying on the bottom of the test vessels; NOAEC values for sublethal endpoints range from 0.085 : g a. i./ L ( MRID 44546032; Acceptable) and 0.14 : g a. i./ L ( MRID 44546031).

Studies assessing the acute toxicity of three cypermethrin formulations in the water flea were submitted; results are summarized in Table E 3b. The formulations tested were GFU 034/ A ( 36% a. i.), GFU 061 ( 36% a. i.), and GFU 070 ( 24% a. i.). Results of these studies were reported as EC50 values, rather than LC50 values. The 48 hour EC50 values ranged from 1.56 : g a. i./ L ( MRID 62793; Supplemental) to 21.6 : g a. i./ L ( MRID 89040; Supplemental),  E 21 indicating that these cypermethrin formulations are very highly toxic to freshwater invertebrates on an acute basis. Sublethal effects reported in these studies include immobilization and decreased movement response to stimulation. Based on these results, cypermethrin TGAI and the cypermethrin formulations tested appear to have a degree of toxicity to freshwater fish on an acute basis.

Acute toxicity tests in freshwater invertebrates were also submitted for the cypermethrin degradate 3 phenoxy benzoic acid in the water flea. Results yield 48 hour EC50 values of 89.0 mg degradate/ L ( MRID 152739; Acceptable) and 111 mg degredate/ L ( Acc. No. 42444601, Acceptable). Based on these acute toxicity values, 3 phenoxy benzoic acid is categorized as practically non toxic to slightly toxic to freshwater invertebrates on an acute basis. Thus, the 3 phenoxy benzoic acid degradate is much less toxic than cypermethrin TGAI to freshwater invertebrates.

Table E 3a: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Freshwater Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification Technical Grade Cypermethrin Daphnia magna ( water flea, first instar) 91.5 Static test conditions. Concentrations tested: 0.05, 0.17, 0.38, 0.61, 1.6, and 2.8 ( units not given, no control) ( units are probably µ g a. i./ L based on units reported for toxicity endpoints)

48 hr EC50 = 1.01 µ g a. i./ L ( based on mean measured concentrations) ( 95% C. I. = 0.80 1.31) Very highly toxic MRID 62793 ( ICI 1980) Acceptable Daphnia magna ( water flea) 95.7 Flow through test conditions. Concentrations tested: 0, 0 ( DMF solvent control), 84, 139, 232, 387, 645, and 1075 ng a. i./ L 48 hr EC50 = 161.5 ug a. i./ L ( 95% C. I. = 134.4  191.7) ( based on nominal concentrations)

NOAEC could not be determined due to mortality in the lowest test concentration. Very highly toxic MRID 43293501 ( Wheat and Evans, 1994) Acceptable Table E 3a: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Freshwater Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 22 Daphnia magna ( water flea, first instar) 98.4 Flow through test conditions. Concentrations tested: 0, 0, ( acetone solvent control), 0.11, 0.23, 0.46, 0.92, and 1.8 µ g a. i./ L. Mean measured concentrations: 0.085, 0.14, 0.29, 0.55, 1.2 µ g a. i./ L Sublethal signs of test material toxicity were limited to lethargy and lying on the bottom of the test vessel; effects observed in the 0.14, 0.29, and 0.55 µ g a. i./ L treatments.

48 hour EC50 = 0.48 ppb a. i. ( µ g a. i./ L) ( based on mean measured concentrations) ( 95% C. I. = 0.39  0.60)

NOAEC ( sublethal effects) = 0.085 ppb a. i. ( µ g a. i./ L) Very highly toxic MRID 44546032 ( Putt, 1998) Acceptable Cypermethrin Technical ( WL 43467)

Daphnia magna ( water flea) 84.6 24 hr test results given; no other study details given.

Daphnia magna ( water flea;< 24 hr old)

24 hr EC50 = 2.0 µ g a. i./ L 24 hr LC50 = 2 µ g a. i./ L Very highly toxic Accession No. 42444601 ( Stephenson 1980) Supplemental Table E 3a: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Freshwater Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 23 14C labeled Betacypermethrin Daphnia magna ( water flea, first instar) > 95 Flow through test conditions. Concentrations tested: 0, 0 ( acetone solvent control), 0.094, 0.19, 0.38, 0.75, and 1.5 µ g a. i./ L Mean measured concentrations: 0.057, 0.14, 0.25, 0.50, and 1.1 µ g a. i./ L Sublethal signs of test material toxicity were limited to lethargy; observed at the three highest test concentrations.

48 hr EC50 = 0.42 ppb a. i. ( µ g a. i./ L) ( based on mean measured concentrations) ( 95% C. I = 0.36  0.50 ppb ai)

NOAEC ( lethality/ immobilization) = 0.14 ppb a. i. ( µ g a. i./ L) Very highly toxic MRID 44546031 ( Putt, 1998) Acceptable Table E3b: Acute Toxicity of Cypermethrin Formulations to Freshwater Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification Cypermethrin Formulation GFU 034/ A Table E3b: Acute Toxicity of Cypermethrin Formulations to Freshwater Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 24 Daphnia magna ( water flea, first instar) 36% Static test conditions.

Concentrations tested: 0.05, 0.22, 0.79, 3.8 ( units not given, no control) ( µ g formulated product/ L or a. i./ L)

Units reported as follows for endpoints:

48 hr EC50 = 1.56 µ g a. i./ L ( 95% C. I. = 1.17 2.10) =

4.33 µ g formulated product/ L Very highly toxic MRID 62793 ( ICI 1980) Supplemental Table E3b: Acute Toxicity of Cypermethrin Formulations to Freshwater Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 25 Cypermethrin Formulation GFU 061 Daphnia magna ( water flea, first instar) 36% cis: trans = 53.6: 46.4.

Nominal concentrations ranged from 0.06  260 µ g a. i./ L ( control used). Measured concentrations ranged from 0.05  341 µ g a. i./ L.

Daphnia were recorded as affected if they were immobilized or showed only minor movements after stimulation.

Values for immobilization

24 hr EC50 = > 341 µ g a. i./ L 48 hr EC50 = 21.6 µ g a. i./ L 72 hr EC50 = 0.83 µ g a. i./ L Very highly toxic MRID 89040 ( Edwards et al., 1980) Supplemental Cypermethrin Formulation GFU 070 Daphnia magna ( water flea, first instar) 24% cis: trans = 55: 45. Nominal concentrations ranged from 0.03  240 µ g a. i./ L ( control used). Measured concentrations ranged from 0.05  230 µ g a. i./ L.

Daphnia were recorded as affected if they were immobilized or showed only minor movements after stimulation.

Values for immobilization

24 hr EC50 = > 240 µ g a. i./ L 48 hr EC50 = 3.00 µ g a. i./ L 72 hr EC50 = 0.21 µ g a. i./ L MRID 88949 ( Edwards et al., 1981) Supplemental  E 26 Table E 3c: Acute Toxicity of Cypermethrin Degradates to Freshwater Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification 3 phenoxybenzoic acid ( metabolite)

Daphnia magna ( water flea, first instar) 99.0 Static test conditions. Concentrations ( nominal) tested: 0, 25, 50, 100, 200, and 400 mg/ L 3 phenoxybenzoic acid. Mean measured concentrations: Test I = 24.0, 52.2, 104, 220, and 425 mg/ L3 phenoxybenzoic acid Test II = 25.2, 50.7, 104, 216, and 404 mg/ L 3 phenoxybenzoic acid.

48 hour EC50 = 89.0 mg/ L 3 phenoxybenzoic acid ( average value from Test I and Test II)

( 95% C. I. = 52 104 for Test I and 51 104 for Test 11).

NOAEC = 52.2 mg/ L ( value estimated by EPA reviewer, not reported by authors)

The authors suggested that the break down of Cypermethrin in the environment to 3 PBA and dihalovinyl cyclopropane acid greatly reduces the toxicity. Slightly toxic MRID 152739 ( Everett et al. 1983) Acceptable Daphnia magna ( water flea, first instar) 73.0 Static test conditions. Mean measured concentrations used, because of precipitation at higher concentrations: 0, 10.4, 20, 25, 41, 51, 82, 101, 157, 183, 245, 268 ppm 3 phenoxybenzoic acid 48 hr EC50 = 111 ppm 3 phenoxybenzoic acid ( 95% C. I. = 82 147) Practically non toxic Accession No. 42444601 ( Edwards et al., 1980)

Same data reported in MRID 89046 ( Edwards et al., 1980) Acceptable  E 27 d. Freshwater Invertebrate, Chronic A freshwater aquatic invertebrate life cycle test using the TGAI is required for cypermethrin because the end use product is expected to be transported to water from the intended use site. A 21 day life cycle on Daphnia magna was submitted to provide data on the chronic toxicity of cypermethrin TGAI to freshwater invertebrates ( MRID 428983 01). However, due to several deviations from guideline recommended methodologies, this study was classified as invalid. The guideline [ § 72 4( b)] is not fulfilled. No chronic toxicity studies of cypermethrin formulations or cypermethrin degradates in freshwater invertebrates were submitted.

e. Freshwater Benthic Organisms and other macroinvertebrates Studies in benthic organisms are not guideline requirements. Results of submitted studies on the toxicity of cypermethrin TGAI on benthic organisms are summarized in Table E 4. Studies were submitted for several types of benthic organisms, including midge, amphipod, mayfly, isopod, and gastropod. Two types of protocols were used in these studies, a water system and a water sediment system.

In the water system studies, organisms were exposed only to cypermethrin in overlying water; there was no sediment in the test chamber. Thus, while data from these studies provide information regarding the sensitivity of benthic organisms to cypermethrin in surface water, no data are available from these studies regarding exposure to cypermethrin in sediment. Therefore, data are insufficient for use in quantifying risks to benthic organisms.

For studies conducted using the water sediment system, cypermethrin was applied to water sediment systems and allowed to settle for 2 days; organisms were introduced to the above water sediment systems, and toxicity was assessed after a 10 day exposure duration. Studies using the water sediment system more accurately depict the environmental exposure of benthic organisms than the water system studies.

Two studies on cypermethrin TGAI were conducted using a water sediment system, one study on midge ( MRID 44074402; Supplemental) and one study on amphipod ( MRID 44074406; Supplemental); both studies were conducted using the same protocol. Cypermethrin was added to three different water sediment systems using sediments from three sources ( Florissant, Mississippi, and Duluth). Overlying water and sediment concentrations of cypermethrin were measured on Days 0 and 10 of exposure. Since concentrations in overlying water decreased over the 10 day period, it appears that the water sediment system was not at equilibrium. Thus, all toxicity values for these studies are expressed in terms of the concentration of cypermethrin in sediment (: g a. i./ kg) on Day 0. The reported toxicity endpoints varied depending upon the sediment source. In general, toxicity decreased, as reflected by higher LC50 values, with increasing organic carbon content of the sediment. Results of these studies yield 10 day LC50 values ranging from 3.6 : g a. i./ kg sediment ( Florrisant) in amphipods to 67 : g a. i./ kg sediment in midge ( Mississippi). In midge, exposure resulted in a decrease in dry weight, with 10 day NOAEC values ranging from 4.9 to 25 : g a. i./ kg sediment. In amphipod, length and dry weights were decreased, with 10 day NOAEC values ranging from < 1.8 to 2.3 : g a. i./ kg sediment. Taking the most conservative approach, EFED will use the lowest 10 day LC50 value, 3.6 : g a. i./ kg sediment in amphipods, to characterize the risk of acute exposure of benthic organisms to cypermethrin TGAI.

Results of the water system studies yield lethality values ranging from the 96 hour LC50 value of 0.009 : g a. i./ L in amphipods ( Acc. No. 42444601; Acceptable) to the 24 hour LC50 value of > 5 : g a. i./ L in midge larvae and gastropod ( Acc. No. 42444601, Supplemental). Based on these results, cypermethrin TGAI is categorized as very highly toxic to freshwater benthic organisms on an acute basis, following exposure in overlying water. No toxicity tests on cypermethrin formulations or cypermethrin degradates in freshwater benthic organisms were submitted.  E 28 Table E 4: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Freshwater Benthic Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification Technical Grade Cypermethrin Oronectes sp. ( crayfish) 91.69 Flow through test conditions. Mean measured concentrations: 0, 0 ( unidentified solvent control), 0.017, 0.023, 0.044, 0.11, and 0.21 µ g a. i./ L.

24 hr LC50 > 0.21 µ g a. i./ L 48 hr LC50 = 0.070 µ g a. i./ L ( 95% C. I. = 0.044 0.110)

96 hr LC50 = 0.068 µ g a. i./ L ( 95% C. I. = 0.053 0.090) Very highly toxic Accession No.

42444601 ( Jaber 1981) Acceptable Table E 4: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Freshwater Benthic Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 29 Baetis rhodani ( mayfly larvae) tech 14C labeled cypermethrin as 97.6% of applied radioactivity. Assumption that date are reported in terms or a. i./ L Flow through test conditions.

EC50 and LC50 calculated from mean measured concentrations of two tests:

Test 1 = 0, 1.7, 2.7, 6.2, 12.4, and 25.2 pptr ( ng a. i. L)

Test 2 = 0, 2.1, 3.4, 6.0, 11.7, and 22.0 pptr ( ng a. i./ L)

24 hr EC50 = 9.5 pptr ( ng a. i./ L)

48 hr EC50 = 9.2 pptr ( ng a. i./ L)

96 hr EC50 = 5.7 pptr ( ng a. i./ L)

48 hr LC50 > 25 pptr ( ng a. i./ L)

72 hr LC50 = 22.4 pptr ( ng a. i./ L)

96 hr LC50 = 12.3 pptr ( ng a. i./ L) Very highly toxic Accession No. 42444601 ( Edwards et al. 1980);

Supplemental Table E 4: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Freshwater Benthic Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 30 Cypermethrin Technical ( WL 43467)

Cleon dipterum ( mayfly larvae) 98.1 Flow through test conditions. Concentrations tested: 0, 0.7, 2, 7, 10, 24 pptr a. i. ( ng a. i./ L) ( no solvent control)

Ability of mayfly larvae to recover the ability to make escape responses when returned to uncontaminated water wasn't assessed due to high control mortalities.

96 hr EC50 mayfly larvae = 4 pptr ( ng a. i./ L)( 95% C. I. = 2 6)

96 hr LC50 mayfly larvae = 20 pptr a. i. ( ng a. i./ L)

( 95% C. I. = 10 70) Very highly toxic Accession No.

42444601 ( Stephenson and Kane 1980) Acceptable Table E 4: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Freshwater Benthic Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 31 Various freshwater species 84.6 24 hr test results given; no other study details given.

Gyrinus natator ( whirligig; adult)

24 hr EC50 = 0.07 µ g a. i./ L 24 hr LC50 = > 5 µ g a. i./ L Notonecta spp.

( backswimmer; adult)

24 hr EC50 = 0.30 µ g a. i./ L 24 hr LC50 = > 5 µ g a. i./ L Corixa punctata ( waterboatman; adult)

24 hr EC50 = 0.70 µ g a. i./ L 24 hr LC50 = > 5 µ g a. i./ L Piona carnea ( water mite; adult)

24 hr EC50 = 0.02 µ g a. i./ L 24 hr LC50 = 0.050 µ g a. i./ L Cloeon dipterum ( mayfly)

24 hr EC50 = 0.070 µ g a. i./ L 24 hr LC50 = 0.60 µ g a. i./ L Very highly toxic Accession No. 42444601 ( Stephenson 1980) Supplemental . Table E 4: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Freshwater Benthic Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 32 Gammerus pulex ( freshwater amphipod) 98.1 Flow through test conditions. Concentrations tested: 0, 0.7, 2, 7, 10, 24 pptr a. i. ( ng a. i./ L) ( no solvent control)

Shrimp were shown to recover the ability to make escape responses when returned to uncontaminated water.

96 hr EC50 = 4 pptr a. i. ( ng a. i./ L) ( 95% C. I. = 2 7)

96 hr LC50 = 9 pptr a. i. ( ng a. i./ L) ( 95% C. I. = 7 10) Very highly toxic Accession No.

42444601 ( Stephenson and Kane 1980) Acceptable Table E 4: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Freshwater Benthic Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 33 Various freshwater species 84.6 24 hr test results given; no other study details given.

Gammarus pulex ( amphipod; 3 8 mm)

24 hr EC50 = 0.04 µ g a. i./ L ( 95% C. I. = 0.02 0.06)

24 hr LC50 = 0.10 µ g a. i./ L ( 95% C. I. = 0.08 0.20)

Chironomus thummi ( midge larvae)

24 hr EC50 = 0.20 µ g a. i./ L ( 95% C. I. = 0.10  0.30 )

24 hr LC50 = > 5 µ g a. i./ L Asellus spp. ( isopod; 3 8mm)

24 hr EC50 = 0.02 µ g a. i./ L ( 95% C. I. =  )

24 hr LC50 = 0.20 µ g a. i./ L ( 95% C. I. = 0.10  0.40)

Lymnea peregra ( gastropod; < 8mm)

24 hr EC50 = > 5 µ g a. i./ L 24 hr LC50 = > 5 µ g a. i./ L Chaoborus spp. ( midge; larvae)

24 hr EC50 = 0.03 µ g a. i./ L ( 95% C. I. =  )

24 hr LC50 = 0.2 µ g a. i./ L ( 95% C. I. = 0.03 /( sic) 4) Very highly toxic Accession No. 42444601 ( Stephenson 1980) Supplemental . Table E 4: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Freshwater Benthic Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 34 14C labeled Cypermethrin Chironomus riparius ( midge) ??? Radio chemical purity > 89%

Static test conditions. First instar exposed to ( nominal) : 0, 0 ( acetone solvent control), 0.0016, 0.0031, 0.0062, 0.0125, 0.025, 0.05, and 0.1 µ g/ L.

First instar mean measured: 0.0018, 0.0034, 0.0052, 0.010, 0.019, 0.037, and 0.072 µ g/ L Fourth instar exposed to ( nominal): 0, 0 ( acetone solvent control), 0.250, 0.5, 1.0, 2.0, and 4.0 µ g/ L.

Fourth instar mean measured: 0.20, 0.33, 0.74, 1.4, and 2.9 µ g/ L.

First instar 48 hr LC50 = 0.0069 µ g a. i./ L ( 95% C. I. = 0.0056 0.0085) ( based on mean measured concentrations)

Fourth instar 48 hr LC50 = 4.6 µ g/ L ( 95% C. I. = 2 600) ( based on mean measured concentrations); however, the authors report that this value " has very wide confidence limits and is outside the range of concentrations tested. Thus the LC50 is best quoted as > 2.9 µ g/ L, the highest mean measured concentration tested." Very highly toxic MRID 44074401 ( Rapley and Hamer 1996) Supplemental Table E 4: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Freshwater Benthic Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 35 Chironomus tentans ( midge) tech Radio chemical purity > 96%

Cypermethrin applied to three water sediment systems, then allowed to settle for 2 days:

Florissant sediment ( 0.99 % Organic Carbon ( OC)); nominal concentrations = 0, 0 ( acetone solvent control), 2.2, 6.7, 20, 60, and 180 µ g a. i./ kg.

Mississippi sediment ( 3.1 % OC); nominal concentrations = 0, 0 ( acetone solvent control), 3.4, 11, 33, 100, and 300 µ g a. i./ kg. Duluth sediment ( 13.3 % OC); nominal concentrations = 0, 0 ( acetone solvent control), 5.6, 17, 50, 150, and 450 µ g a. i./ kg.

Third instar Chironomus were introduced to the above watersediment systems, and 10 days later, survival and dry weight of survivors was measured.

10 day LC50' s ( based on sediment concentrations measured at day 0):

Florrisant = 14 µ g a. i./ kg Mississippi = 67 µ g a. i./ kg Duluth = 62 µ g a. i./ kg NOAEC's ( based on dry weight):

Florrisant = 4.9 µ g a. i./ kg Mississippi = 25 µ g a. i./ kg Duluth = 14 µ g a. i./ kg Very highly toxic MRID 44074402 ( Gentle et al. 1996) Supplemental Table E 4: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Freshwater Benthic Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 36 Hyalella azteca ( amphipod) tech Radiochemical purity > 89%

Static test conditions. 7 14 day old amphipods exposed to ( nominal): 0, 0 ( acetone solvent control), 0.0016, 0.0031, 0.0062, 0.0125, 0.025, 0.05, and 0.1 µ g/ L. Mean measured concentrations: 0.0016, 0.0033, 0.0054, 0.010, 0.019, 0.035, 0.071 µ g/ L.

48 hr LC50 = 0.0053 µ g a. i./ L ( 95% C. I. = 0.0043  0.0065) ( based on mean measured concentrations). Very highly toxic MRID 44074401 ( Rapley and Hamer 1996) Supplemental Table E 4: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Freshwater Benthic Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 37 Hyalella azteca ( amphipod) tech Radiochemical purity Cypermethrin applied to three water sediment systems, then allowed to settle for 2 days:

Florissant sediment ( 0.99 % OC); nominal concentrations = 0, 0 ( acetone solvent control), 2.5, 5, 10, 20, and 40 µ g a. i./ kg. Mississippi sediment ( 3.1 % OC); nominal concentrations = 0, 0 ( acetone solvent control), 0.74, 2.2, 6.7, 20, and 60 µ g a. i./ kg. Duluth sediment ( 13.3 % OC); nominal concentrations = 0, 0 ( acetone solvent control), 1.9, 5.6, 17, 50, and 150 µ g a. i./ kg.

Amphipods were introduced to the above water sediment systems, and 10 days later, survival and length and dry weight of survivors was measured.

10 day LC50' s ( based on sediment concentrations measured at day 0):

Florrisant = 3.6 µ g a. i./ kg Mississippi = 19 µ g a. i./ kg Duluth = 23 µ g a. i./ kg NOAEC's ( based on length and dry weight):

Florrisant = < 1.8 µ g a. i./ kg Mississippi = 2.3 µ g a. i./ kg Duluth = 1.8 µ g a. i./ kg Very highly toxic MRID 44074406 ( Rapley and Hamer 1996 Supplemental Table E 4: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Freshwater Benthic Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 38 Hyalella azteca ( amphipod) tech Radiochemical purity = 97%

Static test conditions. Adult amphiphods exposed to ( nominal): 0 ( acetone solvent control), 0.78, 1.56, 3.12, 6.25, 12.5, 25, 50, 100, 200, and 400 ng a. i./ L.

In addition to mortality, amphipods were assessed as being affected if they failed to respond to a stimulus by swimming.

96 hr EC50 = 3.6 ng a. i./ L ( 95% C. I. = 2.0 4.9) Very highly toxic MRID 44423501 ( Hamer 1997) Supplemental III. Toxicity to Estuarine and Marine Animals a. Estuarine and Marine Fish, Acute Acute toxicity testing with estuarine/ marine fish using the TGAI is required for cypermethrin because the end use product is expected to reach this environment because of its use in coastal areas. The preferred test species is the sheepshead minnow. Acute toxicity studies in estuarine/ marine fish were submitted for sheepshead minnow ( 5 studies) and Atlantic salmon ( 1 study). Study details are provided in Table E 5. Results of these studies yield 96 hour LC 50 values ranging from 0.95 : g a. i./ L ( MRID 90075; Supplemental) to 4.3 : g a. i./ L ( MRID 41968212; Acceptable), indicating that cypermethrin TGAI is very highly toxic to estuarine/ marine fish on an acute basis. Taking the most conservative approach, EFED will use the lowest 96 hour LC 50 value of 0.95 : g a. i./ L in sheepshead minnow to evaluate acute toxic exposure to estuarine/ marine. The guideline [ § 72 3( a)] is fulfilled.

No acute toxicity studies of cypermethrin formulations or cypermethrin degradates in estuarine/ marine fish were submitted.  E 39 Table E 5: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Estuarine/ Marine Fish Species % a. i. LC50 Toxicity Category Identification Number Study Classification Technical Grade Cypermethrin Cyprinidon variegatus ( sheepshead minnow) 91.5 Flow through test conditions. Concentrations tested: 0, 0 ( acetone solvent control), 0.32, 0.63, 1.25, 2.50, and 5.00 µ g a. i./ L. Mean measured concentrations: 0.11, 0.24, 0.48, 0.64, and 1.90 µ g a. i./ L.

After 96 hrs, mortality was 100% at 1.9 µ g a. i./ L. There was no mortality in the controls or at concentrations # 0.48 µ g a. i./ L.

24 hr LC50 = 1.1 µ g a. i./ L ( 95% C. I. = 0.64 1.90) ( based on mean measured concentrations)

48 hr LC50 = 1.1 µ g a. i./ L ( 95% C. I. = 0.64 1.90) ( based on mean measured concentrations).

96 hr LC50 = 0.95 µ g a. i./ L ( 95% C. I. = 0.48 1.90) ( based on mean measured concentrations).

NOAEC ( lethality) = 0.48 µ g a. i./ L. Very highly toxic MRID 90075 ( Jaber and Hawk 1981) Acceptable Table E 5: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Estuarine/ Marine Fish Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 40 Cyprinidon variegatus ( sheepshead minnow) 98.4 Flow through test conditions.

Concentrations ( nominal) tested: 0, 0 ( acetone solvent control), 0.85, 1.4, 2.4, 3.9, and 6.5 µ g a. i./ L Mean measured concentrations: 0.64, 1.1, 1.4, 2.1, 4.2 µ g a. i./ L Loss of equilibrium noted at the two highest concentration treatment levels.

Mortalities observed at 96 hrs. at 2.1 µ g a. i./ L, and at 24, 48, 72, and 96 hrs. at 4.2 µ g a. i./ L.

96 hour LC50 = 2.7 ppb a. i. ( µ g a. i./ L) ( 95% C. I.: 2.1 4.2 ppb a. i.)

NOAEC = 1.4 ppb a. i. ( µ g a. i./ L) Very highly toxic MRID 44546033 ( Dionne 1998) Acceptable Salmo salar ( Atlantic salmon) 98.5 Study details not given.

96 hr LC50 = 2.0 µ g a. i./ L Very highly toxic MRID 41068003 ( McLeese et al., 1980) Supplemental Technical Cypermethrin ( FMC 45806)

Cyprinidon variegatus ( sheepshead minnow) 91.5 Flow through test conditions. Concentrations tested: 0, 0 ( DMF solvent control), 0.71, 1.19, 1.98, 3.29, and 5.49 µ g a. i./ L.

96 hr LC50 = 3.42 µ g a. i./ L ( 95% C. I. = 1.89 4.07)

NOAEC = 1.89 µ g a. i./ L Very highly toxic MRID 41968212 ( Chandler, 1990) Acceptable Table E 5: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Estuarine/ Marine Fish Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 41 Cypermethrin S ( Fury Technical) ( FMC 56701)

Cyprinidon variegatus ( sheepshead minnow) 88.2 Flow through test conditions. Concentrations tested: 0, 0 (( DMF solvent control), 0.7, 1.17, 1.94, 3.24, and 5.4 µ g a. i./ L. Mean measured concentrations: 0.28, 0.62, 0.91, 1.79, and 3.0 µ g a. i./ L.

No mortality was observed in the controls or the three lowest test concentrations.

96 hr LC50 = 2.37 µ g a. i./ L ( 95% C. I. = 1.79 3.0)

NOAEC ( mortality) = 1.79 µ g a. i./ L. Very highly toxic MRID 41968211 ( Overman et al. ,1990) Acceptable 14C labeled Betacypermethrin Cyprinidon variegatus ( sheepshead minnow) 98.6 > 95% Radio chemical Purity Flow through test conditions. Concentrations ( nominal) tested: 0, 0 ( acetone solvent control), 1.3, 2.2, 3.6, 6.0, and 10 µ g a. i./ L. Mean measured concentrations: 0.84, 1.7, 2.5, 5.0, and 8.5 ppb a. i. ( µ g a. i./ L )

Signs of test material toxicity were noted at all but the lowestconcentration treatment level and included lethargy and loss of equilibrium.

96 hour LC50 = 2.4 ppb a. i. ( µ g a. i./ L)

NOAEC ( sublethal effects) = 0.84 ppb a. i. ( µ g a. i./ L ) Very highly toxic MRID 44546034 ( Sousa 1998) Acceptable  E 42 b. Estuarine and Marine Fish, Chronic No chronic toxicity tests in estuarine/ marine fish were submitted by the registrant. The guideline [ § 72 4( a)] is not fulfilled. No chronic toxicity studies of cypermethrin formulations or cypermethrin degradates in estuarine/ marine fish were submitted.

c. Estuarine and Marine Aquatic Invertebrates, Acute Acute toxicity testing with estuarine/ marine invertebrates using the TGAI is required for cypermethrin because the active ingredient may reach this environment because of its use in coastal communities. The preferred test species are mysid shrimp and eastern oyster. Acute toxicity studies using cypermethrin TGAI have been submitted for mysid shrimp ( 4 studies), other shrimp ( 2 studies), lobster ( 1 study), fiddler crab ( 1 study), and oyster ( 2 studies); results are summarized in Table E 6. The toxicity values ( EC 50 and LC 50 ) reported for shrimp range from the 96 hour LC 50 value of 0.00475 : g a. i./ L ( Acc. No. 42444601; Acceptable) to the 96 hour LC 50 value 0.01 : g a. i./ L ( MRID 41068003; Supplemental). Similar results were observed in lobster ( 96 hour LC 50 = 0.04 : g a. i./ L; MRID 41068003; Supplemental) and fiddler crab ( 96 hour LC 50 = 0.197 : g a. i./ L; MRID 89045; Supplemental). Based on these results, cypermethrin TGAI is categorized as very highly toxic to shrimp, lobster and crab. Results of acute toxicity tests in molluscs show that cypermethrin TGAI is moderately to highly toxic in oysters, with a 96 hour EC 50 value of 0.37 mg a. i./ L in Eastern oyster ( MRID 89049; Acceptable) and a 48 hour LC 50 value of > 2.27 mg a. i./ L in Pacific oyster ( Acc. No. 42444601; Acceptable). Comparison of the shrimp and mollusc toxicity values suggests that molluscs are less susceptible than shrimp to cypermethrin toxicity on an acute basis. Taking the most conservative approach, EFED will use the lowest acute toxicity value, the 96 hour LC 50 value of 0.00475 : g a. i./ L in mysid shrimp ( Acc. No. 42444601; Acceptable), to categorize acute risk to estuarine/ marine invertebrates. The guideline [ § 72 3] is fulfilled. No acute toxicity studies of cypermethrin formulations or cypermethrin degradates in estuarine/ marine invertebrates were submitted.

Table E 6: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Estuarine/ Marine Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification Technical Grade Cypermethrin Table E 6: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Estuarine/ Marine Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 43 Penaeus duorarum ( pink shrimp) 91.5 Flow through test conditions. Concentrations tested: 0, 0 ( unidentified solvent control), 8.6, 12, 25, 58, and 94 pptr a. i. ( ng a. i./ L)

24 hr LC50 = 74 pptr a. i. ( ng a. i./ L) ( 95% C. I. = 58 94)

48 hr LC50 = 43 pptr a. i. ( ng a. i./ L) ( 95% C. I. = 36 53)

72 hr LC50 = 38 pptr a. i. ( ng a. i./ L)( 95% C. I. = 32 46)

96 hr LC50 = 36 pptr a. i. ( ng a. i./ L) ( 95% C. I. = 31 43) Very highly toxic MRID 89043 ( amendment to Accession No. 42444601)

( Jaber 1981) Acceptable C. septemspinosa ( shrimp), and Homarus americanus ( lobster) 98.5 96 hr LC50 shrimp = 0.01 µ g a. i./ L 96 hr LC50 lobster = 0.04 µ g a. i./ L Very highly toxic MRID 41068003 ( McLeese et al. ,1980) Supplemental Crassostrea virginia ( eastern oyster) 91.5 Flow through test conditions. Mean measured concentrations: 0, 0 ( unidentified solvent control), 13.9, 92.0, 217, 351, 677 µ g a. i./ L Criterion was a 50% reduction in shell growth compared to controls 96 hr shell deposition EC50 = 370 ppb a. i. ( µ g a. i./ L) ( 95% C. I. = 245 556) Very highly toxic MRID 89049 ( Jaber 1981) Acceptable Table E 6: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Estuarine/ Marine Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 44 Mvsidopsis bahia ( Mysid shrimp) 95.9 Concentrations ( nominal) tested:

0, 0 ( acetone solvent control), 3.75, 6.25, 10, 15, and 25 ng a. i/ L. Mean measured concentrations: 3.1, 3.9, 4.5, 6.0, and 10.0 ng a. i/ L Precipitate observed at the highest concentration ( appeared slightly golden colored at 48 hours).

There was slight test material contamination, which had no apparent biological consequences; survival was 95% or greater in the control groups and the first two treatment levels.

96 hr LC50 = 5 ng a. i/ L ( based on measured concentrations) ( 95% C. I. = 5 6)

NOAEC ( survival) = 3.9 ng a. i/ L Very highly toxic MRID 42444601 ( Ward et al. 1992) Acceptable Table E 6: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Estuarine/ Marine Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 45 Mvsidopsis bahia ( Mysid shrimp 98.4 Flow through test conditions. Concentrations ( nominal) tested: 0, 0 ( acetone solvent control), 2.2, 3.7, 6.1, 10, and 17 ng a. i./ L. Mean measured concentrations: 1.0, 1.7, 2.8, 4.6, 7.7 ng a. i./ L/

Signs of test material toxicity were noted at the three highestconcentration treatment levels and included lethargy, erratic swimming behavior, loss of equilibrium, and surfacing.

96 hour LC50 = 5.5 pptr a. i. ( ng a. i./ L) ( 95% C. I.: 4.6 6.9)

NOAEC ( sublethal effects) = 1.7 pptr a. i. Very highly toxic MRID 44561210 ( Putt 1998) Acceptable Crassostrea gigas ( Pacific oyster) 91.5 cis: trans ratio = 48.8: 42.7.

48 hr EC50 > 2.27 ppm a. i 48 hr LC50 > 2.27 ppm a. i Due to limited solubility of test compound in seawater, higher concentrations could not be tested. Moderately toxic Accession No. 42444601 ( Thompson 1981) Acceptable Table E 6: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Estuarine/ Marine Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 46 Uca pugilator ( fiddler crab) 91.5 Flow through test conditions. Mean measured concentrations: 0, 0 ( unspecified solvent control), 29, 44, 85, 161, and 389 pptr a. i. ( ng a. i./ L)

96 hr LC50 = 197 pptr a. i. ( ng a. i./ L) ( 95% C. I. = 162 243) Very highly toxic MRID 89045 ( Jaber 1981) Supplemental Table E 6: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Estuarine/ Marine Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 47 14C labeled Technical Mvsidopsis bahia ( Mysid shrimp > 97 % Flow through test conditions. Mean measured concentrations tested: 0, 0 ( solvent control, solvent unspecified), 1.7, 2.5, 6.7, 10, and 24 pptr a. i. ( ng a. i./ L)

24 hr LC50 = > 24 pptr a. i. ( ng a. i./ L)

48 hr LC50 = 16.5 pptr a. i. ( ng a. i./ L) ( C. I.= 8.44 42.5)

72 hr LC50 = 9.27 pptr a. i. ( ng a. i./ L) ( 95% C. I. = 5.09 18.1)

96 hr LC50 = 4.75 pptr a. i. ( ng a. i./ L) ( 95% C. I. = 4.01 5.67)

48 hour LOAEL ( lethality) = 2.5 pptr a. i. ( ng a. i./ L)

48 hour NOAEL ( lethality) = 1.7 pptr a. i. ( ng a. i./ L) Very highly toxic Accession No. 42444601 ( Jaber 1981) Acceptable 14C labeled Betacypermethrin Table E 6: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Estuarine/ Marine Invertebrates Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 48 Mvsidopsis bahia ( Mysid shrimp) tech > 95% Radio chemical Purity Flow through test conditions. Concentrations ( nominal) tested: 0, 0 ( acetone solvent control), 1.1, 2.1, 4.3, 8.5, and 17 ng a. i./ L. Mean measured concentrations: 0.62, 1.2, 2.3, 5.0, 8.6 ng a. i./ L Signs of test material toxicity were noted at the two highestconcentration treatment levels and included lethargy and erratic swimming behavior.

96 hour LC50 = 5.9 pptr a. i. ( ng a. i./ L) ( 95% C. I.: 5.1 6.7)

NOAEC ( sublethal effects) = 2.3 pptr a. i. ( ng a. i./ L Very highly toxic MRID 44561209 ( Putt 1998) Acceptable  E 49 Table E 7: Chronic Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Estuarine/ Marine Invertebrates Species % a. i. LC50 Identification Number Study Classification 14C labeled Technical Mvsidopsis bahia ( Mysid shrimp) > 97 % active ingred ient 28 day test. Mean measured concentrations used: 0, 0 ( unspecified solvent control), 0.44, 0.64, 1.5, 2.8, and 5.6 pptr a. i. ( ng a. i./ L).

Reproduction endpoints measured by number of offspring, number of females with offspring, and brood pouches per female.

Number of offspring in treatment groups significantly different from controls in 2.8 and 5.6 pptr a. i. ( ng a. i./ L) group.

28 day LOAEC = 2.8 pptr a. i. ( ng a. i./ L)

28 day NOAEC = 1.5 pptr a. i. ( ng a. i./ L) Accession No. 42444601 ( Jaber 1981) Acceptable Table E 7: Chronic Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Estuarine/ Marine Invertebrates Species % a. i. LC50 Identification Number Study Classification  E 50 14C labeled Cypermethrin ( FMC 30980) Table E 7: Chronic Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Estuarine/ Marine Invertebrates Species % a. i. LC50 Identification Number Study Classification  E 51 Mysidopsis bahia ( mysid shrimp) 98.1 Early life stage toxicity test under flow through conditions; duration unknown. Concentrations ( nominal) tested: 0, 0 ( DMF solvent control), 2.0, 1.0, 0.5, and 0.25 ng ai/ L. Mean measured concentrations: 0.125, 0.233, 0.411, 0.781 and1.976 ng ai/ L Mortality of first generation mysids ranged from 8% percent ( mean measured concentration of 0 0.411 ng a. i./ L) to 35% ( mean measured concentration of 1.976 ng a. i./ L). Mortality was statistically reduced only at 1.976 ng a. i./ L when compared to controls.

LOAEC ( first generation mortality) = 1.976 ng a. i./ L NOAEC ( first generation mortality) = 0.781 ng a. i./ L Mean number of young per female reproductive day. No statistical difference between treatment groups and controls NOAEC (# young/& reproductive day) > 1.976 ng a. i./ L Length and dry weight of male mysids in the 1.976 ng/ L group were statistically reduced from controls, while only female dry weight in the 1.976 ng a. i./ L group was statistically reduced.

LOAEC (% length and wt)= 1.976 ng a. i./ L NOAEC (% length and wt) = 0.781 ng a. i./ L LOAEC (& weight) = 1.976 ng a. i./ L NOAEC (& weight) = 0.781 ng a. i./ L Second generation mysid survival was not adversely affected. Survival was not less than 95% in any of the treatment groups.

LOAEC ( second generation survival) > 1.976 ng a. i./ L NOAEC ( second generation survival) = 1.976 MRID 42725301 ( Wheat 1992) Acceptable Table E 7: Chronic Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Estuarine/ Marine Invertebrates Species % a. i. LC50 Identification Number Study Classification  E 52 14C labeled Betacypermethrin Mysidopsis bahia ( mysid shrimp) Radio purity > 95% Flow through test conditions. Test was conducted for 28 days. Time to sexual maturation of surviving mysids was reported to be 14 days.

Concentrations ( nominal) tested: 0, 0 ( acetone solvent control), 0.37, 0.75, 1.5, 3.0, and 6.0 ng a. i./ L. Mean measured concentrations: 0.21, 0.44, 0.79, 1.5, and 3.3 ng a. i./ L No sublethal signs of toxicity reported.

For survival and reproduction 28 day LOAEC = 3.3 ng a. i./ L 28 day NOAEC = 1.5 ng a. i./ L ( based on mean measured concentrations).

Due to significant reduction in survival, growth endpoints ( length and wt) could not be assessed at the highest treatment level ( 3.3 ng a. i./ L). However, no significant effects on growth parameters were observed at concentration up to 1.5 ng a. i./ L. MRID 44546035 ( Sousa 1998) Acceptable v. Aquatic Field Studies Several aquatic field studies on the effects of cypermethrin formulations have been reviewed for this risk assessment. Results are summarized in Table E 8. Data from field studies were obtained from studies submitted by the registrant and from open literature studies identified from searches of the ECOTOX database. Results of these studies provide information on the effects of cypermethrin on fish and invertebrates ( including benthic organisms) in freshwater aquatic environments. Due to the variability in experimental techniques and methodologies employed in these studies, results of these studies are not sufficient for use in quantitative assessments. Thus, results will be used qualitatively in this assessment.

Data from field studies on the effects of cypermethrin on fish were obtained from three registrantsubmitted studies ( MRID 155770, Supplemental; MRID 155772, Supplemental; MRID 152737, Supplemental) and two open literature studies ( Crossland et al. 1982; Davies and Cook 1993).  E 53 Results of the registrant submitted studies using single applications of cypermethrin application at rates ranging from 0.0012 lb a. i/ A ( MRID 152737) to 0.089 lb a. i./ A ( MRID 155770) show no lethal or sublethal effects on fish populations. In the open literature studies, application rates ranged from 0.011 lb a. i./ A ( Davies and Cook 1993) to 0.0623 lb a. i./ A ( Crossland et al., 1982). Although no adverse effects were observed on fish populations at the higher application rate of 0.0623 lb a. i./ A, sublethal effects ( including loss of equilibrium, lethargy, muscle tetany) were reported following single application of 0.011 lb a. i./ A ( Davies and Cook 1993). In this study, sublethal effects were observed for 8 days following application and attributed, in part, to exposure to cypermethrin from ingestion of dead and dying invertebrates.

For field studies assessing the effects of cypermethrin on aquatic invertebrate populations, results range from no observable effects on aquatic invertebrate and benthic populations to catastrophic drift and profound decreases in population diversity and abundance. For studies reporting no adverse effects on macroinvertebrate populations ( Acc No 250506, Supplemental; MRID 155772, Supplemental), application rates range from a single application of 0.0623 lb a. i./ A ( MRID 155772) to repeated applications of 0.126 lb a. i./ A, ( 6 applications at 5 day intervals to cotton fields) ( Acc. No. 250506, Supplemental). However, results of several field studies show that exposure to cypermethrin at application rates ranging from 0.00025 lb a. i./ A ( Mulla et al. 1978) to 0.125 lb a. i./ A ( Acc. No. 250506; Supplemental) causes significant decreases in abundance and diversity of aquatic invertebrate populations. Effects include catastrophic drift within 0 90 minutes after application of cypermethrin ( Crossland et al., 1982; Farmer et al. 1995; Moshen and Mulla 1982), and decreased abundance and diversity of macroinvertebrates over a longer time period ( several weeks to several months) ( MRID 155770, Supplemental; MRID 152737, Supplemental; Farmer et al. 1995; Kedwards et al. 1999 a, b; Mulla et al. 1978; Mulla et al. 1982). In some cases, recovery of individual species was rapid ( MRID 155770, Supplemental; Kedwards et al. 1999a, b; ); however, for other species, recovery did not occur for several months ( Kedwards et al.; 1999b; Davies and Cook 1993).  E 54 Table E 8 Aquatic Field Studies of Cypermethrin Study Duration % a. i. Methodology and Results Identification Number Study Classification Cypermethrin Formulation Not Specified Not given formulated product  not specified Methods: A cotton field adjacent to a pond was treated with a total of 16 aerial applications of cypermethrin. Treatments were made at 5 day intervals at a rate of 0.125 lbs a. i./ acre. The test pond was observed for drift and runoff contamination, water quality and biological impact of the treatments.

Observations: Authors state that the only effects due to cypermethrin were localized to an area of shoreline closest to the test cotton field. Macroinvertebrate and zooplankton populations varied throughout the study, but authors concluded this was primarily due to seasonal population fluctuations and organism mobility. Adverse effects to aquatic insects localized to the area of the pond adjacent to the cotton field; hemipterans appeared to be particularly sensitive.

One year treatments, the macroinvertebrates had reestablished themselves in the affected area, and authors concluded there were no permanent population effects from the cypermethrin.

EPA reviewer concluded the detection level in sediments in this study of 0.005 mg/ kg and of 20 pptr were not sensitive enough for the analysis results to be of value.

EPA reviewer concluded that the lack of sufficient number of organisms and/ or sufficient number of species defeated any meaningful statistical analysis relevant to assessing populations. Accession No. 250506 ( ICI, date not given, study done 1980) Supplemental The EPA reviewer rated this study as supplemental, due to its inadequacy to address runoff potential ( test field was too small relative to the pond size to provide a realistic runoff exposure). Table E 8 Aquatic Field Studies of Cypermethrin Study Duration % a. i. Methodology and Results Identification Number Study Classification  E 55 2 weeks Formulation not identified   Emulsifiable concentrate containing 400 g/ L cypermethrin , 10% emulsifiers, 50% mixed petroleum xylenes Mature 20 m x 5m x 0.8m deep pond was oversprayed with emulsifiable concentrate at a rate of 100 g cypermethrin/ ha.

Surface and subsurface water, and sediment analyzed for cypermethrin.

Macroinvertebrates sampled 1 wk before treatment and 1 and 2 wks after treatment.

2 wks after treatment, pond was pumped dry and fish removed, identified and counted.

No effects were observed on wild populations of fish and amphibians.

Authors note a " considerable" effect on the community of invertebrates , marked by a reduction in species richness, arising from mortality of aquatic insects and Crustacea.

Other effects noted:

1) Later instar nymphs of waterboatment ( Nonecta sp.) showed signs of hyperactivity and disorientation. 2) Water beetles, particularly Dytiscus marginalis died at the surface of the pond within a few hours. 3)

Dipterous larvae such as chironomids, were not noticeably affected until 24 hrs after treatment. 4) Crustacea in the zooplankton were not killed until 24 48 hr after treatment. MRID 155770 ( Crossland 1982) Supplemental Table E 8 Aquatic Field Studies of Cypermethrin Study Duration % a. i. Methodology and Results Identification Number Study Classification  E 56 16 weeks Emulsifiable concentrate containing 400 g/ L cypermethrin , 10% emulsifiers, 50% mixed petroleum xylenes Methods: Mature, 20m pond divided into two 9m x 10m x 0.7 m ponds; one pond was oversprayed with emulsifiable concentrate at a rate of 100 g cypermethrin/ ha. 12 days before treatment both ponds were stocked with 75 small rudd fish. Behavioral observations of fish were made immediately before and after treatment. Samples of surface water, subsurface water, sediment, vegetation and fish were analyzed for cypermethrin at regular time intervals after treatment. Macroinvertebrates were collected and counted to give information on the effect of cypermethrin on numbers of individuals and species, as well as effect on diversity index.

Results: No mortality of any fish or wild populations of newts was observed. For macroinvertebrates. ( based on graphic representation data), there appeared to be a sharp reduction in numbers of individuals and species, as well as the Shannon diversity index at approximately 2 wks after treatment when compared to the control pond; however this reduction is not substantiated statistically. The number of species and diversity index appeared to recover at approximately 6 8 wks after treatment ( similar population numbers in treated and untreated ponds). The number of individuals per species appeared to be lower in the treated pond than the untreated pond for the entire 16 weeks; however, data were presented only graphically. MRID 155770 ( Crossland 1982) Supplemental Table E 8 Aquatic Field Studies of Cypermethrin Study Duration % a. i. Methodology and Results Identification Number Study Classification  E 57 Not given 100 g/ L emulsifiable concentrate formulation of cypermethrin Effect of spray drift was investigated in ponds adjacent to fields of sugar beets and potatoes treated with cypermethrin at 70 g/ ha; Cypermethrin concentrations were assessed in water and fish from the ponds.

There were no detectable residues in fish and no apparent effects on aquatic fauna. Detection limit in fish was 5 ug/ kg No reductions in numbers macroinvertebrates was observed. MRID 155772 ( Crossland et al. ,1982) Supplemental 120 minutes not reported Field study: Cypermethrin added to manmade creak ( Thousdand Palms Canyon, CA) at a rate of 0.01 ppm/ 15 minutes [ appears that cypermethrin was diluted into 200 mL of stream water, then added to the stream over a 15 minute period]. Organisms were sampled 50, 250, 750, and 1,300 m downstream of application site. Sampling was conducted from 0 120 minutes after application of cypermethrin.

Non Target species sampled: Ephemoroptera ( mayflies), Trichoptera ( caddisflies), Odonata ( dragonflies and damselflies), and Chironomidae ( benthic water beetle).

Results: " Catastrophic drift" ( organisms immobilized or dead) was observed for mayfly nymphs, benthic water beetle, caddisfly larvae, dragonflies and damselflies. Effect was most pronounced during time 0 90 minutes after " application" of cypermethrin. Mohsen and Mulla 1982 Open Literature ( Not Classified) Table E 8 Aquatic Field Studies of Cypermethrin Study Duration % a. i. Methodology and Results Identification Number Study Classification  E 58 10 week multiple application period, followed by ~ 14 week postapplication period not reported Methods: 3.4 acre farm pond in Alabama. Cypermethrin formulation ( not specified) was aerially applied 10 times to a cotton crop at a rate of 112 g a. i./ ha [ equivalent to 0.11 lb a. i./ A a], with an application interval of 1 week. Abundance of Chironomidae larvae ( freshwater midge) assessed at 2 week intervals pre, during, and postapplication ( 154 days after last application).

Results: Significant decreases in midge abundance during the application period, starting with the first application. However, effects were transient, with rapid recovery. Decrease in emergence and abundance of Diptera ( flies) associated with increasing sediment concentrations of cypermethrin. Kedwards et al. 1999a Open Literature ( Not Classified)

4 applications over 8 weeks, followed by 7 week observation period not reported Methods: Concrete experimental ponds stocked with hydrosoil. Ponds seeded with aquatic organisms ( no fish). Cypermethrin ( 0.7 g a. i./ ha) [ 0.0006 lb a. i./ A ] sprayed on the surface of the ponds four times, with 2 week application interval. Species evaluated: Grammaridae ( amphipod), Planorbidae ( snail), Chironomidae ( midge), and Asellidae ( isopod crustaceans).

Results: No significant effect on emergence of the macroinvertebrate community. Significant decreases in abundance of amphipod and isopod from start of treatment period throughout the postrecovery observation period. At the end of te observation period, abundance of isopod was returning to control levels; abundance of amphipod remained below pre treatment levels and did not show signs of recovery. Kedwards et al. 1999b Open Literature ( Not Classified) Table E 8 Aquatic Field Studies of Cypermethrin Study Duration % a. i. Methodology and Results Identification Number Study Classification  E 59 4 applications over 8 weeks formulation not reported Methods: Cypermethrin applied at rate of 0.7 g a. i./ ha [ 0.0006 lb a. i./ A ], under conditions simulating spray drift. Cypermethrin concentrations measured in surface water and sediment.

Concentration of cypermethrin in surface water and sediment: Concentration in surface water declined rapidly, with a halflife of ~ 1day. 1 hour after the 3rd application, surface water concentration was 35 ng/ L ( only measurement reported for cypermethrin). Residues in sediment increased during the application period ( concentrations for cypermethrin not reported). At 13 weeks after final application, residues in sediment were undetectable.

Ecological effects: For algae, No adverse effects on algal chlorophyll content, productivity, community metabolism, abundance or biomass. No statistically significant effects on zooplankton populations. For macroinvertebrates, 1 hour after application, erratic movements observed in Notonectidae ( backswimmers) and Gyrrinidae ( beetles). Decreased numbers of Asellidae ( isopod) and Gammaridae ( amphipod). Isopod showed evidence of recovery 3 weeks after last treatment; amphipod showed no signs of recovery. No decrease in number of mayfly nymphs or emergence. Decreases in Chironomidae ( amphipod) numbers, but not emergence. Farmer et al. 1995 Open Literature ( Not Classified) Table E 8 Aquatic Field Studies of Cypermethrin Study Duration % a. i. Methodology and Results Identification Number Study Classification  E 60 Cypermethrin ( Ammo Formulation)

Single application followed by 14 day observation period 30% Methods: Single application of cypermethrin applied at 0.001 lb a. i./ A. Abundance of the following non target organisms was assessed   mayfly naiads, dragonfly naiads, adult diving beetles, and Ostracods ( crustacean).

Results: No adverse effects were observed on abundance of water beetle populations, dragonfly naiads, and Ostracods. A marked decrease in mayfly populations was oberved, with no significant recovery at the end of the 2 week observation period. Mulla et al. 1982 Open Literature ( Not Classified)

FMC 33297 ( Pounce Formulation)

Single application followed by a 3 week observation period. 21% Methods: Single application of cypermethrin applied at 0.00025. 0.0005, and 0.001 lb a. i./ A. Effects on abundance of mayfly, dragonfly, midge and beetle larvae.

Results: Mayfly abundance greatly reduced for 3 weeks after application. No affect on dragonfly, beetle and midge larvae. Mulla et al. 1978 Open Literature ( Not Classified) Table E 8 Aquatic Field Studies of Cypermethrin Study Duration % a. i. Methodology and Results Identification Number Study Classification  E 61 Formulation GFU 36% w/ v Table E 8 Aquatic Field Studies of Cypermethrin Study Duration % a. i. Methodology and Results Identification Number Study Classification  E 62 11 months Emulsifiable concentrate formulation GFU 061, 36% w/ v cypermethrin Methods: Two concrete ponds ( 5mx5mx1m) were sprayed with a handheld boom sprayer 8 times at 5 day intervals with cypermethrin formulation GFU 061 at a rate of 1.4 g cypermethrin/ ha. In addition, there were two ( concrete) untreated control ponds. Two cages each with 5 carp were placed in each pond after the 2nd application until 17 days after the last application. All four ponds were stocked with zooplankton and macroinvertebrates. Invertebrates were sampled 9 times during the exposure period, and 5 more times during the following year. Microbial assessments were made 13 times during the treatment period.

Results:

For fish   cypermethrin had no effect on the fish. For invertebrates   there was no treatment effect on Turbellaria, Collembola, or Rotiform. Numbers of Oligochaeta and Hirudinum increased. Asellidae and Gammaridae were eliminated and the numbers of Hemiptera, Colaoptera and possibly Odonata were reduced. Cladocera initially decreased but recovered during treatment and became more abundant in the treated ponds, although with a different species composition. Other groups showing a decline followed by an increase were Copepoda, Ephemeroptera and Chironomidae. Major reductions of sensitive species occurred after the first spray. For microbes   Changes in numbers of visible bacteria were attributed to seasonal variations and not to cypermethrin.

Authors conclude that low rates of cypermethrin drift are unlikely to be toxic to fish, higher plants, and microorganisms, but can cause changes in the relative abundance of arthropod species. MRID 152737 ( Getty et al. 1983) Supplemental Table E 8 Aquatic Field Studies of Cypermethrin Study Duration % a. i. Methodology and Results Identification Number Study Classification  E 63 Ripcord Formulation Samples collected from 0 48 hours after application. not reported Methods: Two fields tests: Ripord spayed on two fields: ( A) 2 applications to sugar beet and potato in U. K. at rate of 70 g formulation/ ha [ equivalent to 0.0623 lb formulation/ ai]; and ( B) vineyards in France at rate of 30 or 45 g formulation/ ha [ equivalent to 0.027 or 0.04 lb formulation/ ai]. For test site A, effects on evaluated for adjacent ponds. For test site B, effects evaluated for adjacent streams.

Results:

Test site A: No detectable residues in fish at 24 hr after application. No effects observed in aquatic organism, except for some knock down, but no mortality , of some air breathing insects.

Test site B: 0.5 hours after application, maximum concentrations in surface water of streams ranged from 0.4 to 1.7 : g/ L. Cypermethrin levels in surface water rapidly decreased to Within 2 hours after spraying, increased invertebrate drift was observed for Gammaridae ( amphipod), Ephemeroptera ( mayflies), Coleoptera ( beetles), and Hemiptera ( true bugs). Sample collected at 24 and 8 hours after application show invertebrate drift had returned to pretreatment conditions. Based on date collected 48 after cypermethrin application, for benthic invertebrates, species richness, evenness and diversity appeared unaffected by application of cypermethrin. Crossland et al. 1982 Open Literature ( Not Classified) Table E 8 Aquatic Field Studies of Cypermethrin Study Duration % a. i. Methodology and Results Identification Number Study Classification  E 64 single application of cypermethrin formulation, sampling from 0 days to 16 months after application not reported Methods: Cypermethrin ( Polytrin formulation) applied by aerial spray at 12.6 g a. i./ ha [ equivalent to 0.011lb a. i./ A] to eucalyptus. Populations in adjacent tributary streams sampled from time 0 days to 16 months.

Results: For macroinvertebrates   Immediately after spraying, significant increase in invertebrate drift, with increased drift of Plecoptera ( stone fly) and ephemeroptera ( mayfly). Benthic abundance of Plecoptera ( stone fly) and ephemeroptera ( mayfly) also decreased. Abundance of these organisms was decreased for 77 days after application. Recovery of benthic populations was observed within 6 months. For Fish   no reported lethality. Fish showed changes in color pattern, loss of seld righting ability, lethargy, appearance of muscle tetany, and anemic appearance of blood and gills. Transient changes in muscle RNA/ DNA levels and brain and muscle acetylcholinesterase levels were related to the application event. Authors conclude that sublethal effects in fish due to dietary intake of cypermethrin from dead and dying invertebrate drift. Davies and Cook 1993 Open Literature ( Not Classified)

a Conversion of the application rate expressed in terms of g a. i./ ha to lb a. i./ A was done as follows:

lb a. i./ A = ( g a. i./ ha) × ( 1 ha/ 2.471 A) × ( 0.0022 lb/ 1 g)

III. Toxicity to Plants Inhabiting Aquatic Environments Studies of the effects of cypermethrin on plants inhabiting aquatic environments were not submitted.  E 65 IV. Toxicity to Terrestrial Animals a. Birds, Acute and Subacute An acute oral toxicity study using the technical grade of the active ingredient ( TGAI) is required to establish the toxicity of cypermethrin to birds. The preferred test species is either mallard duck ( a waterfowl) or bobwhite quail ( an upland gamebird). Results of acute oral toxicity studies in birds yield an LD50 value of > 9,520 mg a. i./ kg body weight in mallard ducks ( Acc. No. 241598l Acceptable) and an LD50 value of > 2,000 mg a. i./ kg body weight in bobwhite quail ( MRID 44546024; Acceptable), indicating that cypermethrin TGAI is practically non toxic on an acute oral basis in bird. Study details are provided in Table E 9. Taking the most conservative approach, EFED will use the lowest LD50 value of > 2,000 mg a. i./ kg body weight in bobwhite quail to assess the risk of acute oral exposure of birds to cypermethrin. The guideline ( 71 1) is fulfilled.

No acute oral toxicity studies of cypermethrin formulations or cypermethrin degradates in avian species were submitted.

Table E 9: Acute Oral Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Birds Species % a. i. LC50 Toxicity Category Identification Number Study Classification Technical grade Cypermethrin Anas platyrhynchos ( mallard duck) 92.9 Single doses of 0 and 9,520 mg a. i./ kg body wt to males and single doses of 0 and 11,227 mg a. i./ kg body wt to females; birds observed for 21 days.

No mortalities in any treatment group. No gross abnormalities post mortem. Several birds in the test groups attempted to vomit,

but only one bird was seen to reject any of the dose material, and this appeared to be only a very small proportion of the dose.

No other abnormal signs were observed, and the birds appeared to remain in good health throughout the study.

LD50 ( males): > 9,520 mg a. i./ kg body wt LD50 ( females): > 11,227 mg a. i./ kg body wt Practically non toxic Accession No. 241598 ( Ross et al. 1977) Acceptable Table E 9: Acute Oral Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Birds Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 66 Beta Cypermethrin Colinus virginianus ( bobwhite quail) 97.1 Avian single dose LD50 test. Concentrations ( nominal) tested:

0 ( 0.5% methylcellulose vehicle control), 500, 1000, and 2000 mg a. i./ kg body weight.

No treatment related signs of toxicity and no mortalities were observed in the dosage groups.

LD50: > 2000 mg a. i./ kg NOAEL = 2000 mg a. i./ kg Practically non toxic MRID 44546024 ( Johnson 1998) Acceptable Two subacute dietary studies using the TGAI are required to establish the toxicity of cypermethrin to birds. The preferred test species are mallard duck and bobwhite quail. Results of subacute dietary studies are tabulated below in Table E 10. In mallard ducks, acute LC50 values range from > 2,634 mg a. i./ kg diet ( MRID 90071; Acceptable) to > 5290 mg a. i./ kg diet ( MRID 44546025; Acceptable), indicating that cypermethrin TGAI is slightly toxic to practically non toxic to mallard ducks on an acute dietary basis. Similar results were reported for the studies in bobwhite quail; acute LC50 values range from > 3,951 mg a. i./ kg diet ( MRID 90072; Acceptable) to > 5,290 mg a. i./ kg diet ( MRID 44546026l Acceptable), indicating that cypermethrin TGAI is slightly toxic to practically nontoxic to bobwhite quail. Taking the most conservative approach, EFED will use the lowest LC50 value of > 2,634 mg a. i./ kg diet in mallard ducks to assess the risk of acute dietary exposure of birds to cypermethrin. The guideline ( 72 1) is fulfilled.

No acute dietary toxicity studies of cypermethrin formulations or cypermethrin degradates in avian species were submitted.  E 67 Table E 10: Acute Dietary Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Birds Species % a. i. LC50 Toxicity Category Identification Number Study Classification Technical Grade Anas platyrhync hos ( mallard duck) 87.8 cis: trans = 53: 47 Dietary concentrations: 0, 1756, 2634, 3951, 5926, 8889, 13333, and 20000 ppm a. i ( mg a. i./ kg diet)

Ducks had an aversion to dietary concentrations of cypermethrin > 2634 ppm; thus, it is unclear whether observed reductions in body weight gain and food consumption were related to toxic effects of cypermethrin or this aversion. The EPA reviewer corrected the LC50 value for this aversion effect.

Dietary LC50: > 2,634 ppm a. i. Slightly toxic MRID 90071 ( Roberts et al.

1980) Acceptable Colinus virginianus ( bobwhite quail) 87.8 cis: trans = 53: 47 Birds fed 0, 1756, 2634,

3951, 5926, 8889, 13333, and 20000 ppm a. i. ( mg a. i./ kg diet) in the diet.

Quail had an aversion to dietary concentrations of cypermethrin > 3951 ppm. It is unclear whether observed reductions in body weight gain and food consumption were related to toxic effects of cypermethrin or this aversion. The EPA reviewer corrected the LC50 value for this aversion effect.

Dietary LC50: > 3,95l ppm a. i. Slightly toxic MRID 90072 ( Roberts et al.

1981) Acceptable Table E 10: Acute Dietary Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Birds Species % a. i. LC50 Toxicity Category Identification Number Study Classification  E 68 Beta Cypermethrin Anas platyrhync hos ( mallard duck) 97.1 Concentrations ( nominal) tested: 0, 163, 325, 650, 1300, 2600, and 5200 ppm a. i.. Measured concentrations: 168, 315, 633, 1290, 2550, and 5290 ppm a. i. Five day exposure period followed by a 3 day observation period.

A reduction in body weight gain was observed in the 5200 ppm group during the exposure period. Feed consumption values were reduced for the 2600 and 5200 ppm a. i. groups during both the exposure and observation periods. No mortalities observed.

LC50: > 5290 ppm a. i.

NOAEC = 1290 ppm a. i. Practically non toxic MRID 44546025 ( Johnson 1998) Acceptable Colinus virginianus ( bobwhite quail) 97.1 Concentrations ( nominal) tested: 0, 163, 325, 650, 1300, 2600, and 5200 ppm a. i. Measured concentrations: 168, 315, 633, 1290, 2550, and 5290 ppm a. i. Five day exposure period followed by an 11 day observation period.

There was a reduction in body weight values only in the 5200 ppm group during the exposure and observation periods. Food consumption was not affected at any treatment level.

LC50: > 5290 ppm a. i. ( based on measured concentrations)

NOAEC: 2550 ppm a. i. ( based on measured concentrations) Practically non toxic MRID 44546026 ( Johnson 1998) Acceptable  E 69 b. Birds, Chronic Avian reproduction studies using the TGAI are required for cypermethrin because birds may be subject to continuous exposure to the pesticide, especially preceding or during the breeding season. The preferred test species are mallard duck and bobwhite quail. Results of reproductive studies in mallard ducks ( MRID 90073; Acceptable) and bobwhite quail ( MRID 90074; Acceptable) show no treatment related effects on adult birds, reproductive parameters, or offspring ( Table E 11) at the highest dietary concentrations tested in these studies ( 50 mg a. i/ kg diet). EFED will use the NOAEC value of > 50 mg a. i/ kg diet to assess chronic risk of cypermethrin in avian species., however, the avian reproduction study must be repeated and a LOAEC determined. The guideline ( 71 4) is not fulfilled. No chronic toxicity studies of cypermethrin formulations or cypermethrin degradates in avian species were submitted.

Table E 11: Chronic Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Birds Species % a. i. LC50 Identification Number Study Classification Technical Grade Cypermethrin Anas platyrhynchos ( mallard duck) 87.8 cis: trans = 53: 47 Adults fed 0, 5, or 50 ppm a. i. in the diet for 11 wks before the start of the egg laying period, which lasted 12 weeks.

No treatment related effect on adults ( adult food consumption and body weight) or reproductive parameters ( number of eggs laid and proportion damaged, egg weight, eggshell thickness, number of infertiles , embryonic deaths, hatchings, 14 day old surviving ducklings, and duckling body weights at hatching and 14 days later).

NOAEC: > 50 ppm a. i. MRID 90073 ( Roberts et al. 1981) Supplemental Table E 11: Chronic Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Birds Species % a. i. LC50 Identification Number Study Classification  E 70 Colinus virginianus ( bobwhite quail) 87.8 cis: trans = 53: 47 Adults fed 0, 5, or 50 ppm a. i. in the diet for 19 wks before the start of the egg laying period, which lasted 12 weeks.

No treatment related effect on adults ( adult body wt and food consumption) or reproductive parameters ( number eggs laid and proportion damaged, egg weight and shell thickness, number of infertiles, embryonic deaths, hatchlings, 14 day old survivors, and chick body weights at hatching and 14 days later).

NOAEC: > 50 ppm a. i. MRID 90074 ( Roberts et al. 1981) Supplemental c. Mammals, Acute and Chronic Wild mammal testing is required on a case by case basis, depending on the results of lower tier laboratory mammalian studies, intended use pattern and pertinent environmental fate characteristics. In most cases, rat or mouse toxicity values obtained from the Agency's Health Effects Division ( HED) substitute for wild mammal testing. Results of pertinent toxicity studies in laboratory mammals on cypermethrin are reported below in Table E 12. Results of the acute oral toxicity study yield an LD50 value of 247 mg a. i./ kg body weight in male rats ( MRID 00056800; Acceptable); this value will be used to assess the acute risk of cypermethrin to terrestrial mammals. Results of 3 generation reproductive studies in rats yield NOAEL values for toxicity to both parents ( decreased body weight gain) and offspring ( decreased weight gain during lacation in pups) ranging from 100 mg a. i./ kg diet ( MRID 00090040; Acceptable) to 150 mg a. i./ kg diet ( MRIDs 00112912, 42068504, 92027040l Acceptable). Taking the most conservative approach, EFED will use the lowest NOAEL value of 100 mg a. i./ kg diet ( MRID 00090040) for toxicity to parents and offspring to assess chronic risk to terrestrial mammals.  E 71 Table E 12: Toxicity of Cypermethrin to Mammals Species % a. i. Toxicity Value Identification Number Study Classification rat tech Males: LD50 = 247 mg a. i./ kg body weight Females: LD50 = 309 mg a. i./ kg body weight Deaths: $ 150 mg/ kg, usually in first day.

Clinical signs of neurotoxicity, gait abnormalities; some persisting to 14 days.

Based on acute LD50 values, cypermethrin is categorized as moderately toxic. MRID 00056800 Acceptable rat 90.6 to 93.1 3 generation reproduction study. Dietary concentrations of 0, 50, 150 or 1000/ 750 ppm ( reduced to 750 ppm after 12 weeks because of severe neurological symptoms). These dose levels correspond to 2.5, 7.5 or 50/ 37.5 mg/ kg/ day.

The parental/ offspring LOAEL is 750 ppm ( 50/ 37.5 mg/ kg/ day) based on consistent decreased body weight gain in both sexes in the parents and decreased mean litter weight gain during lactation.

The parental/ offspring NOAEL is 150 ppm ( 7.5 mg/ kg/ day; the decreases in mean body weight and body weight gain at 150 ppm are not considered to be toxicologically significant). MRIDs 00112912, 42068504, 92027040 Acceptable rat 98 3 generation ( 2 litters/ generation) reproduction study. Dietary concentrations of 0, 10, 100 or 500 ppm. These dose levels correspond to 0, 0.5, 5 or 25 mg/ kg/ day.

The parental LOAEL is 50  37.5 mg/ kg/ day based on decreased body weight gain. The parental NOAEL is 7.5 mg/ kg/ day.

The offspring LOAEL is 50  37.5 mg/ kg/ day based on a decrease in pup body weight gain on lactation day 21 for one or both sexes of one or both litters of each generation. The offspring NOAEL is 7. 5 mg/ kg/ day. MRID 00090040 Supplementary  E 72 d. Terrestrial Insects, Acute Contact A honey bee acute contact study using the TGAI is required for cypermethrin because its outdoor treatment use will result in honey bee exposure. The acute contact LD50, using the honey bee, Apis mellifera, is an acute contact, singledose laboratory study designed to estimate the quantity of toxicant required to cause 50% mortality in a test population of bees. The TGAI is administered by one of two methods: whole body exposure to technical pesticide in a nontoxic dust diluent or topical exposure to technical pesticide via micro applicator. The median lethal dose ( LD50) is expressed in micrograms of active ingredient per bee (: g a. i./ bee). One acute contact study on the cypermethrin TGAI in honey bees was submitted ( Acc. No. 260647; Acceptable); details are provided in Table E 13a. Based on the 48 hour contact LD50 value of 0.023 : g a. i./ bee, cypermethrin TGAI is classified as highly toxic to honey bees.

Acute contact tests LD50 values in honey bees were also determined for cypermethrin formulations, as summarized in Table E 13b. Results are similar to those reported for the acute contact toxicity of cypermethrin TGAI, with 48 hour contact LD50 values ranging from 0.088 : g a. i./ bee ( 44544208; Acceptable) to 0.13 : g/ bee ( Acc. No. 260647; Acceptable), indicating that the cypermethrin formulations are highly toxic to honey bees. Results of a test investigating the effects of toxicity of cypermethrin residues on foliage was conducted with the cypermethrin formulation Cymbush 3E ( 35.6% a. i.) ( Acc. No. 40274001; Acceptable). When applied at a rates equivalent to 0.06 and 0.13 lb a. i./ A, exposure to residues on foliage resulted in approximately 75 95% mortality after a 24 hour exposure. The foliar application rates used in this study are similar to the maximum single application rate of 0. l lb a. i./ A considered in this assessment.

Table E 13a: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Honey Bees Species % a. i. LC50 Toxicity Category Identificatio n Number Study Classification Technical Grade Cypermethrin Apis mellifera ( honey bee) 91.5 Acute contact toxicity test. Bees anesthetized and 0 ( acetone solvent control), 0.01, 0.02, 0.05, 0.1, 0.2 and 0.5 µ g a. i./ bee, applied to the thorax 24 hr contact LD50 = 0.037 : g a. i./ bee[( 95% C. I. ( from unclassified MRID) = 0.022 0.055]

48 hr contact LD50 = 0.023 : g a. i./ bee [ 95% C. I. ( from unclassified MRID) = 0.018 0.029] Highly toxic DER for Accession No. 260647 ( Bull and Wilkinson 1980); appears to be the same unclassified study MRID 155740 ( Bull and Wilkinson 1980) Acceptable Table E 13a: Acute Toxicity of Technical Grade Cypermethrin Isomers ( TGAI) to Honey Bees Species % a. i. LC50 Toxicity Category Identificatio n Number Study Classification  E 73 Apis mellifera ( honey bee) 91.5 Acute oral toxicity test. Each group of bees fed 0 ( acetone solvent control), 0.05, 0.1, 0.2, 0.45, 0.87, and 1.64 µ g a. i./ bee in sucrose solution.

24 hr oral LD50 = 0.181 : g a. i./ bee ( 95% C. I. from MRID study = 0.117 0.263)