To determine MeHg and THg exposure via drinking water, inhalation, and food consumption, we calculated PDI values for the general adult population according to the following formula:
where PDI is given in micrograms per kilogram of body weight (bw) per day; bw = 60 kg; C is the concentration of exposed medium; IR is intake rate (or ingestion rate or inhalation rate), and i = intake of air, water, rice, fish, vegetable, corn, meat, and poultry.
This calculation is based on the assumption that MeHg exposure from other routes [i.e., ambient atmosphere (Gnamus et al. 2000 ; WHO 1990 ); dental amalgam fillings (Barregard et al. 1995 (link); Batista et al. 1996 (link)); other foods (i.e., food oil, salt, beverage such as milk) (Cheng et al. 2009 (link)); and dermal exposure (U.S. EPA 1997 ; WHO 2003 )] is negligible.
The intake rates for different exposure media for the adult populations used were based on the Guizhou Statistical Yearbook reported by BGS (2007) (Table 2 ).
To better relate the different characteristics of Hg exposure in the population in inland China who consume a a rice-based diet with those of a population who consume more fish in their diet, we used two typical regions with high fish consumption for comparison: a Japanese population of rural, coastal women (Iwasaki et al. 2003 (link)), and a reference group of the general Norwegian population (Mangerud 2005 ). We also compared the MeHg exposure in the present study with the MeHg exposure assessment of women in the U.S. general population (Carrington and Bolger 2002 (link); Mahaffey et al. 2004 (link)). These calculations were based on the assumption that each adult’s body weight was 60 kg for the Guizhou population and for U.S. women, 55 kg for Japanese women, and 70 kg for the Norwegian population.
where PDI is given in micrograms per kilogram of body weight (bw) per day; bw = 60 kg; C is the concentration of exposed medium; IR is intake rate (or ingestion rate or inhalation rate), and i = intake of air, water, rice, fish, vegetable, corn, meat, and poultry.
This calculation is based on the assumption that MeHg exposure from other routes [i.e., ambient atmosphere (Gnamus et al. 2000 ; WHO 1990 ); dental amalgam fillings (Barregard et al. 1995 (link); Batista et al. 1996 (link)); other foods (i.e., food oil, salt, beverage such as milk) (Cheng et al. 2009 (link)); and dermal exposure (U.S. EPA 1997 ; WHO 2003 )] is negligible.
The intake rates for different exposure media for the adult populations used were based on the Guizhou Statistical Yearbook reported by BGS (2007) (
To better relate the different characteristics of Hg exposure in the population in inland China who consume a a rice-based diet with those of a population who consume more fish in their diet, we used two typical regions with high fish consumption for comparison: a Japanese population of rural, coastal women (Iwasaki et al. 2003 (link)), and a reference group of the general Norwegian population (Mangerud 2005 ). We also compared the MeHg exposure in the present study with the MeHg exposure assessment of women in the U.S. general population (Carrington and Bolger 2002 (link); Mahaffey et al. 2004 (link)). These calculations were based on the assumption that each adult’s body weight was 60 kg for the Guizhou population and for U.S. women, 55 kg for Japanese women, and 70 kg for the Norwegian population.
Free full text: Click here
