11.1 Effects
Besides through food and air, PCBs can enter the bodies of humans and animals through skin contact (Maroni et al., 1981; Fishbein, 1974). However, the data quantifying the contribution of a dermal exposure to PCBs in an occupational environment or in recreational waters are scant in the literature.
Jan and Tratnik (1988) studied the effects on members of the population living in the vicinity of (<1 km from the river; Group A) and away (1 - 3 km from the river; Group B) from the Krupa River (Slovenia, Yugoslavia) contaminated with PCBs (0.3 µg/L). They concluded that dermal exposure from bathing and clothing washed in the river water was the primary cause of high PCB levels in the blood of the Group A population (PCBs are trapped on the fibres of underwear during washing, and the underwear acts as a transfer agent for PCBs between the water and skin). Twenty-five months after ceasing to use the river for bathing and washing, the PCB levels declined in human blood from 247 to 15 ng/g (mean of three samples) and in human skin fat from 295 to 12 µg/g (mean of two samples). The PCB concentration in fish caught from the Krupa River was 117 µg/g, but the residents of the area did not eat fish from the river.
In examining the health and PCB levels in the blood of electrical workers, Maroni et al. (1981) found that mean PCB (trichlorobiphenyl) concentrations were 215 ng/g (range 77 - 407 ng/g) in the workers with abnormal liver findings and 92 ng/g (range 13 - 345 ng/g) in those without abnormal liver findings. Based on these data, one would expect ill effects in some residents near the Krupa River (see above). However, note that evaluation of hepatic findings (i.e., abnormal liver findings) in the Maroni study were complicated by: (a) the small number of individuals showing hepatic abnormality (16 cases out of 80), (b) lack of association between severity of the hepatic effects and duration of exposure, and (c) unrelated health problems that may have contributed to the hepatic effects in three of the workers (US PHS, 1989).
Other concerns for PCBs in waters used for recreational purposes are expected to be the same as those for drinking water.
11.2 Criteria from the Literature
The criteria of 0.1 µg/L PCBs and 0.001 µg/L PCBs for recreational water were recommended by the Province of Quebec in Canada and the State of Indiana in U.S.A., respectively (Trépanier, 1984; IJC, 1985). Criteria from other jurisdictions, including the CCREM, were not found in the literature.
The criterion of 0.001 µg PCBs/L for recreational waters recommended by the State of Indiana pertains to providing protection for fish-eating birds, rather than humans swimming in it. The recreational water criterion of 0.1 µg PCBs/L quoted for Quebec (Trépanier, 1984) is out-dated; currently, a PCB criterion for recreational waters has not been recommended by Quebec.
11.3 Recommended Criteria
Criteria for PCBs in waters used for recreational purposes are not recommended at this time.
11.4 Rationale
Criteria for PCBs in waters used for recreational activities are not recommended in this document primarily for the lack of pertinent information.
In practice, the PCB criterion recommended for the protection of aquatic life (0.1 ng/L) would also apply to waters used for recreation.