Document VGQ0QO47bGkVVLdKe8XNE54zN

Tft/ Taft Stettinius & Hollister LLP 425 Walnut Street, Suite 1800/Cincinnati, OH 45202-3957 /Tel: 513.381.2838 / Fax: 513.381.0205 / www.taftlaw.com Cincinnati / Cleveland / Columbus / Dayton / Indianapolis / Northern Kentucky / Phoenix / Beijing Robert A. Bilott 513.357.9638 bilott@taftlaw.com July 14, 2009 TSCA Confidential Business Information Center (7407M) EPA East - Room 6428, Attn: Section 8(e) & FYI U.S. Environmental Protection Agency 1200 Pennsylvania Avenue, NW Washington, DC 20460-0001 Re: Submission To TSCA 8(e)/FYI Database Re: PFOA/PFOS To TSCA 8(e)/FYI Database: We are hereby providing the following information for inclusion in the TSCA=8(e)/ FYI databases with respect to PFOA/PFOS: 1. Steenland, K., et al., "Predictors of PFOA Levels in a Community Surrounding a Chemical Plant," 117 Environ. Health Perspectives 1083-88 (July 2009); 2. Frisbee, S.J., et al., "The C8 Health Project: Design, Methods, and Participants," Environ. Health Perspectives (Online edition) (doi: 10.1289/ehp.0800379)(online July 13, 2009); and 3. C8 Science Panel, Study Summary/Status Report (July 8, 2009). RAB:mdm Enclosure 11461999.1 89090000334 Contains Ho CM * "A N S NOCB 3 X )5 9 n P-2 Research Predictors of PFOA Levels in a Community Surrounding a Chemical Plant Kan d f n n T l r X (Lhuangfan9 Jin '2 Jessica MacNeil.' Cathy Lally,' Alan Ducatman * Veronica Vieira,* BA CK G R U N D : Pcrfluorooctanoic acid (PFOA) is considered a probable human carcinogen by the vv/ l i 7 ^ ,/ 0n,T T t J Protect,on Ae ency- h does n oust in nature but has been used widely since Worid War II. It is present in the scrum o f most Americans at about 4 -5 ng/mL, although the routes or exposure remain unknown. " O BJEC T IV ES: We examined predictors o f PFOA in mid-Ohio Valley residents living near a chemical plant that until recently released large quantities o f PFOA into the environment, contaminating drinking water. & died 69,030 residents in six contaminated water districts who participated in a SUnCy mvtJvinB * questionnaire and blood tests. O f these. 64,251 had complete data on PFOA and covariates. W e also analyzed a subset (71%) for whom we had occupational history We ran linear regression models to determine serum PFOA predictors. in 2 0 0 5-2006 and gathered data from 69,000 O hio and West Virginia residents who lived in six contaminated water districts surround ing the chemical plant. The C8 Health Project included blood draws and subsequent measurement o f serum PFOA (West Virginia University 2009). The present study is an analysis o f these data to study factors associ ated with PFOA levels. Materials and Methods RESULTS: Mean PFOA serum level was 83.0 ng/mL (median. 28.2). The most important predic tors were current (median for all districts, 38.4; highest district, 224.1) and past (median/ 18 6) residence in contaminated water districts, and current (median, 147.8) and past (median 74 9) employment at tire chemical plant (/? model . 0.55). PFOA was higher for males, those consum ing load vegetable, and those using well water rather than public water, and lower for those using bottled water. PFOA was higher at younger and older ages. C onclusions: PFOA levels in this population varied with distance o f residence from the plant and employment at the plant. Effects o f age and sex reflected prior findings. Effects o f other demo graphic and lifestyle covariates were relatively weak. K w wowos: PFOA, serum levels, water contamination. Environ Health Penpect 117:1083-1088 (2009). doi:10.1289/ehp.0800294 available via http:lldx.douorgl (Online 23 March 2009] Pcrfluorooctanoic acid (PFOA, or C8) docs not occur in nature. It is used as a polymerization aid in the manufacture ol several types o f fluo ropolymers, which are used in a wide variety of industrial and consumer products, including extensive use in the manufacture o f Teflon. PFOA does not break down once in the envi ronment, leading to widespread buildup and bioaccumulation. The half-life o f PFOA in human serum has been estimated to be about 4 years (Olsen ct a! 2007). Most people in the United States have measurable PFOA in their serum, with a median o f 4 ng/mL in 2003 2004 (CaJafat ct al. 2007b), although the exact sources o f this exposure are not clear. PFOA causes cancer o f the testicles, liver, and pancreas in rodents, and there is some evidence that it also causes breasr cancer in rodents [U S . Environmental Protection Agency (EPA) 2005). It also causes fetal loss and low birth weight in mice and immunotoxic and hepatoxic effects in rodents (U S. EPA 2005). Health effects in humans are not well established. Ihere have been some reports of associations with lower birth weight (Apelberg ct al. 2007; Fei et aJ. 2007), higher cholesterol (Sakr ct al. 2007a, 2007b), and impaired liver function (Olsen et al. 2007), bur these effects arc usually modest, and the literature is sparse. Mortality studies of workers have shown increases in some causes o f death but have not been consistent and have been based on relatively small numbers o f deaths (Gilliland and Mandel 1993; Leonard et al. 2007). PFOA has been used in the manufactur ing o f fluoropolymers at a chemical plant in Washington, West Virginia, since 1951, with use peaking in the late 1990s. PFOA is used a surfactant in the polymerization o f rrifluorocthylenc to make Teflon. Ir entered the groundwater via both air em issions, which were deposited on the soil around the plant and leached downward, and emissions into the Ohio River, which then entered the groundwater that communicates with the river. Public drinking water comes from wells pumping from the groundwater, which are located close to the river. Some local landfill sites may have also contributed to ground water contamination. Emissions have been sharply reduced in the past few years. There is evidence that drinking water is the primary route of exposure for the population living in these districts (Emmett et al. 2006). In 2001, a group o f residents from the O hio and W est Virginia com m unities in the vicinity o f the plant Piled a class-action lawsuit alleging health damage due to con tamination o f human drinking water sup plies with PFOA. The settlement o f the class action lawsuit led to a baseline survey, called the C8 Health Project, which was conducted Study participants. The C8 Health Project, conducted by Brookmar Inc., began data collection in August 2005 and com pleted it in August 2006. Its purpose was to col lect health data from class members through questionnaires and a battery o f blood tests, including a test to ascertain the concentra tion o f PFOA in the scrum. Subjects were eli gible to participate in the C8 Health Project if they had consumed drinking water for at least 1 year before 3 December 2004 sup plied by Little Hocking Water Association (O h io), C ity o f Bclprc (O h io), Tuppers Plains Chester Water District (Ohio), Village o f Pomeroy (O hio), Lubeck Public Service District (West Virginia), Mason County Public Service District (West Virginia), or private water sources within these areas that were contaminated with PFOA. Subjects were also eligible if they could document that they had either worked in a contaminated water district or went to school there for at least 1 year. Figure 1 shows the six water districts. Subjects were compensated $400 if they filled out the extensive questionnaire and came to local survey stations to donate a blood sample. Address correspondence to K. Srecnland, Rollins School o f Public Health, Emory University, 1518 Clifion Rd,, Atlanta, GA 30322 USA. Telephone: (404) 712-8277. Fax: (404) 727-8277. E-mail: n ste en l^sp h . cmory.edu We thank D. Savitz for comments. This research is funded by the C8 Class Action Settlement Agreement (Circuit Court of Wood County, WV. USA) between DuPont and plaintiffs, which resulted from releases into drinking water of the chemical pcrfluorooctanoic acid (PFOA, or C8) Funds were administered by the Garden City Group (Melville, NY) that reports to the court. O ut work and conclusions are independent of either party to the lawsuit. The authors declare they have no competing financial interests. orvRnenceived 18 October 2008; acce1pted 23 March Environmental Health Perspectives VOIUME 1171 NUMBER 7 IJuly 2009 1083 P-3 Steenland et al. A full description of the C8 Health Project is in preparation. The C8 Health Project collected data on 69,030 subjects. It is not known what percent age o f the eligible population participated, because the eligible population was not enu merated (the past populations o f the water districts are not known, nor are the number o f eligible people who lived outside the water districts but went to school or worked there). Nonetheless, it is believed that most partici pated, given the widespread public interest and the financial incentive. We have estimated the participation rate among current residents in 2005-2006 among adults > 20 years o f age using census data (the population > 18 years of age, as studied here, was not available from the census). Estimates o f the population o f the sue water districts were made based on population estimates for census block groups in 2005. Block groups are smaller than census tracts but larger than census blocks. To find the popu lation o f each water district, we determined which block groups were entirely within the water district. We then determined which block groups intersected the boundaries o f the water districts. For those which intersected, we then calculated the ratio o f water district area to block group area within each block group and multiplied the ratio by the block group population. We then summed the populations lor the entire water district and then summed across all six water districts. Finally, we deter mined the numbers of current residents (63% o f total participants) in the water districts who participated in the C8 Health Project in 2005-2006, and divided this number (33,001 residents) by the population (40,721 residents) to find an estimated participation rate o f 81% among current residents > 20 years o f age. I Y Statistical analysis. It was expected a priori that water districts would play an important role in predicting exposure, with subjects in water districts more distant from the plant likely to have lower serum levels. Subjects in the C8 Health Project were required to docu ment past or present consum ption o f con taminated public water from one o f the six contaminated water districts (cither via living in the water district for at least 1 year, or by working or going to school there for at least 1 year; n = 68,873), or having drunk from private wells with documented contamination (n = 157). This documented water district o f exposure is called the "qualifying" water district. Sixty-three percent o f the popula tion reported currently drinking public water (as their main water source) in one o f the six water districts. We classified water district into 12 groups: six for currently (2005-2006) drinking public water in one o f the six con taminated water districts, and six for not currently drinking public water but having previously been exposed by drinking water in one o f the six water districts. Among those classified by their qualifying water district, 73% o f these had a record o f having lived or worked in the past in their qualifying water district, with the remainder presumably hav ing gone to school there (no data were avail able on school history). Hereafter, we loosely describe these variables as "current" (2005 2006) and "past" exposure, because most o f those not currently drinking contaminated public water qualified for the study because of having drunk contaminated water in the past. Besides age, race, sex, and water district, other a priori variables o f interest were having worked at the chemical plant, growing your own vegetables, and drinking bottled water (Emmett ct al. 2006). Detailed employment history was available for only adult study sub jects who consented to make available iden tifiable information to the authors as part o f future follow-up studies (7 1%). We restricted analyses using a variable for current or past employment at the chemical plant to that sub set. Our initial model was based on including these a priori variables found to be important in previous studies, as well as the variables for water district. The initial model then included current or past water district, occupational Table 1. Descriptive statistics of mid-Ohio Valley residents exposed to PFOA |n = 69,030) Variable* No. (%) Blood PFOA in 69.030(100) 2005-2006 Age (years) 0-9 4,915(71) 10-19 9.658(14 01 20-29 10.073 (14.61 30-39 40-49 10.547(153) 12.113(176) 50-59 10,515(15 2) 60-69 i 70 6,881 (100) 4.328(63) Sex Male 33.242148 2) Female 35.788 (51 8) Race White 66.989 (97) Nonwhite 2.041 (3) BMI <24 18,849(281) 24-26 27-29 12,501(18 6) 11.B00 (17 6) a 30 24,005(35 8) Worked at chemical ptenE Yes, current 1.171 (2.4) Yes, previous 1.447 (2.9) No 45.276 (94.9) Grow own vegetables Yes 16.015(23 2) No 53.015(76 8) Currently resident in water district Belpre Tupper Plains Little Hocking Lubeck Mason County 5.388 (7.8) 9,703(14 1) 8.390112 2) 8.289(12.0) 10.066 (14 6) Pomeroy 1.56012.3) Median PFOA |ng/mL| 28.2* 328 26 6 21.0 22.7 28.0 33.6 429 40.1 33 7 237 28 1 295 27 9 29.1 308 26.1 147.8 74.9 24.3 341 26.7 35.0 37 2 224 1 669 124 12.1 Variable* No. 1%) Belpre 3.387 (4 9| Tupper Plains 4.359(6.3) Little Hocking 4.465(6.5) Lubeck 8.552(12 4) Mason County 2.711(3.9) Pomeroy Vegetarian 2.016(2.9) Yes 502(0 7) No 68.528(99.3) Consumed alcohol in last 3 days Yes 8.B83I131) No 59.029 (86.9) Current smoking Yes No Former smoking 14.847 (21.5) 54.088(78.5) Yes 14.697(21 3) No 54.280(78.7) Regular exercise Yes 22,072(32.0) No 46,958(68.0) Bottled water Yes 3.728(5 4) No 65.302(94.6) Well water Yes 4,434 (6 4) No Date of testing 64,596(93.6) First 2 months Second 2 months Third 2 months Fourth 2 months Filth 2 months Last 2 months 10.284(14.9) 14,046(20.4) 15.524(22 4) 14.948(21 7) 8,756(12.7) 5,472(7.9) Median PFOA (ng/mL) 17.3 13.6 33.7 28.4 10.5 11.0 24.5 28.2 334 27.6 25.3 293 31.2 27.5 30.3 27.3 31.3 28.0 21.7 28.7 48 9 399 288 23 8 17.8 14.7 Figure 1. Six contaminated water districts of the C8 Health Project. 83.6 n g/m L geom etric mean 32.9 ng/mL. Oat. on w o rkin g at ch em ical p lan t w e re available lo r only 71% of the p o p u to io n . 1084 voLUMt 1171 number 7 I July 2009 Environmental Health Perspectives P-4 PFOA levels in a community exposure (for the subset with available data), eating local vegetables, use o f bottled water, age, sex, and race (white vs. nonwhite). We included the entire population ( = 6 9 ,0 3 0 ) in analyses using the above regression model (absent occupational expo sure, available on a subset), to which we added a large number of other potentially important variables, ultimately retaining those that had a significant association (at p S 0.05) w ith PFOA. Because the population is so large and any variable only slightly associated with PFOA may be statistically significant, this strategy o f model building led to inclu sion in the final model o f variables statisti cally associated with PFOA levels but without any important contribution to explaining the overall variance o f PFOA. We adopted this strategy partly because o f the exploratory nature o f this analysis and the minimal prior data on factors associated with PFOA in the general population. Results from regression models in which the log o f PFOA was the outcome were transformed back to the origi nal unlogged scale, resulting in multiplicative effects for predictor variables. All predictor variables in the regression were categorical. Predicted values were reported as a percent change compared with baseline values for each categorical variable in the regression. All regression models used the natural log transformation o f PFOA because the log transform was more normally distributed; we checked residuals for normality. Laboratory m ethod fo r PFOA. Analyses were conducted by a large commercial lab (Hxygen, State College, PA, USA). PFOA is customarily measured in the scrum, where virtually all PFOA in whole blood may be found (Fhresman et al. 2007). The analyti cal method for measurement o f PFOA in the serum, which was used in this study, has been described in detail previously (Flaherty et al. 2005; Longneckcret al. 2008). Briefly, the method uses liquid chromatography separa tion with detection by tandem mass spectrom etry. The approach allows for rapid throughput using a 96-w ell plate and can handle large numbers of samples. Extraction o f the serum or plasma samples was done using acetonitrile. Chromatography on the extract was done using a quaternary pump and vacuum degas ser. Ihc mobile phases consisted o f two sys tems: a 2 mM ammonium acetate solution, and methanol with gradients set up to ensure both rapid and complete separation. The lab used ,3C-PFOA at a concentration o f 1 ng/ mL as its internal standard. Mass spectrom etry was done in selected reaction monitoring mode with m fz = 413 -> 369 as the principal ion monitored for PFOA (m lz = 370 for the C internal standard). Fortification recoveries using rabbit serum or plasma as the matrix for PFOA were generally within 90-110% . The coefficient o f variation based on multiple sam ples between batches was generally < 0.10 over the range of 0.5--40 ng/mL, with a more pre cise relative coefficient o f variation o f approxi mately 0.01 for highly fortified (10,000 ng/ mL) samples (Flaherty et al. 2005). T he lim it o f detection for PFOA was 0.5 ng/m L Only 0.06% o f observations were below the limit o f detection, and we assigned these a value o f 0.25 ng/mL Results Table 1 provides descriptive data for the popu lation. Figure 2 shows the distribution o f PFOA. The log o f PFOA is more normally distributed than PFOA, and use o f it in the regression model for the full population led to residuals that were approximately normally dis tributed (Figure 3). The theoretical 2.5% tails o f the distribution o f the studentized residu als (> 1.96 or < -1 .9 6 ) contained 2.76% and 2.60% o f the data, respectively, conforming reasonably to expectations. Table 2 shows the results o f the final model for the entire population, w ith out inclusion o f a variable for working at the chem ical plant (m odel R1, 0 .5 5 ). We added five additional variables [date o f test ing divided into bimonthly intervals, alcohol consumption in the last 3 days, being a veg etarian, body mass index (BM1), and regular exercise) to variables o f a priori interest in the initial model, based on each being signifi cantly associated with PFOA (p < 0.05) when added to the initial model. Table 2 shows strong effects o f water district, with current residence in water dis tricts closest to the plant having the highest Residual Figure 3. Distribution ol residuals from regression model (Table 2). Environmental Health Perspectives vOlUMf 1171 NUMBfR 7 IJuly 2009 1085 P-5 -Ws.:i,bya*.. Steenlaad et al. PFOA levels. Figure 4 shows the data graphi cally. Currently drinking public water in Little Hocking or Lubeck is associated with the high est levels o f PFOA. The well field for Little Hocking public water is located directly across the river from the plant, and the plant itself is located in Lubeck. Current residence in Belpre and Tupper Plains water districts had the next highest levels. These districts are slightly farther away (Belpre is also upstream). Residents of districts farthest away (Mason, Pomeroy) had the lowest levels. Past consumption o f water Table 2. Multiple linear regression model for the log of PFOA level in all six water districts (model # = 055 n= 64,251). '' Variable__________________ Predicted change (%) in PFOA vs. referent group Age (years) 0-9 10-19 2D--29 30-39 40-49 50-59 60-69 Referent -15 -24 -16 -2 12 23 o Al 26 Sex Female Male BMI Referent 35 <24 24-26 27-29 >30 Grow vegetables Referent 2 2 --4 No Yes Currently resident in water district Referent 11 8elpre 203 Tuppei Plains 200 Little Hocking 1,612 Lubeck 421 Mason County 9 Pomeroy 3 Previously lived or wotked in watei district Prior Belpre Prior Tupper Plains 62 36 Prior little Hocking Prior lubeck 246 169 Prior Mason County Prior Pomeroy Vegetarian -2 Referent No Yes Consumed alcohol in last 3 days Referent -10 No Yes Smoking Referent 7 Never Current Former Bottled water Referent 6 -i No Yes Well water Reletent -6 No Yes Race Referent 17 Nonwhite White Time of blood draw First 2 months Referent 7 Months 3-4 Months 5-6 5 Months 7-8 Months 9-10 Months 11-12 -14 -22 -29 Regression coefficient Ichange in log PFOA (95% Cl)) -0.16 (-0.20 to -0.12) -0.281-0.32 to -0.24) -0.17 (-0.21 to-0.13) -0.021-0.06 to 0.02) 011 (0.07 to 0.15) 0.2110.17 to 0.25) 0.1910.11 to 0 27) 0.30(0 29 to 0.31) 0.021-0 01 to 0 03) 0 021-0.01 to 0.03) -0.041-0.05 to -001) 0.10 (0.08 to 0.12) 1.11 (1.07 t o i 15) 1.10(1.06 to 1.14) 2.84 (2 80 to 2.08) 1.61 (1.61 to 169) 0.09(0.05 to 0.13) 0.03 (-0.03 to 0.09) 0 48 (0.44 to 0.52) 0.29(0.25 to 0.33) 1.22 (1.18 to 126) 0.88 (0.84 to 0 92) -0.01 (-0.05 to 0 04) -0.101-0.18 to -0 02) 0 06(0.04 to 0.08) 0.06 (0.04 to 0.081 -0.01 (-0.03 to 001) -0.06 (-0.08 to -004) 0.11(0.09 to 013) 0 02 (-0 02 to 0.06) 0.06 (0 04 to 0 08) -0121-0.14 to -0 10) -0.151-0.17 to --0 13) -0.251-0.27 to -0.23) -0.34 (-0.38 to -0.30) p-Value <0.0001 <0.0001 < 0.0001 0.24 <0.0001 <00001 <00001 <0 0001 013 0.18 <0 0001 < 0 0001 < 00001 <00001 <00001 <0.0001 <00001 0.27 0 005 <0.0001 <00001 <0 0001 0.57 001 < 0.001 < 0 0001 018 <0 0001 <00001 031 < 0.0001 < 0 0001 < 0.0001 < 0.0001 < 0.0001 Variance (%) in PFOA (partial R2) <1 <1 <1 <1 <1 <1 <1 2.9 <1 <1 <1 <1 37 41 21 5 8.2 <1 <1 <1 <1 4.3 3.2 <1 <1 <1 <1 <1 <1 <1 <1 <1 <1 <1 <1 <1 in Little Hocking or Lubeck was also associ ated with elevated levels, although less than for those currently residing in chesc water districts. The median level for current residents o f any water district was 38.4 ng/mL, whereas the median for past residents was 18.6 ng/mL Figure 5 indicates that PFOA levels listed in Table 2 show a J-shaped curve with age. Male sex was also strongly associated with increased PFOA levels. Variables other than water district, age, and sex explained less o f the variation in PFOA level. Growing one's own vegetables was associ ated with increased PFOA, whereas drinking bottled water was associated with decreased PFOA. Drinking well water, current smok ing, and drinking alcohol in the last 3 days were positively associated with an increase in PFOA. The alcohol finding could reflect some unknown aspect o f increased liver activity (protein and lipid production). Table 2 shows an approximate 30% decrease in levels over the year o f testing (2005-2006), which results largely from resi dents outside the six water districts (37%) who were no longer exposed and whose blood levels dropped as they excreted PFOA. N ote that the 34% decrease over time contrasts with the much sharper decrease seen in the unadjusted Walai district Figure 4. PFOA level (geometric mean) by current and former water district. Current water district refers to living in exposed water district in 2005-2006 at time of blood draw. Prior water district refers to having either lived, worked, or gone to school for at least 1 year in one of the six exposed water districts. Model prediction compared with observed median value of 11.50 ng/mL for Prior Pomeroy. Age (years) Figure 5. Predicted PFOA serum level (geometric mean) by age: model prediction compared with observed median value of 32.0 ng/mL for age group 0-9 years. 1086 voiume 1171number 7 1July 2009 Environmental Health Perspectives P-6 PFOA levels in a community data in Table 1; this greater decrease reflects the greater participation o f residents from lowexposure areas toward the end of the year-long study, which does not appear in the adjusted results in Table 2, based on the model in which we included water district as a variable. BM1 (> 30), prior water district, date o f test ing, growing your own vegetables, being a vegetarian, current alcohol consumption, and using well water changed by S 10%. The coef ficients for race, current and former smoking, BM1 (first two categories), and using bottled Olsen ct al. (2007) studied 140 Red Cross donors in 2000 and 2005 with background levels o f exposure and found that men had significantly higher scrum levels o f PFOA than did women but that there were no trends with age. Kannan et al. (2004) studied H igh BM1 was associated w ith lower water changed by > 10%, indicating they 473 serum samples from many countries and PFOA levels. W hite race slightly increased were more affected by outliers. They were found that PFOA was present in most samples PFOA but was not statistically significant. among the least important predictors, none from industrialized countries but found no W e did not include socioeconom ic status of which had a partial correlation coefficient significant differences by sex or age. Emmett (SES) in the model. There was a weak positive > 1%; the coefficients for race, BM1 (first two et al. (2006) studied 371 highly exposed sub trend between household income and PFOA categories), and former smoking were not sta jects drinking PFO A-contam inated water concentration, and a stronger (contradictory) tistically significant in the lull model. (median level - 354 ng/mL), residing near negative trend between years o f schooling and Sim ilarly, for sen sitiv ity analysis we the same plant under study here. They found PFOA for those > 30 years o f age. These con restricted the analysis to 50% o f the data after a J-shaped relationship with age (high expo flicting results do not lend themselves to any generating a uniform random number and sure at young and old ages). They also found simple conclusion regarding an association of taking those in the lower half, to see how sta that eating locally grown vegetables increased PFOA and SES. ble our results were. The model R2was again PFOA levels, whereas drinking bottled water We conducted further analyses restrict 55%. In this analysis, however, there was decreased serum PFOA levels. Work at the ing the data set to the 71% o f the popula more variation in the estimated model coeffi nearby plant sharply increased PFOA levels tion with em ploym ent history, and adding cients. Ten o f 35 coefficients changed > 20%, in serum. Holzer et al. (2007) studied 355 a variable for working at the chemical plant although all had the same sign (positive or exposed and 236 nonexposed com m unity to the model in Table 2. Overall, the Ft2 for negative). Those that changed were among subjects in Germany. The exposed subjects the model for this subset was 58%, similar to the least stable; 7 o f the 10 were not signifi drank water contam inated with fluoropo the R2o f 55% for the model with all subjects. cant at the 0.05 level in the split sample, and lymers, predominantly PFOA; the average Currently working at the plant was associ six o f these had not been significant in the PFOA serum level was approximately 25 ated with a much higher level o f PFOA [coef original complete data analysis. Overall, all ng/mL. Factors significantly associated with ficient = 1.41; standard error (SE) = 0.03; coefficients had the same direction (i.c., were higher PFOA levels were male sex, higher age, p < 0.0001, partial R2 - 0.06], equivalent to consistently positive or negative in the full drinking larger quantities o f public water, a 309% increase in PFOA compared with and 50% split sample). eating local vegetables, and residing in the someone who had never worked at the plant. Prior work at the plant was also associated Discussion exposed versus nonexposed area. Here we have studied such factors in by with a higher level (coefficient = 0.44; SE - PFOA is an important chemical introduced far the largest population to date. This popu 0.02; p < 0.0001; partial R2 = 1%), equiva after WW1I and now found in virtually the lation has been exposed to PFOA primarily lent to a 55% increase in PFOA compared entire U.S. population. The routes o f expo through drinking water contamination from with someone who never worked at the plant. sure in the general population are not known. a nearby plant, as did the population o f 600 C oefficien ts for other variables remained PFOA is known to have some toxic properties studied in Germany (Holzer et al. 2008). largely unchanged, with the exception of the in animals, but no human health effects have W e have found that markedly higher lev coefficient for white versus nonwhitc. which been clearly established. els o f PFOA were associated with working increased from 0.020 to 0.064 (SE = 0.023; Data remain sparse on factors associ at the chemical plant that was the source o f p - 0.005). W orking at the chemical plant ated with serum levels o f PFOA. Two prior the contamination. Workers who no longer was slightly less common for whites than for studies o f the general population [National worked at the plant had much higher levels nonwhites [odds ratio adjusted for age = 0.79; Health and Nutrition Examination Survey (median, 75) than did nonworkers (median. 95% confidence interval (C l), 0.62--1.00], (N H A N E S) population, 1 9 9 9 -2 0 0 0 , and 24) but lower levels than those who contin such that inclusion o f a variable for working N H A N E S 2 0 0 3 -2 0 0 4 ] found that males ued working there (median, 148), consistent at the plant may have made the estimate o f had higher levels, that there was little trend with a gradual excretion o f PFOA from the race more accurate (i.c., occupational expo with age, that whites had higher levels than body after ending high exposure. Other occu sure was a negative confoundcr for the effect Hispanics and blacks, and that increased edu pational data (Sakr et al. 2007a) have shown o f white vs. nonwhite). cation was associated with higher serum lev that 1,000 workers at the plant in 2004 had a As a sensitivity analysis, we reran the els o f PFOA (Calafat et al. 2007a, 2007b). mean serum level o f 428 ng/mL. This is virtu model in Table 2 after eliminating the top R2 values for regression m odels were not ally identical to the mean scrum level we have 1% and bottom 1% o f the distribution o f reported. These findings sometimes failed to found in our data for the subset o f workers studentized residuals, to consider the pos reach statistical significance and sometimes currently at the plant (427 ng/mL) in 2005 sible influence of outliers. This analysis, with were apparent only in certain age groups. 2006 (the PFOA distribution among workers 98% of the original data, increased the R2 of Both studies were restricted to adults. Further was highly skewed, accounting for difference the model from 55% to 63%, as might be research using N H A N ES data for children between the mean and median serum levels, expected. However, this led to little change in has shown that children had higher PFOA 427 versus 147 ng/mL for current workers). most model coefficients, especially the most levels than did adults (Calafat A, personal The other main factor influencing PFOA important predictors. All the same variables communication, May 2008). PFOA levels in levels in the population studied here was the were statistically significant or not statistically the United States may be decreasing in the distance o f residence from the plant. Current significant as in the original analysis, with past several years since several manufacturers residence in water districts near the plant (e.g., the exception of race, which became statis have stopped or drastically reduced the use Little Hocking and Lubeck) was associated tically significant without the outliers. The o f PFOA (Calafat ct al. 2007b; Olsen et al. with the highest levels. Those with prior resi coefficients for age, sex, current water district, 2007). dence near the plant also had high levels, but Environmental Health Perspectives vouimf 117 1number 7 I July 2009 1087 p.7 Steenland et al. much less than those living there currently, again consistent with the gradual excretion of PFOA once high exposure ceases. This analy sis via distance of water district from the plant is crude; a more comprehensive analysis using geocoding o f past and present addresses, as well as estimates o f annual emissions from the plant, is under way. Demographic and other environmental factors played much less important roles. Male sex was the most important demographic fac tor associated with higher levels. Age showed a J-shaped relationship with serum PFOA, with higher levels in the young and the old, similar to what has been found previously by F-mmctt ct al. (2006) and Calafat et al. (per sonal communication. 2008). The reasons for these demographic patterns are not known. Wc also found a trend o f decreasing levels o f PFOA over time during this 1-year study, which was primarily due to decreasing levels among people no longer living in the six water districts and therefore no longer exposed. In conclusion, PFOA levels are far above background in this population that has con sumed contaminated drinking water. Further studies are under way to determine whether PFOA is associated with health effects in this population. References Apelberg BJ, W itte r FR, Hertntm an JB , Calafat A M , Helden RU, Needham LL, et al. 2007. Cord serum c o n c e n tra tio n ! of p erfluorooctene sulfonate (PFOS) and p erfluo ro octa no ate (PFOA) in relation to w e ig ht and size at birth. Environ Health Perspect 115:1670-1676. Calafat A M , Kuklenyik Z, Reidy JA, C audill SP, Tully JS, Needham I L 2007a. Serum c o n ce n tra tio n s of I I polyftuo ro elkyt com pounds in the US population: data fro m the N ational Health and N u trition Exam ination Survey fNHANES). Environ Sei Technol 412237-2242. C alafat A M , W ong LY, K uklenyik Z. Reidy JA , Needham LL 2007b. Polyfkioroalkyl chem icah in the U.S. population: data from the National Health and Nutrition Examination Survey (NHANES) 2003-2004 and com parisons w ith NHANES 1990-2000. Environ Health P erspect 115:1596--1602. Ehresm an D J, F o re h lic h J W , O lsen GW, Chang S-C, B ute nh o tl J L 2007. Com parison of hum an w h ole blood, plasma and serum m atrices to r the determ ination of per* flu oroocanesulfonete (PFOS), p e rfluo ro cta n oa te (PFOA) and other ftuorochemrcals. Environ Res 103:176-194. Emmett EA, Shoter FS, Zhang H. Freeman D. Desai C, Shaw LM. 2006. Community exposure to p e rtluo ro octe no ste: re la tionships between serum concentrations and exposure sources. J Occup Environ M ed 49:769-770. Fei C. McLaughlin JK. Tarons RE, Olsen J. 2007. Perfluormated chem icals and fatal growth: a study w ithin the Oemsh National Birth Cohort Environ HeaMt Perspect 115:1677-1682. Flaherty J M , Connolly PD, Decker ER, Kennedy SM, EHetson ME, Reagan W K, et al. 2005. Q uantitative d eterm ination of perfluorooctanoic acid in serum, and plasma by liquid chrom atography mass sp ectrom etry. J Chrometogr B 819:329-338. Gilliland FD, M endel JS. 1993. M o rta lity among employees of a perfluorooctanoic acid production plant. J Occup Med 35(91:950-954. H lzer J , M id a s c h 0 , R a uch fuss K, K ra ft M , R a u p e n R, A n g e re r J , e l al. 2009. B io m on ito rin g o f p e rftu orina ted com pounds in children end adults exposed to perfluorooctanoate-contam m ated drinking water. Environ Health Perspect 116:651-857. Kennan K, C o rso lin i S, Falandysz J, Fillm ann G, Kumar KS, L og an a th a n BG, e t el. 2004. P e rflu o ro o cta n e su tfo n e te end related fluorochemicals m human blood from several countries. Environ Sci Technol 38:4489-4495. Leo na rd RC, K re ckm a n n KH, S akr CJ, S ym ons J M . 2007. Retrospective cohort mortality study of workers m a poly mer production plant including a reference population of regional w orkers. Ann Epidemiol 18:15-20. Longnecker MP, Smith CS, KissHng GE, Hoppin JA, Butenhotl JL. Decker E, et aL 2008. An intertaboratory study o f perfluorinated alkyl compounds levels in human plasma. Environ Res 107.152-159. Olsen GW, M a ir DC, Raagen WK. 2007. Prelim inary evidence o f a decline in perfluorooctanesutfonete (PFOS) and perfiuorooctanoate (PFOA) concentrations in A m erican Red Cross blood donors. Chemosphere 68:105-111. Sakr CJ, Kreckm ann KH, Green JW , G illies PJ. Reynolds JL, Leonard RC. 2007a. C ross-se ctio na l study of lip id s and liver enzymes related to e serum biomarker of exposure (ammonium perfluorooctanoatB or APF0) as part of a gen era l health survey in e cohort of occupationally exposed workers. J Occup Environ M ed 49:1066-1096. Sakr CJ. Leonard RC, K reckm ann KH, Slade MD, Cullen MR. 2007b. Longitudinal study of serum lipids end liver enzymes in w orkers w ith occupational exposure to ammonium perfluorooctanoate. J Occup Environ M ed 49:872-879. U.S. EPA. 2005. O re ft Risk A s s e s s m e n t o f th e P o te n tia l Human Health Effects A ssociate d w ith Exposure to Perflouroctanoic Acids and Its Salts. U.S. Environmental Protection Agency. Avaiieble: www .epa.gov/oppt/pfoa/ pubs/pfoarisk.htm (accessed 2 February 2009]. W e s t V irg in ia University, Health S ciences Center. C8 Health P ro ject Results. Available: http://ww w.hsc.wvu.edu/sonV cm ed/c8/resultV index.isp (accessed 3 June 2009). 1088 volume 1171number 7 I July 2009 * Environmental Health Perspectives ehponline.org ij IId en v ir o n m en ta l HEALTH PERSPECTIVES The C8 Health Project: Design, Methods, and Participants Stephanie J. Frisbee, A. Paul Brooks, Jr., Arthur Maher, Patsy Flensborg, Susan Arnold3, Tony Fletcher, Kyle Steenland, Anoop Shankar, Sarah S. Knox, Cecil Pollard, Joel A. Halverson, Vernica M. Vieira, Chuanfang Jin, Kevin M. Leyden, Alan M. Ducatman doi: 10.1289/ehp.0800379 (available at http://dx.doi.org/) Online 13 July 2009 National Institute of Environmental Health Sciences N ational Institutes of Health U .S . D e p a rtm e n t o f H ealth and Hum an Services P-9 Page 2 of 38 The C8 Health Project: Design, Methods, and Participants Stephanie J. Frisbee12; A. Paul Brooks, Jr.3; Arthur Maher3; Patsy Flensborg3; Susan Arnold3; Tony Fletcher4; Kyle Steenland5; Anoop Shankar12; Sarah S. Knox1; Cecil Pollard1; Joel A. Halverson1; Vernica M. Vieira6; Chuanfang Jin1; Kevin M. Leyden7; Alan M. Ducatman 1West Virginia University School of Medicine Department of Community Medicine, Morgantown, WV, USA 2West Virginia University School of Medicine Center for Cardiovascular and Respiratory Sciences, Morgantown, WV, USA 3Brookmar, Inc., Parkersburg, WV, USA 4London School of School of Hygiene and Tropical Medicine Public Health and Environmental Research Unit, London, UK 5Emory University Rollins School of Public Health Department of Environmental and Occupational Health, Atlanta, GA, USA 6Boston University School of Public Health Department of Environmental Health, Boston, MA, USA 7West Virginia University Eberly College of Arts and Sciences Department of Political Science, Morgantown, WV, USA Author For Correspondence: Stephanie J. Frisbee, MSc West Virginia University School of Medicine Robert C. Byrd Health Sciences Center 1 Medical Center Drive - PO Box 9105 Morgantown, WV 26506-9105 304-293-6552 sfrisbee@hsc.wvu.edu 1 Page 3 of 38 Running Title: C8 Health Project Methods & Results p. 10 A rticle Descriptor: Risk characterization, Population health, Environmental medicine Key W ords: C8, Environmental contamination, Perfluorocarbons, PFOA, Toxic tort settlement Acknowledgements: The authors gratefully acknowledge the contributions of: Troy Young and Richard Whitener from CPR Solutions Group, Charleston, WV, for providing information technology solutions to the Project; Cathy Lally and Jessica MacNeil from the Emory University Rollins School of Public Health for their expertise and assistance in data cleaning; personnel at Exygen Research Corporation and Axys Analytics for ensuring accurate descriptions of laboratory methods; and Dr. David Savitz for his assistance during the preparation of this manuscript. We also appreciate the suggestions of reviewers. Finally, the scale C8 Health Project necessitated that many individuals provided valuable assistance during its development and implementation. The authors gratefully acknowledge these contributions and thank all those individuals who supported the execution of the Project. Funding Sources): The entirety of the funding for the C8 Health Project was achieved pursuant to the Settlement Agreement in the case of Leach v. E.l. DuPont de Nemours & Co., Civil Action No. 01-C-608 in 2004. Funding was administered by a named, Court-approved Health Project Administrator. Competing Interests Declaration: For SJF, AS, SSK, CP, JAH, CJ, KML, AMD: These authors were engaged in the Project pursuant to a contractual relationship between Brookmar, Inc. and West Virginia University. These authors have no current or prior competing financial or non-financial interests to disclose. These authors declare that their ability to design, conduct, interpret, or publish this research was unimpeded and fully independent of the Court and/or settling parties. 2 p. 11 Page 4 of 38 For APBJr, AM, PF, SA: As described in the paper, Brookmar, Inc. was a for-profit company created solely to carry out the C8 Health Project component of the Court-directed settlement, and remained an active entity throughout the course of and until the closure of this study. APBJr and AM were the sole owners of Brookmar, Inc. PF and SA were employees of Brookmar, Inc. Brookmar, Inc. received funding exclusively from the Settlement, administered through the Health Project Administrator, to conduct the Project. As described in the paper, the design of the Project was developed in consultation with, though not subject to, the wishes of the settling parties. However, these authors declare that the study was performed, and their ability to interpret, and publish this research was unimpeded and fully independent of the Court and/or settling parties. For TF, KS, VMV: These authors are members or contractors of the Court-approved C8 Science Panel. As such, they are in receipt of funding from the C8 Class Action Settlement Agreement between DuPont and Plaintiffs, resulting from releases of chemical perfluorooctanoic acid (PFOA or C8) into drinking water, and approved by the Circuit Court of Wood County, West Virginia. These authors declare that their ability to design, conduct, interpret, or publish research was unimpeded and fully independent of the Court and/or settling parties. In addition, they declare no non-financial competing interests. A bbreviations: Abbreviation APFO C5 / PFPeA C6 / PFHxA C6S / C6 Sulfonate / PFHS C7 / PFHpA C8 / PFOA C8S / C8 Sulfonate / PFOS C 9 / PFNA C10 / PFDA C11 / PFUnA C12 / PFDoA PFC PFO LOD Full Definition Ammonium perfluorooctanoate Perfluoropentanoic acid Perfluorohexanoic acid Ammonium perfluorohexane sulfonate Perfluoroheptanoic acid Perfluorooctanoic acid Perfluorooctanesulfonic acid Perfluorononanoic acid Perfluorodecanoic acid Perfluoroundecanoic acid Perfluorododecanoic acid Perfuorocarbon Perflurooctonoate Limit of Detection 3 p. 12 Page 5 of 38 Section Titles: Abstract Introduction Perfluorocarbons PFCs and Health Origin of the C8 Health Project C8 Health Project Methods Eligibility Data Components Enrollment Data Collection Procedures Blood Sample Processing and Laboratory Methods PFC Quality Assurance Validation of Select Medical Diagnoses Consenting Procedures Implementation Data Analysis and Reporting Data Cleaning Estimation of Participation Rates Results Discussion Conclusion References Tables Table 1. Estimated Percent Participation by Water District Table 2. Availability of Detectable Serum Concentrations for PFCs Table 3. Population Serum Concentrations for 7 PFCs Table 4. Age and Gender Adjusted Serum PFC Concentrations by Qualifying Water Districts Table 5. Summary of Intra- and Inter-Lab Quality Assurance Figures Figure 1. PFC Concentrations Stratified by Age and Gender Figure 2. Comparison of Geometric Means for PFC Serum Concentrations for C8 Health Project Results vs. Two Nationally Representative Samples 4 p. 13 Page 6 of 38 ABSTRACT Background: The C8 Health Project was created, authorized, and funded as part of the Settlement Agreement reached in the case of Jack Leach, et al. v E. I. duPont de Nemours and Company (No. 01C-608 W. Va., Wood County Circuit Court filed April 10, 2002). The settlement stemmed from the perfluorooctanoic acid (PFOA or C8) contamination of drinking water in six water districts in two states near the DuPont Washington Works facility near Parkersburg, West Virginia. Objectives: This study reports on the methods and results from the C8 Health Project, a population study created to gather data which would allow class members to know their own PFOA levels and permit subsequent epidemiologic investigations. Methods: Final study participation was 69,030, enrolled over a 13-month period in 2005-2006. Extensive data were collected including demographic data, medical diagnoses (both self-report and medical records review), clinical laboratory testing, and determination of serum concentrations of 10 perfluorocarbons. Here we describe the processes used to collect, validate, and store these health data. We also describe survey participants and their serum perfluorocarbon levels. Results: The population geometric mean for serum PFOA was 32.91 ng/mL, 500% higher than previously reported for a representative American population. Serum concentrations for PFHS and PFNA were elevated 39% and 73% respectively, while concentrations of PFOS was present at levels similar to the US population. Conclusions: This largest known population study of community perfluorocarbon exposure permits new evaluations of associations between PFOA, in particular, and a range of health parameters. These will contribute to understanding of the biology of perfluorocarbon exposure. The C8 Health Project also represents an unprecedented effort to gather basic data on an exposed population; its achievements and limitations can inform future legal settlements for populations exposed to environmental contaminants. 5 Page 7 of 38 p. 14 INT "T...R.. OD" "U""CTION Perfluorocarbons Perfluorooctanoatic acid (PFOA or C8), is one member of the class of man-made perfluorocarbon (PFC) compounds. PFOA exists as an alkyl acid (PFOA), an ammonium salt (ammonium perfluorooctanoate, APFO), or as a dissociated conjugate base (perflurooctanoate, PFO). A closely related PFC is perfluorooctanesulfonate (PFOS, C8 sulfonate, or C8S). Additional, related PFCs include: C5 (perfluoropentanoic acid, PFPeA), C6 (perfluorohexanoic acid, PFHxA), C6 sulfonate (ammonium perfluorohexane sulfonate, PFHS), C7 (perfluoroheptanoic acid, PFHpA), C9 (perfluorononanoic acid, PFNA), C10 (perfluorodecanoic acid, PFDA), C11 (perfluoroundecanoic acid, PFUnA), and C12 (perfluorododecanoic acid, PFDoA). PFCs are used as plasticizers, wetting agents, and as emulsifiers during the manufacture of fluoropolymers including products that impart nonstick heat resistance to cookware, or breathable yet waterproof properties to fabrics. PFCs may also result from the metabolism or environmental breakdown of fluorinated telomers, including chemicals used to coat commercial food packaging, and for stain-resistant treatment for fabrics and clothing. PFOA may also be a residual impurity in personal care products. PFCs and Health PFOA and other PFCs persist in the environment, and are found in ground and surface water globally (Yamashita et al., 2008). They are present in blood and other tissues of animal species worldwide, including remote regions (Tao et al., 2006). Recent publications have extensively reviewed and summarized the known toxicological properties, environmental distribution, and potential health concerns related to PFOA (Kennedy et al., 2004; Kudo et al., 2003; Lau et al., 2007). Animal toxicology studies have suggested potential suppression of humoral immunity, neuroendocrine effects, and exposure-related gestational and developmental effects. Cumulative evidence from mammalian animal studies has suggested 6 p. 15 Page 8 of 38 that the liver is an important target organ. Reported hepatotoxic effects include liver enlargement, hepatocellular adenomas, and peroxisome proliferation (specifically PPAR-a), possibly suggesting a possible non-genotoxic carcinogenic mechanism for PFCs. Additionally, combined evidence supports that PFCs generally, and PFOA and PFOS specifically, are present in the sera of diverse human populations (Lau et al., 2007). In the US, analysis of NHANES samples reported detection of these chemicals in almost all samples, with a US-population median of 5 ppb PFOA. Both PFOA and PFOS concentrations were higher in the serum of men and those with higher education (Calafat et al., 2007a, Calafat et al., 2007b). While potential sources of human exposure continue to be investigated, current, known sources of PFOA exposure generally include drinking water, household dust, and food or migration from food packaging (in particular commercial and fast-food/take out packages) and cookware (Lau et al., 2007). Occupational studies have shown elevated worker exposures in manufacturing processes that use PFOA or PFOS (Emmet et al., 2006; Olsen et al., 2003). Human population studies, predominately medical surveillance studies of male American workers exposed occupationally to PFOA or PFOS, have reported inconsistent findings (Lau et al., 2007). While some studies have reported associations between exposure and cancer (bladder and prostate in particular), lipids, liver enzymes, and some thyroid hormones, other or follow-up studies have either contradicted earlier findings, or found evidence suggesting explanation through confounding parameters (Lau et al., 2007). Maternal serum or neonatal cord blood studies have implicated an association of PFOA or PFOS with birth weight (Apelberg et al., 2007; Washino et al., 2009), but there are also contradictory findings in high-exposure populations (Nolan et al., 2008). The half-life of PFOS and PFOA in human sera has been reported as approximately 5 and 3.5 years respectively (Olsen et al., 2007). 7  In a review process that remains ongoing, the United States Environmental Protection Agency (EPA) is considering evidence and classification of PFOA as a likely human carcinogen (EPA-SAB-06-006). The PFOA Stewardship Program proscribes PFOA, PFOA precursors, and related, higher homologue chemicals from emissions and products by 2015. In the European Union, the use of PFOS and derivatives was stopped in 2000 and banned in 2008, though PFOA use remains largely unregulated (Jensen et al., 2008). Origin o f the C8 Health Project The C8 Health Project can be traced to legal actions taken by a local family. A portion of this family's farmland was sold to DuPont in 1984, who subsequently converted the land parcel into a site to dispose of waste products from PFC manufacturing from their Washington Works plant. The family alleged that [the then unknown] chemicals from the landfill were responsible for family illness, wildlife death, and the death of almost 300 head of their cattle (see Supplemental File, Note 1). The family agreed to a confidential settlement with DuPont in 2001; associated legal activities, including independently commissioned studies and reports filed by government agencies, served to provide environmental data and to heighten local awareness of the exposure, coincident with an emerging scientific literature. The following points summarize key events in the almost two-decade time-line leading to the C8 Health Project: Cumulative evidence detected PFOA contamination of water supplies along the midOhio River valley. Water pollution was attributed to direct industrial releases from DuPont's Washington Works plant into the Ohio River, a principal source of public drinking water, and airborne pollution more broadly contaminating water tables and aquifer systems, with subsequent well contamination, an important drinking water source in a rural community (See Supplemental File, Note 2). p. 17 Page 10 of 38 August 2001-April 2002: Thirteen plaintiffs filed a lawsuit against DuPont, which was subsequently certified as a Class Action, Leach v. E.l. DuPont de Nemours & Co., Civil Action No. 01-C-608, filed in Wood County, West Virginia Circuit Court. The "Class" was defined as individuals, in West Virginia or Ohio, whose drinking water had been contaminated by quantifiable levels of PFOA. November 2004: A multi-component $107 million pre-trial settlement between the Class and DuPont was reached. Complete settlement terms are part of the public record. Key provisions included: o A $70 million award for Class members, of which $20 million was required to be used for health and education projects; o Provision of water treatment technologies to remove PFOA from the water supply of the six affected water districts; o Formation of an independent panel of three scientific experts to carry out a community study and determine if there is a "probable link" (see Supplemental File, Note 3) between PFOA exposure and human disease. The settlement broadly outlined terms of agreement but did not detail how they were to be satisfied. Post hoc negotiations between settling parties resolved that the health and education projects and Class payments would be achieved through a population-wide health study of the Class, initially known as the "Settlement Class Health & Education Project" and later the "C8 Health Project" (the Project). An independent company, Brookmar, Inc. (Brookmar), was created to design, publicize, and implement the Project under court supervision. Three epidemiologists (the C8 Science Panel) were appointed to determine the presence or absence of what the court termed a "probable link" between PFOA exposure and human disease (see Supplemental File, Note 3). In addition to Project data, the C8 Science 9 Page 11 of 38 p. 18 Panel is to include data from de novo, prospective community studies that they proposed and are conducting. The Project faced significant implementation challenges, including court and population expectations for rapid timelines, and absence of precedent for the likely scale of the community project. Project participation was the established route for Class members to benefit from the settlement, but neither Class size nor participation was known a priori. Accordingly, Brookmar developed procedures to accommodate: rurality; shift workers; eligible Class members no longer living in the area; wide range in participant age and mobility; a deliberately short survey period; expressed community apprehension regarding data privacy and concern about adverse effects on insurability and even employability; and the desire for participants to receive personalized information about laboratory results and general information about Project findings. The data collection methodology implemented by Brookmar, agreed to implicitly or explicitly by counsel for the settling parties, is described below. 10 p. 19 Page 12 of 38 C8 HEALTH PROJECT METHODS Eligibility Class eligibility was defined by exposure to contaminated water, a combination of geographic and concentration criteria, and exposure duration. Key criteria included: Exposure to contaminated water from any of six public water districts (2 in West Virginia, 4 in Ohio; see Supplemental File, Figure 1) or from private water sources within the geographical boundaries of the public water sources which contained >0.05 ppb PFOA. The ability to document a minimum 12 months of exposure to contaminated water between 1950 and December 3, 2004, at either primary residence, place of employment, or school. Participants supplied documentation demonstrating both their identity and exposure using a combination of Court-defined acceptable documents. Brookmar independently verified the authenticity of documents with the issuing agency, and identity documentation was examined to ensure that participants were enrolled only once. Scanned document copies became part of the participant's Project electronic data record. Data Components Four types of data were collected: a) health survey; b) self-reported anthropometric measurements; c) blood sample; and d) medical chart review to validate selected self-reported diagnoses. In identifying clinical laboratory tests and selecting diagnoses for validation, priority was given to those with potential associations to PFC exposure as reported in the scientific literature. Clinical laboratory tests included: serum lipid, immune and inflammatory markers; liver, kidney, and thyroid function; complete blood count; serum electrolytes and protein; and endocrine function, including insulin and glucose (see Supplemental File, Note 4). Validated medical diagnoses included: heart disease; cancers; thyroid disease; neurologic disorders; 11 p. 20 Page 13 of 38 inflammatory and autoimmune disorders; and pregnancy complications (see Supplemental File, Note 5). The health survey gathered: demographic data; current and historic residential and employment information, including water source and use; personal medical diagnoses, treatments including medications, and physical symptoms; family medical history; pregnancy history and pregnancy-related outcomes for women; and information about lifestyle and health behaviors. Participants also self-reported their own height, weight, and blood pressure. Brookmar contracted with a separate company to independently pilot test the survey, and revisions were made based on pilot-test findings. The final version of the survey was accepted by the settling parties. The survey, a list of the clinical laboratory tests, and the eighteen medical diagnoses verified by medical record review are publically available (WVU C8 Health Project Data Hosting Website). Enrollment An independent information technology (IT) company was contracted to build and manage informatics solutions that addressed Class security concerns and created a webbased mechanism for Project registration and health survey completion. Participants could alternatively register in person and use paper-based surveys. After registration and completion of the health survey, participants received instructions regarding requirements for demonstrating eligibility and making an appointment at a Project data-collection site. Standard data quality-assurance techniques for survey data, including a quota for data duplicate entry for paper-based surveys and electronic-based logic rules (e.g., limited-answer menus) for webbased surveys, were in place for the health survey. Data Collection Procedures Temporary modular office units were established in each water district, staffed with nurses, phlebotomists, and intake personnel, and equipped for venipuncture, blood 12 p. 21 Page 14 of 38 processing, and short-term record and blood sample storage. Participants could schedule appointments between 7:30 a.m. and 7:30 p.m. at the location of their convenience Due to both feasibility and participant considerations, fasting was not required for phlebotomy, though self-reported fast duration was collected to facilitate interpretation of laboratory results. At in-person appointments, participants submitted eligibility documentation and the water district indicated by the exposure documentation provided was recorded; this was usually but not always the source of greatest exposure. Project staff verified demographic data, current residential information, completion of the health survey, and asked participants to report their current height, weight, and blood pressure. Participants voluntarily submitted a blood sample. Each verified participant received $150 for completing the health survey and an additional $250 for providing a blood sample (regardless of sample quantity or quality). The payment amount reflected the compensation intentions of the settlement and remuneration for Project participation expenses. Blood Sample Processing and Laboratory Methods Blood samples were obtained and processed at individual data collection sites. Samples were drawn into 4 tubes per participant, with a maximum 35 cc for adults and 26 cc for children. Tubes were spun, aliquotted, and refrigerated until shipping. For limited-volume samples, serum was aliquotted with priority for PFC analysis. Samples were shipped on dry ice daily from each data collection site to the laboratory retained to measure serum PFCs. The clinical laboratory contracted to perform the clinical chemistry analysis picked up samples daily from each data-collection site. Additionally, an aliquot of serum from each participant was frozen and subsequently stored in a Project tissue bank. Clinical laboratory tests were performed at a large, independent, accredited clinical diagnostic laboratory (LabCorp, Inc, Burlington, NC, USA). A customized HL7-interface generated immediate, on-site laboratory-specific identification numbers and tube labels, and 13 permitted subsequent electronic transfer of clinical laboratory results directly into the Project data system. Clinical laboratory tests and quality assurance were performed in accordance with the accreditation standards required of this laboratory. The primary laboratory performing PFC analysis (Exygen Research Inc., State College, PA, USA) was selected based on its ability to meet FDA guidelines for bioanalytical method validation, a lower limit of quantification of 0.5 ng/mL, and 96-well-plate-based technology allowing for high throughput capability. This was the laboratory of record for a previously reported, independently performed study of residents in one water district included in the Project (Emmett et a l,, 2006). The PFOA quantification and validation methodology used by this laboratory has been previously detailed (Flaherty et al,, 2005). The analytic protocol used for the Project was a modification of this methodology. Briefly, the technique used a protein precipitation extraction together with reverse-phase high-performance liquid chromatography/tandem mass spectrometry. Spectrometric detection was performed using a triple quadrupole mass spectrometer in selected reaction monitoring mode, monitoring for the individual m/z transitions for each of the 10 PFCs and the 13C-PFOA surrogate. Results for the 10 PFCs measured were incorporated into the Project information system through a Windowsbased program (See Supplemental File, Note 6). PFC Quality Assurance A two-tiered quality assurance program was implemented consisting of a) evaluation of test reliability in the primary lab (intra-lab) with the use of blank samples, samples spiked with a known PFC concentration, and participant duplicate samples, and b) use of a second, external laboratory (AXYS Analytical Services Ltd., Sidney, BC, Canada) to determine PFC concentrations for participant duplicate samples (inter-lab). This laboratory, with the ability to monitor 10 individual PFCs and a lower limit of quantification of 0.2 ng/mL, employed analytic methods previously described (Kuklenyik et a l,, 2004; Taniyasu et al,, 2005). Briefly, the 14 p. 23 Page 16 of 38 technique used a solid phase extraction on a weak anion exchange column followed by reverse-phase high-performance liquid chromatography/mass spectrometry. Spectrometric detection was performed using a triple quadrupole mass spectrometer in selected reaction monitoring mode, monitoring individual m/z transitions for each of the target PFCs, the 13CPFOA, 13C-PFOS, and 13C-PFDA surrogates and the 13C-PFOA and 13C-FOUEA instrument internal standards. To assess method performance at the primary lab, quality control samples in the form of two control serum blanks, two lab control spikes in control serum, and two sample duplicates, were performed with each batch of 90 samples analyzed. 13C-PFOA (surrogate) was also added to every sample prior to extraction to assess lab preparation. Bulk control blanks and spikes were prepared at the primary lab and sent to the sampling sites. They were then blindly returned with every shipment of samples for analysis to assess storage, transport, and laboratory preparation effects. For these quality control samples, the Project IT system generated in-line dummy ID numbers and two sets of lab-ready, bar-coded phlebotomy tube labels). Site nurses aliquotted two sets of sample tubes, and both were included as part of the standard shipment to the primary laboratory. Based on a per-data collection site sampling plan, samples were also automatically identified by the Project IT system for the secondary lab. Labels and tubes were generated similarly, as were sample aliquots. Results from quality assurance samples were segregated from the main, participant database post hoc by the IT company, the only group unblinded to ID numbering. During analysis of quality assurance results, a consistent difference between the primary and secondary laboratory was detected (approximately 30%) for samples obtained during the first four months of the Project. Investigation and additional, targeted intra- and inter-lab re-testing confirmed these directional (higher) differences. Per a court filing, Exygen discussed the cause as a problem of initially prepared samples used for internal calibration 15 (see Supplemental File, Note 7). Affected samples (approximately 25,000) were retested using serum stored in the Project tissue bank; quality assurance testing, including sample duplicates and replaced spiked and calibration samples, was also repeated. Retested results demonstrated a consistent decrease from initial results and increased consistency with the secondary lab. All analytic results presented here include only retested values for those affected serum samples. For quantitative assessment of quality assurance test results, final test values were matched to participant quality assurance values for the primary or secondary lab. Results reported as less than the limit of detection (LOD) were treated conservatively and excluded from quality assurance analyses. Agreement between two measures was assessed with the absolute difference, percent difference (absolute difference between values divided by value means), and coefficient of variation (standard deviation divided by mean), which were then summarized (mean and median) across the matched-samples results. Validation of Select Medical Diagnoses Participants self-reporting one of the eighteen targeted diagnoses were asked to provide the time and location of diagnosis. After obtaining appropriate record release consent (described below), Brookmar requested a copy of supporting documentation from a medical record or pathology report from health care providers. Cooperating providers were compensated $10 per necessary page. For approximately 36,000 validated diagnoses, the following was recorded: self-reported diagnosis; support (confirmation), non-support (negation), missing (records not obtained), or substitution (i.e., documentation supported a different diagnosis); the alternate diagnosis where appropriate; and type of documentation used for verification. Review of medical records and determination of diagnostic verification was performed by nurses employed by Brookmar. Consenting Procedures 16 p. 25 Page 18 of 38 Brookmar required that participants read (and "check" affirmatively) an introductory section of the health survey that explained the purpose and procedures of the Project, and risks and benefits of participation. This language is publically available as part of the survey tool. All participants submitting a voluntary blood sample completed the standard consent and release forms of the clinical laboratory contracted for phlebotomy. Brookmar obtained a separate consent for the release of medical records necessary for diagnosis validation, which was subsequently mailed (along with a cover letter and specific documentation request) to the health care provider identified by the participant. The Project group at West Virginia University and the C8 Science Panel obtained IRB approval, from their own institutions, permitting access to de-identified Project data. With assistance from Brookmar, the C8 Science Panel obtained an additional IRB approval allowing access to identified data, which facilitates contacting participants for enrollment in follow-up studies. Implementation Following input by the settling parties, Brookmar used multiple avenues to publicize the Project. Communications about Project eligibility requirements, enrollment, data collection procedures, timeline, and remuneration included a series of open meetings conducted in five of the six water districts, Project website messages, a phone bank, and press conferences with local media, an important source of information throughout the duration of the Project. Brookmar also maintained communication with local health care providers. Meetings were conducted to inform the medical community about Project procedures, including medical record requests, as well as the information that participants would be provided pursuant to their Project participation. Efforts to ensure full access for interested participants included multiple sites, 12-hour daily appointment availability, and disability accommodation including handicap access and 17 assistance completing the health survey. Brookmar also coordinated remote data collection for those otherwise eligible Class members unable to travel to a data collection site (e.g., those no longer living in the vicinity). For these participants, eligibility documentation was submitted via mail, followed by remote completion of the health survey and a personal telephone interview. These remote participants then completed phlebotomy at an identified, local, accredited laboratory. Of the total participants, approximately 600 participated via these procedures (personal communication, Brookmar). Brookmar was unable to accommodate participants cognitively unable to complete the survey (or without a representative to accurately complete it on their behalf) or those physically unable to travel to a phlebotomy site. Thus these groups are likely underrepresented among Project participants. Data Analysis and Reporting Participants were mailed individualized results for clinical lab tests, including laboratory normal ranges and flags for abnormal findings. For severely abnormal values, emergency flags triggered a personal communication from Brookmar personnel with advice to seek prompt medical attention. Participants also received a report of their PFC values. Upon completion of the Project, Brookmar filed an electronic dataset with the Wood County Court in May 2008. The dataset included the health survey, clinical laboratory and PFC values, an image of eligibility documents, and record of payment. To protect participant privacy, the presiding judge subsequently sealed the dataset. A mechanism is currently being sought wherein an agency, likely of the federal government, would maintain and make accessible a de-identified dataset for public research use. The C8 Science Panel is conducting analyses using the Project cross-sectional data collected and is also conducting its own independent, environmental and population-based studies, also financed by the settlement. For consenting participants, the C8 Science Panel is p. 27 ' Page 20 of 38 able to link Project-collected data with follow-up and longitudinal studies. A description of ongoing studies is available on the C8 Science Panel's website (C8 Science Panel Website). A tissue bank of participant frozen serum was established at West Virginia University in which samples are stored, handled, and accessed in a manner consistent with the IRB protocol governing the Tissue Bank. The sera can be linked to de-identified Project data, and may be used for further studies related to human PFC physiology. Brookmar contracted with the West Virginia University School of Medicine to report to the general public descriptive summaries of results from the Project. Summary data are reviewable at a website established for that purpose (WVU C8 Health Project Data Hosting Website). The C8 Science Panel and the WVU Project group are preparing and submitting analyses of associations between PFCs and health outcomes, intended for peer-reviewed journals. These will form part of the evidence that will assist the C8 Science Panel in meeting their Court-appointed obligation to determine "probable links" (see Supplemental File, Note 3) between PFOA exposure and health outcomes. Data Cleaning In the first phase of data cleaning, the IT company ensured that question responses were consistent with question "skip patterns" and menu options, as well as ensuring consistent coding and formatting for question responses. For the de-identified dataset, text fields were scrubbed to eliminate potentially identifying information. In the second phase of data cleaning, completed collaboratively by the C8 Science Panel and WVU Project team, continuous variables were examined and decision rules were created for outliers and missing values. Lab-generated error messages for samples that could not be analyzed were deleted and results set to null". For clinical lab results either lower or higher than the LOD, values were replaced with 50% below or above the lower or upper LOD, respectively. 19 Page 21 of 38 p. 28 ` Though serum samples were analyzed for 10 PFCs, not all PFCs were detectable in all samples tested. Four PFCs (PFHS, PFOA, PFOS, PFNA) were detectable in almost all (>97%) samples; for these PFCs, test results reported as less than the LOD were substituted with 0.25 ng/mL (50% of the lower LOD of 0.5 ng/mL). Three PFCs (PFHxA, PFHpA, PFDA) were detectable in approximately 50% of the samples; results for these PFCs are reported with and/or without substitution for values reported as less than the LOD. Three PFCs (PFPeA, PFUnA, and PFDoA) were detectable in only a negligible portion of the tested samples, and are not reported or included in further analyses. Thus, results reported here include 7 of the 10 tested PFCs (PFHS, PFOA, PFOS, PFNA, PFHxA, PFHpA, PFDA). Estimation of Participation Rates Total project participation was estimated by water district as the number of participating residents divided by the total contemporaneous population in that water district. Water district population was estimated using 2005-2006 Census population estimates for block groups, the smallest Census geographic unit that could be accurately identified. Block groups intersecting with water districts were determined, and the population of each block group was apportioned to the water district based on the ratio of water district area to block group area within each block group. The number of participants resident in each water district was based on the assigned water district, that for which the participant presented qualifying eligibility documents, and self-reported residence at the time of enrollment. Participation estimates for each water district was estimated for age and gender strata. 20 p. 29 Page 22 of 38 RESULTS Project enrollment totaled 69,030. Approximately 80% completed registration and the health survey online (personal communication, Brookmar). PFC and clinical laboratory analyses were available for more than 65,000 participants. While children aged <10 years had highest proportion without available blood analyses (almost 1/ 3), laboratory data were nevertheless available for more than 3,400 of these children. Consistent with regional demography, more than 97% of participants identified themselves as white and educational attainment and income levels were lower than national averages. Participants ranged in age from 1.5 years to older than 100, with an average age of 39.119.9 (standard deviation). (See Supplemental File, Table 1.) Twenty-six percent of adults (>18 years at enrollment) reported current smoking, and an additional 26% reported former smoking. A substantial proportion of children (63.3%) and adults (69.1%) lacked a regular exercise program. Further, 39% of children were classified as being at-risk or already overweight based on BMI percentile, and 69% of adults were classified as overweight or obese based on BMI. Flowever, as BMI calculations were completed using self-reported height and weight, they may underestimate actual population proportions. These demographic and health risk data are generally consistent with estimates for Appalachia from nationally representative data sources (Halverson et al., 2004). (See Supplemental File, Table 2.) At the time of enrollment, most participants reported current residence in Ohio (52%) or West Virginia (45%); 63% of participants were resident in a qualifying water district at the time of their participation. Average monthly enrollment in the Project was 5,310, with enrollment peaking in January 2006 (8,003 participants). The largest proportion of participants qualified through Lubeck Public Service District (24.6%), followed by Tuppers Plains (20.4%). (See Supplemental File, Table 3.) 21 p. 30 Page 23 of 38 As shown in Table 1, an estimated 80.3% of the population resident in the water districts during the enrollment period participated in the Project, with a slightly higher proportion of women compared to men participating. Participation by water district ranged from 70.3% of the resident population in Tuppers Plains to almost 95% in the Village of Pomeroy. The age groups with the lowest estimated participation were the elderly (>80 years of age) and young children (<4 years of age). Serum analysis results for 10 PFCs (PFPeA, PFHxA, PFHS, PFHpA, PFOA, PFOS, PFNA, PFDA, PFUnA, PFDoA) were available for 66,899 participants. Table 2 summarizes the proportion of tested samples with a detectable PFC concentration and the number of samples for which 50% of the lower LOD was substituted. Table 3 reports population summary statistics for the seven PFCs, stratified by gender and age groups. Due to population homogeneity (above), stratification by ethnicity was not performed. Patterns by age and gender in the 4 widely detectable PFCs are highlighted in Figure 1. For each, median concentrations were higher in males in most age groups. For PFOA and PFOS, population median concentrations demonstrated a J-shaped pattern, with higher values in younger age groups, lowest values in young- to middle-adult age groups, and highest population concentrations in older adult age groups. For PFHS and PFNA, the highest population median concentrations were observed in children. Project results for four PFCs (PFHS, PFOA, PFOS, PFNA) are compared to results from the nationally representative NHANES sample in Figure 2. An important difference between NHANES and Project results is the inclusion of children <12 in the Project, although this Project age group is likely to have a minimal impact on overall population results in a sample size exceeding 65,000. For all PFCs except PFOS, serum concentrations reported for the Project exceeded NHANES results. The largest differences were observed for PFOA, where the Project population had more than a 500% (1999-2000) or 700% (2003-2004) larger 22 p. 31 Page 24 of 38 geometric mean. Smaller but still substantial differences were also observed for PFHS (57.1% [1999-2000] and 73.6% [2003-2004] larger) and PFNA (178% [1999-2000] and 39% [2003 2004] larger). In contrast, the Project population had a 36.8% (1999-2000) and 7.1% (2003 2004) lower geometric mean for PFOS. Unadjusted, nonparametric Spearman's rho rank-order correlation analysis was performed for 21 pairings (7 PFCs) for the overall population. In general, correlations between the PFCs were low. Modest correlations (approximately 30%) were observed between the pairings of PFHS-PFOA, PFHS-PFNA, PFOA-PFOS, and PFOS-PFDA. Larger correlations were observed between PFHpA-PFOA (approximately 40%), PFHS-PFOS and PFOS-PFNA (approximately 50%), and PFNA-PFDA (approximately 60%). There were no discernable differences in correlations patterns between adults and children or between genders (not shown). (See Supplemental File, Figure 2.) Table 4 reports serum PFC concentrations, weighted by age and gender, stratified by qualifying water district. Participants in Little Hocking Water Association had the highest levels of PFOA, more than 70% higher than the next group, participants with private wells. For all PFCs other than PFOA, the 157 participants qualifying through contaminated private wells had the highest serum concentrations. Participants in Lubeck Public Service District had the highest reported values for PFHxA, PFOS, PFNA, and PFDA. The highest values of PFHS were found in participants in the City of Belpre, OH. Results for the quality assurance analysis are summarized in Table 5. The highest agreements, both intra-lab (within the primary lab) and inter-lab (between the primary and secondary lab), were observed for PFHS, PFOA, PFOS, and PFNA. The median intra-lab difference for PFOA and PFOS was 5.5% and 4.06% respectively, whereas the median inter lab difference for PFOA and PFOS was 16.7% and 14.01% respectively. The least 23 p. 32 Page 25 of 38 agreement, either intra- or inter-lab agreement was observed for PFHxA. For PFFIpA and PFDA, intra-lab but not inter-lab agreement was observed. 24 DISCUSSION p. 33 Page 26 of 38 This unique and large survey resulted from the pretrial Settlement Agreement of a class action lawsuit and a Court-supervised health study of a population (n=69,030) exposed to sustained environmental contamination with PFOA. The demographic characteristics and health behaviors of the participants reflect that of the affected, mostly rural, Appalachian communities: predominately white, with lower-than-national-average levels of education and income, and higher rates of obesity and other health risk behaviors such as smoking and inactivity. Challenges posed by the definition of the Class, specifically the prolonged (50 year) exposure period and inclusion of residential, employment, and school-based exposure, preclude an exact determination of the total eligible population. However, a reasonable approximation suggests that 80% of the current population in affected water districts participated in the Project, though 37% of Project participants resided outside an affected water district at the time of their Project enrollment. It is probable that a combination of public concern about chemical contamination and monetary compensation contributed to participation. The high rates of population participation and the high rate (estimated at 80%) of online (versus paper survey) enrollment and completion of the health survey in a rural, poor area may provide useful lessons for future population surveys. As anticipated, study serum concentrations of PFOA, the identified environmental contaminant, deviated markedly from those of a representative, national sample in all affected water districts. The unadjusted population geometric mean of 28.2 (median 32.91) ng/mL was 6- to 8-fold higher than nationally representative values from the NHANES study. However, observations regarding higher-than-national-sample serum concentrations of PFHS and PFNA, but lower-than-national-sample concentrations for PFOS, were not anticipated. The distribution and pattern of PFHS and PFNA concentrations is not similar to that of PFOA, suggesting a possible exposure source other than the facility identified as the source of PFOA 25 p. 34 Page 27 of 38 . exposure. Comparisons between these two studies are interpreted within the context of possible differences in laboratory analytic techniques (though both studies used solid-phase extraction followed by high performance liquid chromatography-tandem mass spectrometry) and measurement accuracy across a broad spectrum of concentrations. Discernible gender differences for PFOA serum levels in most age groups are consistent with national findings in less-exposed populations. The findings of higher serum concentrations of PFCs in children, particularly for PFHS and PFNA, warrant further study. While these findings are unadjusted for potential confounders, higher concentrations in the youngest age groups is counter to traditional expectations of biologic burden paralleling cumulative environmental exposure, and merit further study. The observation that the highest population burden of PFOA was found in the Little Hocking Water Association district is consistent with water quality measurement reports from the affected water districts (many of which are publically available; also see Supplemental File, Note 2). However, the population PFOA results for Little Hocking are substantially lower than those previously reported in a smaller sample of Little Hocking residents (age and gender adjusted mean of 228 reported here vs. 448 ng/mL; Emmett et al., 2006). While the reasons for these differences are not clear, representativeness of the samples, and study time periods, are possible explanations. The same laboratory performed PFOA analysis in each study. While the highest serum concentrations of PFOA were observed in Little Hocking, it is interesting that higher burdens of other PFCs were found in other water districts. Investigating the association between water PFC concentrations and serum PFC concentrations, and investigating the distributions of occupational contributions, are beyond the scope of the present report. Further work is underway to model occupational, temporal, spatial, and temporal-spatial variation in water PFC levels, including differences between public water supplies and private wells, and the association with serum PFC levels. 26 p. 35 Page 28 of 38 Correlations between the different PFCs were generally modest and without discemable age or gender patterns. Presently, the meaning of these correlations are unclear and will likely need to be interpreted later, within the context of a better understanding of patterns of cumulative exposure, environmental accumulation, and physiological metabolism of these chemicals across the lifespan. Previous studies have reported on the complexity of PFC determination (van Leeuwen et al., 2006). While intra-lab measurements demonstrated reasonable stability, inter-lab measurements showed larger divergence. It is not surprising that measurements from the Project, which at times processed more than 7,000 samples per month, would not achieve the same level of accuracy as federally funded projects with smaller sample sizes and smaller ranges of exposure. Spearman testing of quality-assurance results demonstrates that rank order is highly preserved for intra- and inter-laboratory comparisons. The large size of this cohort, together with the broad range of serum PFC values, provides unique opportunities for investigating associations between PFCs and human health. While the prevalence study design inherently limits causal inference, the Project remains the largest and broadest study to date of associations between PFC exposure and human health. Subcohorts from this population, to be followed over time, have been identified and the C8 Science Panel has already begun enrollment in longitudinal studies. A multivariable analysis of factors determining PFOA levels in the population has been conducted and submitted for publication (Steenland et al., in press 2009). Additional targeted analyses investigating associations between PFCs and specific clinical chemistries and disease endpoints are already underway and will be reported elsewhere. 27 CONCLUSION The data from the 69,030 C8 Health Project participants provide valuable information on serum PFC concentration, demographic factors, clinical chemistry and self-reported disease in a population with a high participation rate. Ongoing work investigating the inter-relationships between them will provide clues about possible etiologic relationships, within the limitations of the prevalence study design. In addition, they provide a valuable baseline characterization of this population for subsequent, prospective studies. The results, therefore, have the potential to improve the current understanding of the biology of PFC exposure and are unprecedented among toxic tort settlements, most of which simply provide compensation for the Class without attempting to generate useful health and exposure data or assess health effects. As an innovative effort to gather data on an exposed population, the C8 Health Project can also serve as a model for future legal settlements for populations exposed involuntarily to environmental contaminants. p. 37 Page 30 of 38 REFERENCES Apelberg BJ, Witter FR, Herbstman JB, Calafat AM, Halden RU, Needham LL, Goldman LR. Cord serum concentrations of perfluorooctane sulfonate (PFOS) and perfluorooctanoate (PFOA) in relation to weight and size at birth. Environ Health Perspect. 2007; 115(11): 1670-6. C8 Science Panel Website. 2007. Available: http://www c8sciencepanei.org/. [Accessed 3/1/2009], Calafat AM, Kuklenyik Z, Reidy JA, Caudill SP, Tully JS, Needham LL. 2007. Serum concentrations of 11 polyfluoroalkyl compounds in the US population: data from the National Health and Nutrition Examination Survey (NHANES) 1999-2000. Environ Sci Technol;41(7):2237-2242. Calafat AM, Wong LY, Kuklenyik Z, Reidy JA, Needham LL. 2007. Polyfluoroalkyl chemicals in the U.S. population: data from the National Health and Nutrition Examination Survey (NHANES) 2003-2004 and comparisons with NHANES 1999-2000. Environ Health Perspect;115(11): 1596-1602. Emmett EA, Shofer FS, Zhang H, Freeman D, Desai C, Shaw LM. 2006. Community exposure to perfluorooctanoate: relationships between serum concentrations and exposure sources. J Occup Environ Med;48(8):759-770. EPA-SAB-06-006. 2006. "SAB Review of EPA's Draft Risk Assessment of Potential Human Health Effects Associated with PFOA and Its Salts". Available: http:i7w w w .epa.gov/sab/panels/pfoa_rev_panel.htm . [Accessed 9/12/2008]. Flaherty JM, Connolly PD, Decker ER, Kennedy SM, Ellefson ME, Reagen WK, Szostek B. 2005. Quantitative determination of perfluorooctanoic acid in serum and plasma by liquid chromatography tandem mass spectrometry. J Chromatogr; 819:329-338. Halverson JA, Harner EJ, Ma L. 2004. "An Analysis of Health Disparities and Access to Medical Care in the Appalachian Region: A Report to the Appalachian Regional Commission". Available: http://ww w .arc.goV/index.do7nodeid-57#heaIthc. [Accessed: 11/2008], Jensen AA, Letters H. 2008. Emerging endocrine disrupters: perfluoroalkylated substances. Int J Androl;31(2):161-169. Kennedy Jr GL, Butenhoff JL, Olsen GW, O'Connor JC, Seacat AM, Perkins RG, Biegel LB, Murphy SR, Farrar DG. 2004. The toxicology of perfluorooctanoate. Crit Rev Toxicol;34(4):351 -384. Kudo N, Kawashima Y. 2003. Toxicity and toxicokinetics of perfluorooctanoic acid in humans and animals. Toxicol Sci;28(2):49-57. Kuklenyik Z, Reich JA, Tully JS, Needham LL, Calafat A. Automated solid phase extraction and measurement of perfluorinated organic acids and amides in human serum and milk. Environ Sci Technol. 2004;38:3698-3704. Lau C, Anitole K, Hodes C, Lai D, Pfahles-Hutchens A, Seed J. 2007. Perfluoroalkyl acids: a review of monitoring and toxicological findings. Toxicol Sci;99(2):366-394. Nolan LA, Nolan JM, Shofer FS, Rodway NV, Emmet EA. 2008. The relationship between birthweight, gestational age, and perfluorooctanoic acid (PFOA)-contaminated public drinking water. Reprod Toxicol; 27(3-4): 231-238. Olsen GW, Burris JM, Burlew MM, Mandel JH. 2003. Epidemiologic assessment of worker serum perfluorooctanesulfonate (PFOS) and perfluorooctanoate (PFOA) concentrations and medical surveillance examinations. J Occup Environ Med;45(3):260-270. Olsen GW, Burris JM, Ehresman DJ, Froehlich JW, Seacat AM, Butenhoff JL, Zobel LR. 2007. Half-life of serum elimination of perfluorooctane sulfonate, perfluorohexane sulfonate, 29 p. 38 Page 31 of 38 and perfluorooctanoate in retired fluorochemical production workers. Environ Health ` Perspect; 115(9): 1298-1305. Steenland K, Jin C, MacNeil J, Lally C, Ducatman AM, Vieira V, Fletcher T. Predictors of PFOA levels in a community surrounding a chemical plan. Environ Health Perspect. [Accepted; March 2009; Epub in EHP-in-press at: http://www.ehponline.org/docs/2009/0800294/abstract.html] Taniyasu S, Kannan K, So MK, Gulkowska A, Sinclair E, Okazawa T, Yamashita N. Analysis of flurotelomer alcohols, fluorotelomer acids, and short- and long-chain perfluorinated acids in water and biota. J Chromatogr A. 2005;1093:89-97. Tao L. Kannan K, Kajiwara N, Costa MM, Fillmann G, Takahashi S, Tanabe S. Perfluorooctane sulfonate and related chemicals in albatrosses, elephant seals, penguins, and polar skuas from the Southern Ocean. 2006. Environ Sci Technol; 40(24): 7642-7648. van Leeuwen SPJ, Karrman A, van Bavel B, de Boer J, Lindstrom G. 2006. Struggle for quality in determination of perfluorinated contaminants in environmental and human samples. Environ Sci Technol;40:7854-7860. Washino N, Saijo Y, Sasaki S, Kato S, Ban S, Konishi K, Ito R, Nakata A, Iwasaki Y, Saito K, Nakazawa H, Kishi R. Correlations between prenatal exposure to perfluorinated chemicals and reduced fetal growth. Environ Health Perspect. 2009 Apr;117(4):660-7. WVU (West Virginia University) C8 Health Project Data Hosting Website. 2007. Available: http://ww w .hsc.w vu.edu/som /cm ed/c8/. [Accessed 3/1/2009]. Yamashita N, Taniyasu S, Petrick G, Wei S, Gamo T, Lam PK et al. 2008. Perfluorinated acids as novel chemical tracers of global circulation of ocean waters. Chemosphere; 70 (7) 1247-55. 30 Table 1. Estimated Percent Participation by Water District Age Group 0-4 5-10 11-14 15-19 20-24 25-29 30-34 35-39 40-44 4 5 -4 9 50-54 55-59 60-64 65-69 70-74 75-79 80+ Total M ale Fem ale Total 20+ City of B e lp re (O H) 3 9 .6 % 7 9 .8 % 8 5 .6 % 1 0 1 .9 % 99.6% 8 8 .2 % 8 7 .6 % 8 7 .3 % 9 4 .8 % 9 4 .6 % 8 5 .8 % 8 9 .3 % 9 8 .3 % 8 9 .4 % 9 0 .5 % 7 9 .8 % 5 1 .8 % 8 5 .6 % 8 5 .0 % 8 6 .1 % 8 7 .8 % Tuppers Plains ____(O H ) 5 4 .2 % 7 1 .7 % 7 3 .7 % 8 2 .0 % 7 2 .5 % 7 4 .6 % 7 6 .1 % 7 6 .7 % 7 5 .7 % 7 1 .3 % 7 9 .9 % 6 9 .6 % 7 1 .3 % 6 7 .7 % 5 7 .7 % 5 4 .2 % 3 5 .4 % 7 0 .6 % 6 9 .6 % 71.6% 7 0 .2 % Little Hocking W a te r A s s o c ia tio n _________ (O H ) 54.8% 81.8% 90.7% 9 0 .7 % 77.6% 84.5% 92.9% 90.8% 86.2% 85.0% 8 4 .8 % 84.1% 8 2 .2 % 8 8 .8 % 78.6% 55.2% 4 1 .9 % 8 2 .3 % 80.9% 8 3 .8 % 82.6% Lubeck Public Service District (W V) 38.5% 7 2 .3 % 9 2 .2 % 107.5% 8 1 .0 % 7 3 .2 % 8 1 .6 % 9 4 .5 % 100.1% 8 9 .6 % 7 9 .1 % 8 9 .5 % 9 6 .8 % 9 1 .3 % 8 4 .4 % 6 5 .1 % 3 9 .8 % 8 3 .9 % 8 2 .8 % 8 5 .0 % 8 5 .2 % p. 39 Page 32 of 38 Mason County (W V) 3 9 .5 % 79.8% 9 5 .8 % 9 6 .9 % 90.0% 9 0 .5 % 93.7% 9 4 .6 % 9 1 .4 % 9 0 .8 % 8 3 .3 % 7 8 .1 % 8 2 .8 % 78.8% 7 4 .0 % 5 8 .3 % 31.0% 8 2 .3 % 7 9 .9 % 8 4 .8 % 83.1% Village of Pom eroy (O H) 3 6 .2 % 8 7 .7 % 8 8 .6 % 110.2% 98.9% 8 6 .7 % 9 2 .7 % 103.2% 9 4 .9 % 109.7% 102.5% 9 8 .8 % 101.6% 8 8 .6 % 9 4 .3 % 8 2 .6 % 6 3 .2 % 9 1 .6 % 8 9 .2 % 93.6% 9 4 .8 % Total 45.5% 77.0% 87.2% 9 4 .6 % 82.8% 81.9% 86.1% 8 8 .7 % 88.4% 8 5 .4 % 82.8% 8 1 .2 % 8 5 .1 % 82.0% 75.6% 6 2 .1 % 4 0 .1 % 8 0 .3 % 78.8% 8 1 .8 % 81.0% 31 Page 33 f 38 , Table 2. Availability of Detectable Serum Concentrations for PFCs PFPeA PFHxA PFHS PFHpA PFOA PFOS PFNA PFDA PFUnA PFDoA N um ber of S am ples with D etectable Concentration N 3247 35574 65499 25095 66857 66600 65348 30996 5835 488 %a 4 .9 % 5 3 .2 % 9 7 .9 % 3 7 .5 % 9 9 .9 % 9 9 .6 % 9 7 .7 % 4 6 .3 % 8.7% 0.7% N um ber of S am ples with Concentration <LO D N 63652 31326 1400 41804 42 299 1551 35903 61064 66411 %a 9 5 .2 % 4 6 .8 % 2 .1 % 6 2 .5 % 0.1% 0.5% 2.3% 5 3 .7 % 9 1 .3 % 9 9 .3 % p. 40 N um bers of S am ples with Substitution of 5 0 % of LO D (0 .2 5 ng/mL) N %a 0 0.0% 0 0.0% 1400 2 .1 % 0 0.0% 42 0.1% 299 0.5% 1551 2.3% 0 0.0% 0 0.0% 0 0.0% aDenominator is total possible samples (66,899) 32 Table 3. Population Serum Concentrations for 7 PFCs (ng/ml_) Age Fem ale <k/-) CO CD > Male CN V I otai Fem ale kf? CO >CD M a le CVJ Total Fem ale k. CO CD > O) M ale CO 1 o CsJ i oiai S 2 . co r e m a ie Gender Mean M e d ia n G eom etric Mean Std. Deviation Mean M e d ia n G eom etric M ean Std. Deviation Mean M e d ia n G eom etric M ean Std. Deviation Mean M edian Geom etric M ean Std. Deviation Mean M e d ia n G eom etric M ean Std. Deviation Mean M e d ia n Geom etric M ean Std. Deviation Mean M e d ia n Geom etric M ean Std. Deviation Mean M e d ia n Geom etric M ean Std. Deviation Mean M e d ia n Geom etric M ean Std. Deviation Mean M e d ia n Geom etric M ean Std. Deviation PFHxAa 0.9 0.7 0.7 0.9 1.0 0.7 0.7 1.0 1.0 0.7 0.7 1.0 0.8 0 .5 0.5 1.0 0.9 0.6 0.6 1.3 0.9 0.6 0.6 1.2 0.8 0.3 0.5 1.0 1.0 0.6 0.6 1.4 0.9 0 .5 0.6 1.2 0.8 0.5 0.5 1.0 PFHxAb 1.3 1.0 1.1 1.0 1.3 1.0 1.1 1.0 1.3 1.0 1.1 1.0 1.4 1.0 1.1 1.2 1.4 1.0 1.1 1.5 1.4 1.0 1.1 1.4 1.4 1.0 1.1 1.2 1.5 1.0 1.2 1.6 1.4 1.0 1.2 1.4 1.4 1.0 1.1 1.1 PFHS PFHpAa 10.6 6.1 6.5 13.0 12.6 6.9 7.4 18.3 11.6 6.4 7.0 15.9 6.2 3.7 4.0 9.5 8.3 4.9 1.1 0.7 0.7 1.3 1.1 0.7 0.7 1.3 1.1 0.7 0.7 1.3 0.7 0.3 0.5 0.8 1.0 0.6 5.3 11.8 7.3 4.3 4.6 10.8 3.0 2.2 2.2 3.0 5.3 3.8 3.8 7.6 4 .0 2.9 2.9 5.7 3.3 2.4 2.3 3.7 33 0.6 1.2 0.9 0.6 0.6 1.0 0.5 0.3 0.4 0.6 0.6 0.3 0.4 0.7 0.5 0.3 0.4 0.7 0.5 0.3 0.4 0.8 PFHpAb 1.4 1.0 1.1 1.5 1.5 1.0 1.1 1.5 1.4 1.0 1.1 1.5 1.2 0.9 1.0 0.9 1.5 1.0 1.2 1.4 1.3 0.9 1.1 1.2 1.0 0.8 0.9 0.8 1.2 0.8 1.0 1.0 1.1 0.8 0.9 0.9 1.1 0.8 0.9 1.2 PFOA 73.0 30.7 34.8 120.1 82.1 35.1 39.1 129.1 77.6 32.6 36.9 124.9 51.0 22.1 25.1 85.2 68.4 30.2 33.9 104.9 59.9 25.7 29.3 96.2 42.3 17.0 19.8 118.3 76.5 28.3 33.4 208.1 58.1 21.8 25.2 166.6 80.2 25.7 30.4 260.7 PFOS 22.6 19.9 19.7 12.7 24.6 21.7 2 1 .5 13.4 23.6 2 0 .7 20.6 13.1 20.1 18.0 17.6 11.0 23.4 20.5 2 0 .6 12.7 2 1 .8 19.3 19.1 12.0 16.6 14.8 14.0 9.7 2 4 .3 22.2 2 0 .7 12.8 20.1 18.1 16.8 11.9 2 0 .8 17.7 16.9 14.2 PFNA 1.9 1.6 1.7 1.4 1.9 1.6 1.7 1.1 1.9 1.6 1.7 1.3 1.4 1.3 1,3 0.7 1.6 1.5 1.5 0.8 1.5 1.4 1.4 0.7 1.4 1.2 1.2 0.8 1.7 1.6 1.6 0.8 1.5 1.4 1.4 0.8 1.5 1.3 1.3 0.8 PFDAa 0.5 0.5 0.4 0.3 0.5 0.5 0.4 0.3 0.5 0.5 0.4 0.3 0.5 0.4 0.3 0.4 0.3 0.5 0.3 0.4 0.3 0.5 0.3 0.4 0.3 0.5 0.3 0.4 0.4 0.5 0.5 0.4 0.6 0.5 0.3 0.4 0.5 0 .3 0.4 0.4 PFDAb 0.7 0.6 0.7 0.2 0.7 0.6 0.7 0.3 0.7 0.6 0.7 0.3 0.7 0.6 0.7 0.3 0.7 0.7 0.7 0.3 0.7 0.6 0.7 0.3 0.8 0.6 0.7 0.4 0.8 0.7 0.7 0.8 0.8 0.7 0.7 0.6 0.8 0.7 0.7 0.4 Page 34 of 38 IV 'd Age CD 0) >CO c o 3Q_ Qo_ Id o 1- Gender M a le Total Fem ale M ale Total Fem ale M ale Total Mean M e d ia n Geom etric Mean Std. Deviation Mean M e d ia n Geom etric M ean Std. Deviation Mean M e d ia n Geom etric Mean Std. Deviation Mean M e d ia n Geom etric M ean Std. Deviation Mean M e d ia n Geom etric Mean Std. Deviation Mean M e d ia n Geom etric M ean Std. Deviation Mean M e d ia n Geom etric M ean Std. Deviation Mean M e d ia n Geom etric M ean Std. Deviation PFHxA3 0.9 0.5 0.6 1.1 0.9 0.5 0.6 1.0 0.8 0.3 0.5 0.9 0.9 0.3 0.5 1.1 0.8 0.3 0.5 1.0 0.8 0.5 0.5 1.0 0.9 0.6 0.6 1.2 0.9 0.5 0.6 1.1 PFHxAb 1.4 1.0 1.2 1.2 1.4 1.0 1.1 1.2 1.3 1.0 1.1 1.0 1.5 1.0 1.2 1.4 1.4 1.0 1.1 1.2 1.4 1.0 1.1 1.1 1.4 1.0 1.2 1.4 1.4 1.0 1.1 1.3 PFHS 4.7 3.4 3.5 16.8 4.0 2.9 2.8 11.9 4.7 3.3 3.4 5.3 4 .6 3.4 3.4 5.3 4.7 3.3 3.4 5.3 4.3 2.7 2.8 6.2 5.9 3.8 4 .0 12.8 5.1 3.2 3.3 10.0 PFHpA3 0.6 0.3 0.4 0.8 0.5 0.3 0.4 0.8 0.7 0.3 0.4 1.1 0.6 0.3 0.4 0.9 0.6 0.3 0.4 1.0 0.6 0.3 0.4 0.8 0.7 0.3 0.4 0.9 0.6 0.3 0.4 0.9 PFHpAb 1.2 0.8 1.0 1.2 1.2 0.8 0.9 1.2 1.4 0.9 1.0 1.6 1.3 0.9 1.0 1.3 1.3 0.9 1.0 1.4 1.2 0.8 1.0 1.2 1.3 0.9 1.0 1.3 1.2 0.9 1.0 1.2 PFOA 120.4 37.7 43.8 339.0 99.4 30.7 36.2 301.4 107.0 41.0 44.2 199.9 120.8 42.8 47.2 394.1 113.8 41.9 45.7 311.7 68.8 23.6 27.9 190.6 98.2 33.7 39.4 284.3 82.9 28.2 32.9 240.8 PFOS 26.6 23.5 22.3 16.7 2 3 .6 20.5 19.3 15.7 28.2 24.2 2 2 .9 19.7 3 0 .3 26.1 24.7 2 3 .2 29.2 25.1 2 3 .7 2 1 .5 2 0 .7 17.6 17.0 14.1 2 6 .0 22.9 2 1 .9 16.5 2 3 .3 20.2 19.2 15.6 PFNA 1.6 1.5 1.5 0.9 1.6 1.4 1.4 0.9 1.5 1.3 1.3 0.8 1.5 1.4 1.3 0.9 1.5 1.4 1.3 0.8 1.5 1.3 1.3 0.8 1.7 1.5 1.5 0.9 1.6 1.4 1.4 0.9 PFDAa 0.5 0.3 0.4 0.8 0.5 0.3 0.4 0.6 0.5 0.3 0.4 0.4 0.5 0.3 0.4 0.4 0 .5 0.3 0.4 0.4 0 .5 0.3 0.4 0.4 0.5 0 .3 0.4 0.6 0.5 0.3 0.4 0.5 PFDAb 0.8 0.7 0.7 1.1 0.8 0.7 0.7 0.9 0.8 0.7 0.7 0.4 0.8 0.7 0.7 0.5 0.8 0.7 0.7 0.5 0.8 0.7 0.7 0.4 0.8 0.7 0.7 0.8 0.8 0.7 0.7 0.7 3 Substitution with 50% of LOD for values reported as <LOD bNo substitution for values reported as <LOD p. 42 34 Table 4. Age and Gender Adjusted Serum PFC Concentrations by Water Districts Page. 36 of 38 W ater District Ditv nf Rfilnrfi (O H ) Little Hocking W a te r Association (O H) Lubeck Public Service District (W V) Mason County (W V) Tuppers Plains (O H) Village of Pom eroy (O H) Private W ell (W V or O H ) M ean (ng/m L) Std. Error M ean (ng/m L) Std. Error M ean (ng/m L) Std. Error M ean (ng/m L) Std. Error M ean (ng/m L) Std. Error M ean (ng/m L) Std. Error M ean (ng/m L) Std. Error PFHxA3 0.86 0.01 0.85 0.01 1.02 0.01 0.72 0.01 0.84 0.01 0.83 0.02 0.65 0.09 PFHxAb 1.41 0.02 1.39 0.02 1.51 0.01 1.28 0.02 1.38 0.02 1.38 0.03 1.88 0.16 PFHS 5.82 0.11 5.70 0.09 5.58 0.08 4.15 0.09 4 .4 8 0.08 4 .2 5 0.17 9.27 0.79 PFHpA3 0.64 0.01 PFHpAb 1.10 0.02 PFOA 4 2 .9 6 2.48 1.15 1.86 2 2 7 .5 9 0.01 0.01 2.03 0.61 0.01 0.38 0.01 0 .4 3 0.01 0.38 1.05 0.01 0.83 0.02 0.91 0.02 0.83 9 2 .3 6 1.78 16.00 2.06 4 2 .0 7 1.96 15.96 0.01 0.04 3.83 0.82 1.48 1 3 2 .5 6 0.07 0.14 18.41 PFOS 2 3 .1 8 0.16 2 3 .4 7 0.14 2 4 .9 6 0.12 23.01 0.14 2 2 .2 9 0.13 2 0 .9 7 0.25 2 6 .1 5 1.22 PFNA 1.50 0.01 1.60 0.01 1.64 0.01 1.59 0.01 1.50 0.01 1.46 0.02 1.67 0.07 PFDAa PFDAb 0.47 0.73 0.01 0.01 0.50 0.77 0.01 0.01 0.55 0.00 0.45 0.01 0.53 0.04 0.47 0.82 0.01 0.72 0.01 0.74 0.01 0.69 0.00 0.02 0.40 0.81 0.01 0.08 a Substitution with 50% of LOD for values reported as <LOD bNo substitution for values reported as <LOD p. 43 35 Page 37 o f 38 Table 5. Summary of Intra- and Inter-Lab Quality Assurance Prim ary Lab T est Results (ng/mL) PFHxA PFHS PFHpA PFOA PFOS PFNA PFDA N Mean M ed ian N Mean M ed ian N Mean M ed ian N Mean M e d ia n N Mean M e d ia n N Mean M ed ian N Mean M e d ia n 664 1.3 1.0 1236 4.6 3.1 446 1.2 0.9 1269 77.3 25.3 1261 22.9 19.5 1246 1.6 1,4 566 0.8 0.7 Intra-Lab Com parisons3 Prim ary Lab QA Sam ple (ng/mL) A b s o lu te D iffe re n c e Percent D iffe re n c e Coefficient of Variation Prim ary Lab Test Results (ng/mL) Inter-Lab Com parisons6 Secondary Lab QA Sam ple (ng/mL) Absolute D iffe re n c e Percent D iffe re n c e Coefficient of Variation 612 1.3 0.9 1241 4.6 3.1 434 1.2 0.9 1269 80.4 25.3 1261 23.2 19.8 1243 1.6 1.4 570 0.8 0.7 574 0.3 0.1 1234 0.4 0.2 410 0.1 0.1 1269 9.7 1.4 1260 2.0 0.7 1240 0.2 0.1 516 0.1 0.0 574 18.3% 11.8% 1234 9.4% 4 .9 % 410 8.5% 4.2% 1269 10.1% 5.2% 1260 8.4% 4 .1 % 1240 9.0% 6.5% 516 6.9% 0.0% 574 0.1 0.1 1234 0.1 0.0 410 0.1 0.0 1269 0.1 0.0 1260 0.1 0.0 1240 0.1 0.1 516 0.1 0.0 1180 1.2 0.9 2561 4 .9 3.5 1074 1.5 1.0 2603 134.5 43.9 2594 22.3 19.4 2539 1.6 1.4 1200 0.8 0.7 All values reported as <LOD 2319 4.6 3.2 583 1.4 0.9 2599 129.7 39.3 2588 22.7 19.6 2329 1.3 1.2 409 0.8 0.6 2316 1.3 0.8 572 0.8 0.5 2599 27.1 6.9 2588 3.9 2.6 2314 0.4 0.3 371 0.3 0.2 N /A 2316 2 8 .8 % 2 3 .9 % 572 4 4 .3 % 4 2 .0 % 2599 2 1 .0 % 16.7% 2588 17.4% 14.0% 2314 2 8 .7 % 2 4 .9 % 371 3 3 .8 % 28.6 2316 0.2 0.2 572 0.3 0.3 2599 0.2 0.1 2588 0.1 0.1 2314 0.2 0.2 371 0.2 0.2 Comparison between matched samples for main test results and blinded, duplicate QA samples sent to the primary lab 6 Comparison between matched samples for main test results and blinded, duplicate QA samples sent to the secondary lab p. 44 36 Figure 1. PFC Concentrations Stratified by Age and Gender Panel A: PFOA Panel B: PFOS wcejL Panel C PFHS A**prr*J M4`*n C l S A n m (n*fU A O'*) 254x190mm (96 x 96 DPI) p. 45 Page 38 of 38 Page 39 of 38 Figure 2. Comparison of Geometric Means for PFC Serum Concentrations for C8 Health Project Results vs Two Nationally Representative Samples Pans! A: PFOA (ng/m l) Panai B: P f OS (ng/mL 254x190mm (96 x 96 DPI) C8 Science Pn'el Website p. 47 Page 1 o f 17 C8 Science Panel C8 Science Panel Studies H om e T he S cien ce P a n el..................... Summary of the C8 Science Panel Studies Panel M embers Press C8 Science Panel Studies - Introduction - Why Further Study is Necessary - Summary of Studies - Timeline - Confidentiality of Personal Information - Additional Community Participation Info for Study Participants C8 Study results Consent Form C8 Health Project C8 Test Results N ew sletter Links Contact No single epidem iologic study is sufficient to determine whether C8 damages health. The Science Panel has designed a series of different kinds of studies which are described briefly below. These studies began in late 2006 and are currently ongoing, with results already coming out of them (follow link at left to C8 study results). Results from these studies take from one year to five years from starting. Some of these studies are based on already collected information, while others require collection of new information, including interviews and blood samples. Any inform ation gathered on individuals w ill be kept confidential by the Science Panel. In many cases a study requires a team of investigators, but in all studies a member of the Science Panel is overseeing the conduct of each specific study. Choose from the list below to jump to a specific study: 1. Cholesterol, diabetes, uric acid, and C8 levels among participants in the C8 Health Project 2. Cross Sectional Study of C8 and Immune Function. Hematopoietic Function. Liver. Kidney, and Endocrine Disorders and Cancer Prevalence - a Prevalence study among partic ip a nts in the C8 Health Project. 3. Community follow-up study 4. W orker follow-up study 5. The Study of Birth Outcomes in the Mid-Ohio V alley 6. The Study of Birth Outcomes among the C8 Health Project Participants 7. The Geographic Patterns of Cancer Study 8. Short Term Follow-up Study of C8 and Immune. Liver. Kidney and Endocrine Function 9. Exposure study http://www.c8sciencepanel.org/studies.html 7/13/2009 C8 Science Panel Website p. 48 Page 2 o f 17 10. Half-life study 11. Study of C8 and Neurobehavioral Development among children from the C8 Health Project 1. Cholesterol, diabetes, uric acid, and C8 levels among participants in the C8 Health Project (study completed) Investigator: Kyle Steenland Outline of study The C8 Health Project carried out by Brookmar gathered information from August 2005 to July 2006 and analyzed blood for C8 level, cholesterol and uric acid. Information on self-reported diabetes was also recorded. In three different reports we have looked at the data collected from approximately 55,000 participants over age 20 to determine whether cholesterol and uric acid increased with C8 levels in the blood, and whether those with higher C8 levels in the blood had more diabetes. Analyses were adjusted for other variables which could affect the outcomes, such as age, gender, obesity, and smoking. More detailed results of these studies can be found elsewhere on this website (link). Briefly, higher C8 was linked to higher cholesterol. Those in the highest 25% of C8 had a 50% increased risk of having high cholesterol (>240 mg/dl) compared to those in the lowest 25% of C8. Higher C8 was also associated with high uric acid, although less dram atically, with about a 30% increased risk of high uric acid for those in the top 25% of C8 vs. the lowest 25%. Higher levels of C8S (C8 with a sulfur group attached - this chemical was not used by Dupont nor released into the environment) was also associated with higher levels of cholesterol and uric acid. Neither self-reported nor medically validated diabetes (adult onset, Type II diabetes) were associated with higher levels of C8. Study status (June 2009) These three reports were completed in early 2009. Results of these studies are available here. Briefly, higher C8 was associated with higher cholesterol and higher uric acid, while self-reported diabetes was not linked to C8. However, these reports do not provide conclusive evidence http://www.c8sciencepanel.org/studies.html 7/l 3/2009 C8 Science Panel Website p. 49 Page 3 o f 17 regarding whether there is a probable link between C8 and disease because 1) one cannot determ ine whether C8 exposure preceded or followed the outcome of interest, and 2) in many cases the outcome is a biom arker and not a disease itself. Nonetheless they provide useful evidence that adds to the overall picture. A top 2. Cross Sectional Study of C8 and Immune Function, Hematopoietic Function, Liver, Kidney, and Endocrine Disorders and Cancer Prevalence - a Prevalence study among participants in the C8 Health Project. Investigator: Tony Fletcher Outline of study This study addresses the cross sectional relationship of C8 and a number of disease and clinical disease markers in a population of 69,030 participants in the C8 Health Project. They resided or worked in the six w ater districts near the DuPont plant in Parkersburg, WV and participated in the C8 Health Project. The C8 Health Project collected data during August 2005 to August 2006 and participants completed a questionnaire and gave blood. The blood was analyzed for C8 and a substantial set of clinical parameters. The questionnaire included self-reported medical history and information on education, smoking habits, age, and other characteristics which are taken into account in the analyses. Self-reported medical history included questions about whether the participant has ever been diagnosed with a number of diseases including cancers. Some analyses will focus on the relationships between C8 blood levels and clinical parameters, including the results of blood tests on liver enzymes, hormones, and markers of immune function. Other analyses will investigate the relationship between reported disease (including cancer, diseases indicating disturbance of the immune system, disease related to hormone imbalances, liver and kidney disease) and estim ates of C8 exposure leading up to the reported date of diagnosis. These exposure estimates will make use of measured C8 levels in blood and estim ates of http://www.c8sciencepanel.org/studies.html 7/13/2009 C8 Science Panel Website p. 50 Page 4 o f 17 exposure to C8 in the past. Comparisons are adjusted for other variables of importance such as age, sex, smoking and weight. The first phase of analyses uses the C8 concentrations measured at the time of the C8 Health Project. The second phase will allow rates of disease to be analyzed in relation to estimated past C8 exposure. This will focus on diseases including kidney, liver, autoimmune and thyroid diseases and will take place in 2010 once we have integrated historic exposure data and date of disease onset. Study status (June 2009) A report on immune biomarkers was submitted to the court in March 2009 and is available here. Results suggested that there may be a relation between immune function and PFOA exposure in exposed persons. However as noted in the report, these results cannot be directly interpreted as indicating an increase in disease risk in this population, but they warrant further investigation which is underway in study #8 "Short Term Follow-up Study of C8 and Immune, Liver, Kidney and Endocrine Function". Other analyses and reports are being prepared and several w ill be made public during 2009. This work is being done in collaboration with WVU researchers who also hold a copy of the data from the C8 Health Project. A top 3. Community follow-up study Investigator: Kyle Steenland, Emory University Outline of study This study is a 4 year follow-up study exploring disease occurrence among adult participants in the C8 Health Project, a survey of about 70,000 community residents (of which 55.00 were above age 20) residing in six water districts conducted from July 2005 - August 2006. Among these, about 40.000 have agreed to participate in the community follow-up study. We are interviewing these 40,000, asking about disease occurrence over time. There are two interviews - one in 2009 and another in 2010. http://www.c8sciencepanel.org/studies.html 7/13/2009 C8 Science Panel Website p. 51 Page 5 of 17 Diseases of interest include cancer, heart disease, and any other important disease such as diabetes and neurologic disease. Interviews can be completed on the phone or on the Web. Forty dollars per person is paid for answering the questionnaire, which takes less than 30 minutes. For those who answer positively to the occurrence of certain diseases we w ill ask permission to view medical records to confirm the new disease occurrence. We will also trace any deaths which occur during the 4 year follow-up and determine the cause of death. Finally, we will cross-link study participants with Ohio and WV cancer registries for another source of inform ation on cancer occurrence. Once all this information has been collected, we will compare the rate of disease occurrence in this population of adults to that expected based on comparable Americans who had minimal or no exposure to C8. If C8 is related to any health damage, then disease rates among the 40,000 living near the W ashington W orks plant w ill be higher than those in comparable Americans without exposure. Otherwise, they will not. We will also make some comparisons of disease rates within the 40,000 adults with past exposure. Here we w ill draw on the C8 blood level measured during the C8 Health Project. We will compare the rate of new disease occurrence among those with higher levels in 2005-2006 to the rate among those with low levels in 2005-2006. We will also estimate past levels of C8 exposure over time for all people in the study, based on the ir residential history and an estimate of C8 levels in the water over time (see Exposure Study). We can then analyze disease occurrence by total C8 in the body. If C8 is related to any health effects, long term exposure could be more im portant than recent exposure as measured in the blood in 2005-2006 in the C8 Health Project. T im e lin e : data collection now to 2010, results in 2011. Study status (June 2009) As of June 2009, approxim ately 70% of study subjects had completed initial interviews, and the response rate for those contacted was above 90%. Subjects report a higher-thananticipated proportion of medical conditions which require medical verification, which may result in a need for supplemental funds for this study. We are evaluating to what extent we can use the previously collected medical validation http://www.c8sciencepanel.org/studies.html 7/13/2009 C8 Science Panel Website p. 52 Page 6 o f 17 data from Brookmar's C8 Health Project. Initial data suggests that for approximately half of the currently reported medical conditions, a prior verification exists from Brookmar. We are now seeking medical records from the first several thousand people who have completed interviews. This study is anticipated to provide im portant evidence regarding whether there is a probable link between C8 and disease because they are follow -up studies in which it is clear that C8 exposure preceded disease. Taken together with all the other evidence, it will provide the basis for a judgm ent about a probable link for chronic diseases such as cancer, heart disease, diabetes. A top 4. Worker follow-up study Investigator: Kyle Steenland, Emory University Outline of study C8 has been used in the m anufacturing of Teflon and other products by DuPont in its W est Virginia W ashington Works plant. Many workers in the plant have been exposed to C8 over time, at levels higher than the surrounding community. We will conduct a study of disease occurrence among workers at the plant. DuPont has already assembled a group of approximately 6,000 workers who worked at the Washington Works plant at any time between 1 Jan 1952 and 31 Dec 2001. DuPont has studied the mortality of these workers to determine whether they died of certain diseases at a higher rate than expected. However, studies of death patterns may be less revealing than studies of disease occurrence (fatal and non-fatal disease). We are following these same workers to determine what diseases they have had, including non-fatal as well as fatal disease. We are interested in major diseases such as cancer, heart disease, diabetes. Workers are currently being interviewed in 2009, and will be interviewed once more with a shorter second interview in 2010. All workers will be free to participate or not. This study will be conducted independently of DuPont, and all information will be kept confidential. No inform ation collected http://www.c8sciencepanel.org/studies.html 7/13/2009 C8 Science Panel Website p. 53 Page 7 o f 17 on any individual worker w ill be given to DuPont or anyone else. We estimate that about 2/3 of the 6,000 workers are no longer working. DuPont has developed a way to estim ate C8 exposure depending on where a worker has worked, based on C8 blood measurements for approxim ately 1,000 workers in 2004. DuPont has classified plant jobs into three groups of low, medium, and high exposure to C8. We plan to develop this work further, in order to take into account changes in exposure level over time. We may also create additional exposure categories beyond the low, medium, and high categories. Interviews are done either via a telephone interview or website interview, and take approxim ately 30 minutes in length. Interviews cover medical history and other descriptive inform ation such as years of schooling, marital status, smoking history, alcohol history, height, and weight, and medications. Subjects are paid for their time as in the commuhity study. As part of our study we will determine whether workers have died and if so, cause of death.. In addition, we w ill check the records of the West Virginia and Ohio cancer registries to see who has developed cancer. For those workers who report having had a disease, we will ask permission to review their medical records to confirm this information. For workers who have died we will interview their relatives to find out what diseases they had. Once all this inform ation has been collected in 2009-2010, we will then compare the rate of new disease occurrence among the workers to that expected based on comparable Americans who had minimal or no exposure to C8. If C8 is related to any health damage, then disease rates among the workers will be higher than those in comparable Americans without exposure. Otherwise they will not. We will also make some comparisons within the workers based on their level of exposure to C8. We will compare rate of new disease occurrence among those with higher levels of C8 over time to rate among workers with low levels of exposure. Tim eline: data collection now to 2010, results in 2011 Study Status (June 2009) As of June 2009 approximately 50% of workers had http://www.c8sciencepanel.org/studies.html 7/13/2009 C8 Science Panel Website p. 54 Page 8 o f 17 completed initial interviews, and the response rate for those contacted was above 90%. Subjects report a higher-than-anticipated proportion of medical conditions whichrequire medical verification, which may result in a need for supplem ental funds for this study. We are evaluating to what extent we can use the previously collected medical validation data from Brookmar's C8 Health Project. Initial data suggests that for approximately half of the currently reported medical conditions, a prior verification exists from Brookmar. This study is anticipated to provide im portant evidence regarding whether there is a probable link between C8 and disease because they are follow up studies in which it is clear that C8 exposure preceded disease. Taken together with all the other evidence, it will provide the basis for a judgm ent about a probable link for chronic diseases such as cancer, heart disease, diabetes. 5- The study of Birth Outcomes in the Mid-Ohio Valley Investigator: David Savitz Outline of study This study w ill evaluate whether C8 exposure is related to birth outcomes, including stillbirth, preterm birth (early delivery), and birth weight. Birth outcome information will be collected from state birth records for selected counties in Ohio and West Virginia. We are including areas that had C8 in the drinking w ater and areas that did not have C8 in the drinking water, all within the same general region. The State Health Departments' Vital Records offices maintain birth records and can provide a complete list of all births in the region. C8 exposure for the mother and child will be based on the estim ated amount of C8 in the drinking water where the mother was living at the time the baby was born. We will get this estim ate from another Science Panel study (see the Exposure Study). The Exposure Study is working to estim ate exposure for different places at different times based on distance from the Washington Works plant and the amount of C8 released from the plant. The Study of Birth Outcomes in the Mid-Ohio Valley http://w'ww.c8sciencepanel.org/studies.html 7/13/2009 C8 Science Panel Website p. 55 Page 9 o f 17 w ill help to determine whether mothers with higher estimated C8 exposure had a higher risk of having poor birth outcomes. If exposure to C8 increases the risk of a poor birth outcome, we expect to see worse birth outcomes in women with more C8 exposure. We will make adjustm ents for other influences on pregnancy health, including m other's age, race, education, marital status, number of previous births, and smoking habits. These characteristics about the mother are listed on the birth certificate. We will also take into account information from the U.S. Census about com munity characteristics, such as average income, proportion below the poverty level, and average housing value. Study Status (June 2009) We have received birth records for selected areas of Ohio and West Virginia from the State Health Departments. For Ohio, we have live birth records for the period from 1989 2004. For West Virginia, we have live birth and stillbirth records for the period 1980 - 2004. The mother's residence at the time of birth has been assigned to a location using either address or Zip Code. We are tabulating the U.S. Census data about the community characteristics. Once the data from the Exposure Study are available, we will continue with the analyses. This project has begun and is expected to be completed in 2010 once the estim ates of C8 exposure are available from the Exposure Study. A tog 6. The Study of Birth Outcomes among the C8 Health Project Participants Investigator: David Savitz Study Overview This study will evaluate whether C8 exposure is related to birth outcomes, including miscarriage (pregnancy loss before 20 weeks), preterm birth (early delivery), low birth-weight, average birth-weight, preeclampsia (pregnancy complication with high blood pressure), and birth defects. The primary data source for this study is the C8 Health Project questionnaire. Women who enrolled in the C8 Health Project in 2005 - 2006 were asked questions about any http://www.c8sciencepanel.org/studies.html 7/13/2009 C8 Science Panel Website p. 56 Page 10 o f 17 pregnancies they had. Because women may not remember exactly how long the pregnancy lasted before the baby was born (important to define preterm birth) or exactly how much a baby weighed at birth (im portant to define low birth-weight births), we w ill also use data from birth records kept by the Ohio and West Virginia Health Departments. The birth records are helpful because they have an exact measurement of gestational age and birth-w eight. However, we w ill only be able to use the extra inform ation from the birth certificates for the 70% of women who consented to participate in Science Panel research linking data sources. For all women in the C8 Health Project reporting one or more pregnancies, we will estimate their blood levels at the time of their pregnancies based on where she lived, her water consumption patterns, and her C8 blood level measured at the time of her enrollment. We will get this estimate from another Science Panel study (see the Exposure Study). The Study of Birth Outcomes among the C8 Health Project Participants will help to determine whether mothers with higher estimated C8 exposure had a higher risk of having poor birth outcomes. If exposure to C8 increases the risk of a poor birth outcome, we expect to see worse birth outcomes in women with more C8 exposure. We w ill make adjustm ents for other influences on the health of pregnancy, such as m other's age, race, education, marital status, number of previous births, and smoking habits. Study Status (June 2009) An initial analysis of C8 Health Project participants' births was completed and submitted to the court in March 2009. You can view the status report here. For this initial analysis, we restricted to births in the 5 years before the Health Project and used the C8 blood measurement as the measure of exposure. This analysis used only data from the C8 Health Project questionnaire. For the 70% of the women who provided consent, we are linking the women's pregnancies to the Ohio and West Virginia State Health Department birth records for births from 1980-2004. Once the exposure data are available from the Exposure study we will conduct additional analyses that include more births to more women over longer periods of time. This project has begun and is expected to be completed in 2010 once the estimates of C8 exposure are available from the Exposure Study. A top http://wavw.c8 sciencepanel.org/studies. html 7/13/2009 C8 Science Panel Website p. 57 Page 11 o f 17 7. The Geographic Patterns of Cancer Study Investigators: Tony Fletcher and Veronica Vieira, Boston University Outline of study This study addresses the relationship between past cancer incidence from 1993 to 2005 in regions of West Virginia and Ohio including the six contaminated water districts along with surrounding counties. The goal is to determine if cancer rates by geographical area vary in relation to the C8 levels in those areas. The study is being carried out in collaboration with researchers at Boston University and Battelle and the state cancer registries in WV and OH. The population of approximately 500,000 people will be grouped by residence into census blocks and tracts according to sim ilar average C8 exposure. The same exposure category w ill be assigned to all individuals in a geographic area (rather than to each individual as in the community cohort study). Information on cancer cases in the relevant counties is available from the West Virginia Cancer Registry and Ohio Cancer Surveillance Systems. Estimated exposure to C8 in the water for these same geographical areas over time w ill be provided by the parallel exposure modeling project. Cancer cases will be assigned to these exposure groups by residence at time of diagnosis. Cancer incidence rates will then be computed to determine whether rates of cancer incidence d iffe r in relation to levels of average exposure to C8. Results from this study will complement the community cohort study results. However, no Probable Link determ ination concerning cancer and C8 will be made until both studies are completed. Study to be completed in 2010. Study status (June 2009) The study is currently on target to be completed in 2010, assuming cancer data are supplied by both State cancer registries. Definition of exposure areas in terms of evolving water supplies has been completed. Cancer data have been received for the Ohio counties and is being classified into exposure areas. Provision of detailed cancer data from West http://www.c8sciencepanel.org/studies.html 7/13/2009 C8 Science Panel Website p. 58 Page 12 of 17 Virginia has been somewhat delayed by temporary freeze on recruiting staff in the state. Detailed Exposure data are anticipated by February 2010 to allow com pletion of the analyses. A top 8. Short Term Follow-up Study of C8 and Immune, Liver, Kidney and Endocrine Function Investigator: Tony Fletcher Outline of study This study will primarily assess changes of some clinical markers in relation to changes in C8, and detailed indicators of immune status, in a population of 800 of the C8 Health Project participants who agreed to participate in Science Panel studies. We will also assess the risk of common infectious disease and urinary markers indicative of kidney disease. These participants w ill be recalled and invited to participate in a second interview and provide a second blood sample, and a urine sample. Statistical analyses will focus on the relationship between trends in C8 serum levels and trends in various clinical markers: of immune, cancer, thyroid, endocrine, kidney and liver function; both C8 and the biomarkers will then have been measured on two occasions. An extended panel of tests for assessing immune function will be given and the association with C8 investigated. In a subset of 400 of these participants, the extent to which C8 modifies the protection afforded by influenza vaccination will be assessed. The incidence of infectious disease in relation to C8 will be assessed by both questionnaire data on self reported disease, including infectious diseases and serological tests of recent latent viral infections, specifically herpes simplex virus (HSV) infection. The study will provide important new information because of its longitudinal nature; it w ill consider change in biomarkers over time in relation to changes in C8 levels in the blood. Particular attention will be given to markers of liver, kidney, endocrine and immune function. Additional, more specific ' immune screening tests will allow the assessment of the http://www.c8sciencepanel.org/studies.html 7/13/2009 C8 Science Panel Website p. 59 Page 13 of 17 response of the immune system to C8 exposure, and infectious disease risk in relation to C8 w ill also be assessed. Results are expected in 2011. Results on biomarkers in this study are expected to provide important evidence for the assessment of the relation between C8 and conditions including liver disease, kidney disease, thyroid disease, and auto-immune disease. Study Status (June 2009) Field work is planned for October - December 2009 in the study area. Hiring of some key staff and preparations for the survey are currently ongoing. a top 9. Exposure study Investigators: Kyle Steenland and Barry Ryan, Emory University This project will estimate past exposure levels to C8 in the water for community residents living near DuPont's Washington Works plant. C8 from the plant was released in the air and also released into the Ohio River from the 1950s until recently, resulting in community exposure, largely via drinking water consumption. It is believed that most C8 in the body comes from the water supply rather than breathing air with C8 in it or eating food with C8 in it. C8 reached water supplies by entering the groundwater, which is the source of wells for both public and private drinking water. C8 entered the groundwater both by trickling down through the soil and via the Ohio River, which has some exchange with the groundwater. The peak of C8 use and of emissions occurred in the late 1990s. C8 emissions in the air have been largely eliminated in the last few years, as have any significant releases into the Ohio River. Historical exposure to C8 will be important for the other epidemiologic studies conducted by the Science Panel. The proposed work will estimate exposure for all times back to the beginning of release of C8 from W ashington Works. We will use information on how much C8 was released from the plant each year into air and water, known wind patterns, and whatever actual measurements exist of C8 in the water. http://www.c8sciencepanel.org/studies.html 7/13/2009 C8 Science. Panel Website p. 60 Page 14 o f 17 This will let us estimate how much C8 was in the drinking water over time at different locations around the plant. Taken together with residential histories available from the C8 Health Project, we w ill be able to estimate how much C8 participants in the C8 Health Project have taken into their bodies from drinking water over time. We will also consider what happens to C8 in the body in order to estimate what C8 levels have been in the blood over time for participants in the C8 Health Project. Timeline: data collection and analysis 2007-8, results 2009 Study Status (June 2009) Two unforeseen issues have arisen of importance, namely the way the groundwater flows (speed, direction) and the size of particles emitted from the plant. The groundwater flow is important because we need to understand how long C8 is likely to be present in the groundwater and where it w ill be in relation to the public wells which pump groundwater. The particle size is im portant because we need to know how fast the C8 particles emitted into the air w ill settle on the ground. Both of these have important im plications on the amount of C8 expected to be in public water systems. New data for particle size distributions have been obtained from DuPont. Although the particle size data are sparse, we are using them to develop a better understanding of how C8 is dispersed in the air. With regard to groundwater, we are making significant progress both with regard to groundwater movement and understanding how the Ohio River surface water interacts with the groundwater. This study is to be completed in early 2010. A top 10. Half-life study Investigators: Kyle Steenland and Barry Ryan, Scott Bartell, Emory University Outline of study This project w ill examine the blood C8 levels of about 70,000 people who live near the W ashington Works plant in West http://w'vvw.c8sciencepanel.org/studies.html 7/13/2009 C8 Science Panel Website p. 61 Page 15 o f 17 Virginia and had their blood levels of C8 measured in the C8 Health Project. Although many of these people had been exposed to C8 for decades, their blood C8 levels were never measured before 2005. In order to better understand the relationship between past C8 exposures and current blood C8 levels, and to improve the quality of exposure estim ates in ongoing health studies, we have invited 200 adults from the C8 Health Project to participate in a longer study designed to determine the rate of removal of C8 from the body. The rate of removal is often called the "half-life", the period of time necessary for the body to clear out half of its C8. Before this study there was an estim ate, that the average half-life of C8 for humans was 3-4 years, but this is based on only a few measurements among workers at 3M, another company which has used C8. During 2007-8 carbon filters were installed to remove C8 from several contaminated water systems near the West Virginia chemical plant. People served by these water systems are expected to have lower exposures to C8 once filtration begins, which should cause a decline in blood C8 levels over time. This presents an opportunity to estim ate the rate of decline through a half-life study based on repeated measurement of blood C8 levels before and after the carbon filters are installed. Each participant in this half-life study has been asked to donate up to eight blood samples during a four year period. Levels of C8 will be measured in each blood sample. Participants will also be asked to complete a short questionnaire each time a blood sample is taken, and receive financial compensation amount? for each blood sample. The results w ill help us estim ate past C8 exposures for participants in the C8 Health Project, which will in turn help determine whether C8 has any health effects in the other studies being done by the Science Panel. As in all Science Panel studies, all individual data w ill be kept confidential. Tim eline: data collection 2007-2010, analysis and results ongoing, beginning 2009 and completion in 2011 Study Status (June 2009) Preliminary results based on the first year of the study were released in March, and were submitted to the court as a status report. You can view the status report here. Briefly, the estimated average rate of decrease in serum PFOA concentration after water filtration was 26% per year. Our best preliminary estimate of the average PFOA serum half http://www.c8sciencepanel.org/studies.html 7/13/2009 C8 Science Panel Website p. 62 Page 16 o f 17 life using these data is 2.3 years. Individual estimated half lives varied widely in our study; most were between 1.5 and 4.6 years. At this rate about 95% of PFOA would be removed from the body 10 years after exposure ended. However, data from only one year are not sufficient to accurately estimate half-life. We will have a better estimate as time goes on. A top 11. Study of C8 and Neurobehavioral Development among children from the C8 Health Project Investigator: David Savitz Outline of study This study will evaluate whether neurobehavioral developm ent is related to C8 exposure among children who participated in the C8 Health Project. Neurobehavioral development refers to how children learn and behave compared to other children the same age. Some of the children who participated in the C8 Health Project and who w ill be 6-11 years old during the data collection period will be invited to participate in the Neurobehavioral Development Study. We w ill use data from the C8 Health Project to identify eligible children, and expect to enroll approxim ately 550 of them. Only one child per fam ily w ill be allowed to participate. We will enroll only children who were born and lived their entire lives in one of the affected water districts, and provided consent to participate in Science Panel research. By restricting the study to children who spent their entire lives in only one water district we will have a better idea of how much C8 a child was exposed to over his/her lifetime. A mobile study van will visit eligible families at their home. Children will be weighed and measured, asked questions, and play reading, word, and number games with a specially trained research assistant to assess their skills. At the same time, the child's mother w ill be interviewed. The mother will be asked questions about the child's health, behavior, and home environment. Additionally, the mother will take a short standardized test on vocabulary, sim ilarities and block design. With the mother's permission, we will contact the http://wavw .c8sciencep anel.org/studies.htmI 7/13/2009 C8 Science Panel Website p. 63 Page 17 o f 17 child's teacher for an evaluation of the child's performance at school relative to his/her classmates. At the end of the interview we will cut a small piece of hair from the child's head for measuring environmental exposures. The information we collect from the mother and child, together with the measure of C8 exposure we have from the C8 Health Project, will be used to help us understand whether there is a relation between C8 exposure and the way children learn and behave. Study Status (June 2009) We have finished the planning phase of the Neurobehavioral Development Study and created a list of children who may be eligible to participate. We will begin contacting fam ilies in July 2009 about participating in this study. We w ill be interviewing children and their mothers from summer 2009 fall 2010. We expect to have final study results in 2011. A top http://www.c8sciencepanel.org/studies.html 7/13/2009