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At least 19 recordsLinked to original sources

The relationship of Chironomus riparius larval Se body burden and body concentration to larval dry mass and effects on sensitivity to selenium.

Selenium as selenite was added to laboratory cultures of Chironomus riparius. In two sets of cultures, substrate-bound Se concentrations were typically 10(3) times dissolved Se concentrations, while in the other set dissolved Se concentrations were about 10 to 50 times substrate-bound Se concentrations. Body burdens of individual second-, third-, and fourth-instar larvae and eviscerated fourth-instar larvae were measured. Regressions of Se body burden on larval dry mass found evidence for separate intercepts but common slopes for each instar, and Se body concentrations were diluted by growth. The derivation of body concentration from body burden as a function of larval dry mass was used to derive a model of body burden and body concentration as a function of instar. Toxicity tests were performed to check for a change in sensitivity to Se as a function of culture Se concentration. Larval Se concentrations were highly correlated with dissolved Se concentrations but not with substrate-bound Se concentrations. Increases in Se in substrate caused no sensitization, while increases in dissolved Se caused desensitization. We concluded that covariates such as larval dry mass should be incorporated when deriving water quality criteria.

Animals↗

Systemic burden and body burden of Pu in man: comparison of results from bioassay and autopsy.

A case of plutonium deposition in man within the range of 190 Bq by inhalation from about 12 yr ago is reported. An estimate of systemic burden was made based on analyses of urine and faeces and the models of Langham, Beach/Dolphin, and Durbin while the individual was alive. This estimate was compared with autopsy findings (spleen, thyroid, blood, lung, pulmonary and tracheobronchial lymph nodes, liver, skeleton). According to autopsy findings, the systemic burden (mainly liver and skeleton) had been overestimated by a factor of 11-16, the body burden (whole body) by a factor of 6-9.

Body Burden↗

Comparisons of estimated human body burdens of dioxinlike chemicals and TCDD body burdens in experimentally exposed animals.

Humans are exposed to mixtures of polyhalogenated aromatic hydrocarbons, and the potential health effects of these exposures are uncertain. A subset of this class of compounds produce similar spectra of toxicity in experimental animals as does 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD), and these chemicals have been classified as "dioxins." In this study, we compared the body burdens of dioxins that produce effects in experimental animals to body burdens associated with these effects in humans. Human body burdens were estimated from lipid-adjusted serum concentrations of dioxins, assuming dioxins are equally distributed in body fat and an adult has 22% body fat. The toxic equivalency factor (TEF) method was used to calculate body burdens of dioxins in humans. These calculations included dibenzo-p-dioxins, dibenzofurans, and polychlorinated biphenyls. In the general population, average background concentrations were estimated at 58 ng TCDD equivalents (TEQ)/kg serum lipid, corresponding to a body burden of 13 ng TEQ/kg body weight. Populations with known exposure to dioxins have body burdens of 96-7,000 ng TEQ/kg body weight. For effects that have been clearly associated with dioxins, such as chloracne and induction of CYP1A1, humans and animals respond at similar body burdens. Induction of cancer in animals occurs at body burdens of 944-137,000 ng TCDD/kg body weight, while noncancer effects in animals occur at body burdens of 10-12,500 ng/kg. Available human data suggest that some individuals may respond to dioxin exposures with cancer and noncancer effects at body burdens within one to two orders of magnitude of those in the general population.

Animals↗

Impact of environmental cadmium pollution on cadmium exposure and body burden.

The body burden of cadmium, as estimated from 24-h urine cadmium levels, was determined in 1,523 subjects who were not occupationally exposed and who lived in five areas of Belgium. Urinary cadmium levels differed significantly with place of residence. These differences persisted after standardization for the other significant determinants (i.e., age, body mass index, smoking habits, social class, alcohol consumption, and menopause). The highest 24-h urine cadmium levels were found in subjects who lived in areas that contained cadmium-polluted soils. The body burden overload has been attributed mainly to the consumption of locally grown vegetables and the use of contaminated well water for cooking and drinking. Blood cadmium levels were also dependent on place of residence. However, the geographical differences in blood cadmium did not parallel those of urine cadmium. Blood cadmium is more influenced by recent exposure; therefore, this latter observation might reflect the recent implementation of preventive measures in some areas.

Adolescent↗

The use of comparative 137Cs body burden estimates from environmental data/models and whole body counting to evaluate diet models for the ingestion pathway.

Rongelap and Utirik Atolls were contaminated on 1 March 1954, by a U.S. nuclear test at Bikini Atoll code named BRAVO. The people at both atolls were removed from their atolls in the first few days after the detonation and were returned to their atolls at different times. Detailed studies have been carried out over the years by Lawrence Livermore National Laboratory (LLNL) to determine the radiological conditions at the atolls and estimate the doses to the populations. The contribution of each exposure pathway and radionuclide have been evaluated. All dose assessments show that the major potential contribution to the estimated dose is 137Cs uptake via the terrestrial food chain. Brookhaven National Laboratory (BNL) has carried out an extensive whole body counting program at both atolls over several years to directly measure the 137Cs body burden. Here we compare the estimates of the body burdens from the LLNL environmental method with body burdens measured by the BNL whole body counting method. The combination of the results from both methods is used to evaluate proposed diet models to establish more realistic dose assessments. Very good agreement is achieved between the two methods with a diet model that includes both local and imported foods. Other diet models greatly overestimate the body burdens (i.e., dose) observed by whole body counting. The upper 95% confidence limit of interindividual variability around the population mean value based on the environmental method is similar to that calculated from direct measurement by whole body counting. Moreover, the uncertainty in the population mean value based on the environmental method is in very good agreement with the whole body counting data. This provides additional confidence in extrapolating the estimated doses calculated by the environmental method to other islands and atolls.

Body Burden↗

Uncertainties in estimated body burdens of caesium-137 by whole-body counting.

It is very important to evaluate the uncertainties in individual monitoring for internal exposure of workers. The uncertainties in estimated body burdens of 137Cs with the JAERI whole-body counter were investigated using Monte Carlo simulation and measurements. It was found that the uncertainties of estimated body burdens with the whole-body counter are strongly dependent on various sources of uncertainty, such as radioactivity distribution within the body and counting statistics and that the 137Cs body burden assessed from the result of the whole-body count can be within +/- 60% in error.

Adolescent↗

Evaluation of uncertainties in 90Sr-body-burdens obtained by whole-body count: application of Bayes' rule to derive detection limits by analysis of a posteriori data.

A whole body counter (WBC) designed to measure bremsstrahlung from 90Y, the short-lived daughter of 90Sr, has been used since 1974 to measure 90Sr-body burdens in residents along the Techa River, which was contaminated by releases from the Mayak Production Association. Bayes' rule has been applied to the a posteriori WBC data in order to derive the uncertainties associated with the data: The lower limit of reliable detection is 2.0 kBq and the uncertainty of routine measurements is 1.6 kBq.

Bayes Theorem↗

Body burden of cadmium in man at low level of exposure.

Specimens of heart, kidney, liver, lung, pancreas and skeletal muscle were collected at autopsy from 86 traumatic accident victims. The concentration of cadmium in the samples was determined by atomic absorption spectrophotometry. Tissue burdens and the body burden of cadmium were calculated using individual weights of different organs as a function of age. Total body burden reached its maximum level of approximately 8 mg, in the 30-39 year age group. The highest value (8.3 mg) was measured in the 40-49 year age group. The highest average value of tissue burdens at 40-49 years of age was in kidney (4.9 mg), the amount of cadmium diminishing in different tissues in the following order: liver (1.8 mg), muscle (0.15 mg), lung (0.09 mg), pancreas (0.06 mg) and heart (less than 0.01 mg). At a low level of exposure, kidneys and liver alone contain on an average 85% of the total body burden of cadmium. This value differs greatly from earlier reported figures of 45-50%.

Adolescent↗

Lessons from the polybrominated diphenyl ethers (PBDEs): precautionary principle, primary prevention, and the value of community-based body-burden monitoring using breast milk.

Levels of chemicals in humans (body burdens) are useful indicators of environmental quality and of community health. Chemical body burdens are easily monitored using breast milk samples collected from first-time mothers (primiparae) with infants 2-8 weeks of age. Currently, there is no body-burden monitoring program using breast milk in the United States, although ad hoc systems operate successfully in several European countries. In this article we describe the value of such monitoring and important considerations of how it might be accomplished, drawing from our experiences with pilot monitoring projects. Breast milk has several advantages as a sampling matrix: It is simple and noninvasive, with samples collected by the mother. It monitors body burdens in reproductive-age women and it estimates in utero and nursing-infant exposures, all important to community health. Time-trend data from breast milk monitoring serve as a warning system that identifies chemicals whose body burdens and human exposures are increasing. Time trends also serve as a report card on how well past regulatory actions have reduced environmental chemical exposures. Body-burden monitoring using breast milk should include educational programs that encourage breast-feeding. Finally, and most important, clean breast milk matters to people and leads to primary prevention--the limiting of chemical exposures. We illustrate these advantages with polybrominated diphenyl ethers (PBDEs), a formerly obscure group of brominated flame retardants that rose to prominence and were regulated in Sweden when residue levels were found to be rapidly increasing in breast milk. A community-based body-burden monitoring program using breast milk could be set up in the United States in collaboration with the Special Supplemental Nutrition Program for Women, Infants, and Children (WIC). WIC has a large number of lactating first-time mothers: It has 6,000 clinics nationwide and serves almost half (47%) the infants born in the United States. Educational programs (e.g., those run by WIC) are needed that encourage breast-feeding, especially in lower-income communities where breast-feeding rates are low and where breast-feeding may help protect the infant from the effects of environmental chemical exposures. Education is also needed about reducing chemical body burdens. A body-burden monitoring program would provide valuable data on time trends, background levels, and community hot spots in need of mitigation and follow-up health studies; develop analytic methods for new chemicals of concern; and archive breast milk samples for future analyses of other agents.

Aid to Families with Dependent Children↗

Cadmium body burden of an occupationally non burdened population in southern Bavaria (FRG).

The cadmium body burden of the occupationally non-burdened population in the southern Bavarian area was estimated from the cadmium concentrations in liver and renal cortex, determined by ET-AAS of 263 autopsy cases. A mean value of 17.9 mg cadmium was calculated for all cases and 21.9 mg cadmium for all adults. The body burdens found do not depend on sex but greatly on smoking habits. Mean values for non-smokers are 13.5 mg, for moderate smokers 22.5 mg and for heavy smokers 33.2 mg. The dependence on age is similar to that of the cadmium concentration in the kidney cortex: an increase up to an age of approximately 50 years and a decrease at higher ages. Between the average value we found and the critical body burden calculated by Roels et al. (1983) is a safety factor of 8 to 10, but in some of our cases of middle-aged, heavy smokers this safety factor drops to a value lower than 1. It is concluded that it seems to be imperative to control the further trend of the cadmium body burden in occupationally non-burdened populations.

Adolescent↗

Determination of body burden of uremic toxins.

The body burden of two uremic toxins, di- and trimethylamines, was determined in eight chronic renal failure patients, who received a renal transplant with immediate good function. The "pools" of these amines were calculated on the basis of serum concentration just prior to vascular anastomosis being established and compared to measured amines excreted over a period of five days following transplantation. The amount of DMA and TMA present intra-cellularly in eight muscle samples obtained from these patients was also studied. Both the measured to calculated ratios and intracellular to extracellular ratios of these amine concentrations suggests significant intracellular sequestration in end-stage renal disease. The possible effect on the intracellular milieu is discussed. Serum concentration of these uremic toxins under-estimates the total body burden.

Adolescent↗

Influence of body iron store status and cigarette smoking on cadmium body burden of healthy Thai women and men.

The influence of cigarette smoking, body iron store status and gender on cadmium (Cd) body burden was examined in a group of 197 healthy Thais with overall mean age of 30.5 year (19-47 year). The lowest, geometric mean, and the highest urinary Cd excretion rate was 0.04, 0.46 and 3.84 microg/g creatinine, respectively. The prevalence of low iron stores (serum ferritin <20 microg/l) was 16% and 2% in women and men, respectively. All women (n = 99) were non-smokers, but they had the same Cd body burden as did men (n = 47) who on average smoked 8.7 cigarettes per day for 9 years. These women and men had 1.9-fold greater body Cd burden than did non-smoking men (t = 4, P < 0.001). In addition, the women Cd body burden was found to be inversely correlated with serum ferritin (r = -0.39, P < 0.001) and those with low iron stores showed a 3.4-fold greater Cd body burden than did women whose serum ferritin being between 101 and 200 microg/l (F = 6.2, P = 0.003, one-way ANOVA). In contrast, men's Cd body burden did not show a significant correlation with serum ferritin, but it did show a positive correlation with cumulative cigarette smoking index (r = 0.29, P = 0.02). Thus, iron status and cigarette smoking were found to be determinants of Cd body burden in young adult Thai women and men.

Adult↗

Polychlorinated biphenyls (PCBs) in the UK population: estimated intake, exposure and body burden.

This paper presents a detailed congener-specific estimate of PCB exposure to the UK population. The average sigma PCB intake (i.e. the sum of IUPAC congeners No. 28, 44, 52, 61/74, 66, 99, 101, 105, 110, 118, 138, 151, 153, 156, 170, 180, 183, 187, 189, 194/205, 201, 202, 206 and 209) for the contemporary UK population was estimated to be 0.53 micrograms/person/day. Food consumption accounted for 97% of the sigma PCB exposure, with fish, milk and dairy products, vegetables and meat and animal fat accounting for 32, 24, 24 and 15%, respectively. The congener pattern for different food products varied, with vegetables playing a major part in the intake of lower chlorinated compounds, whilst fatty foods such as fish, dairy products and meat, were of greater importance for the intake of higher chlorinated compounds. Theoretical body burdens and body fat concentrations of selected PCB congeners were derived for the UK population, based on the estimated contemporary human daily intake of PCBs and a number of assumptions. PCB body burdens and adipose tissue concentrations were generally predicted to increase with age. However, adipose concentrations increased at a slower rate in the older population, due to a dilution effect caused by the increase in body fat weight with age. These theoretical estimates were then compared with measured values for adipose tissue from the Welsh population. Theoretical body burdens and adipose tissue concentrations (not accounting for any metabolic losses) were below the actual values measured for the contemporary Welsh population by between a factor of 2.5 and 4. This discrepancy becomes greater when metabolic losses are included, and probably occurs because present day exposure to PCBs through foodstuffs is likely to be lower than in the past. The lower chlorinated congener No. 28 is more readily removed from the body and is predicted to reach an equilibrium concentration in humans. In contrast, the higher chlorinated No. 153 was predicted to accumulate in the body throughout life. The effect of PCB transfer via breast milk is shown to be important in lowering the body burden of the mother (by approximately 20% over 3 months) and substantially increasing that in the offspring.

Adipose Tissue↗

Biological and physical factors affecting the body burden of organic contaminants in freshwater mussels.

Biological and physical factors affecting the body burdens of hexachlorobenzene, octachlorostyrene, and four polychlorobiphenyl (PCB) congeners in freshwater mussels from Lake St. Clair, Ontario, Canada were investigated. Specimens of Lampsilis radiata (Barnes) and the non-native Elliptio complanata (Lightfoot) were deployed for forty days at four Lake St. Clair sites, to investigate whether the water or the sediment phase represented the primary source of contaminants and to examine the effect of enclosure of the mussels on contaminant uptake. No significant differences in body burdens were detected for any of the compounds between mussels placed in corrals containing uncontaminated sand and those with natural sediment, suggesting the water phase represents the xenobiotic source. Among three enclosure types of varying restriction there were no significant differences in the body burden of each compound indicating the effect of confinement on uptake is minimal. Weak negative correlations between body burden and body length existed for all compounds, although there were no significant differences between the sexes or, with the exception of PCB congener 118, among five indigenous species.

Animals↗

Factors influencing the cadmium body burden in a population study.

The cadmium body burden, as estimated from 24-h urinary cadmium (Cd-U), was determined in 1523 non-occupationally exposed subjects living in five areas of Belgium. It increased with age until 55-65 years in both sexes and thereafter decreased slightly. It was higher in smokers but was inversely associated with alcohol consumption and social class. In men only, it was also positively correlated with body mass index. After the menopause, women showed a significant increase in 24-h Cd-U independently of the other factors. In addition, the cadmium body burden was independently associated with place of residence in both sexes. Highest levels of Cd-U were found in subjects living in an area with soils heavily polluted by cadmium.

Adolescent↗

Uncertainties in predicted radionuclide body burdens and doses from discrete stochastic source terms.

Expressions are derived in three cases for the expectation and uncertainty of body burdens and doses calculated from a linear model of environmental transport and human metabolism in terms of expectation and uncertainty in inputs of discrete, stochastic random variables. Three cases are compared to determine the relationship of the expectations and uncertainties under varying assumptions. In the constant input case, the input is selected randomly at the outset of the simulation period [O,T] from the distribution to which the population is exposed and then is held constant throughout [O,T]. In the two time-varying cases, random and autoregressive, it was assumed that N discrete stochastic exposures to the input were made uncorrelated and partially correlated, respectively. Each exposure was constant during each time interval of length T/N. The expectation values of the body burdens and doses in the constant input case were identical to those in the random case and the autoregressive cases for stationary inputs. The uncertainties of the body burdens and the doses in the constant input case were identical in the limit of rapid metabolism to those of the random case and the autoregressive cases for stationary inputs. In the limit of slow metabolism, the uncertainties of the body burdens and the doses in the constant input case were N1/2 and (3N/4)1/2, respectively, greater than those in the random case and were ((1 + alpha)/[(1 - alpha)N])1/2 and (4(1 + alpha)/[3(1 - alpha)N])1/2, respectively, greater than those in the autoregressive case for stationary inputs and autocorrelation coefficient alpha. That is, increasing the number of sampling periods decreases the uncertainty and increasing the autocorrelation increases the uncertainty. In an example application for ingestion of 137Cs at Bikini Island, a weak form of both slow and rapid metabolism limits apply and give the result that the uncertainty of the body burden in the constant input case is 18 times greater than the random case. For alpha = 0.5, the uncertainty of the body burden in the autoregressive case is 1.7 times greater than the random case. The smooth transition of the autoregressive case from the random case to the constant input case is shown as alpha increases from 0 (random) to 1 (constant).

Adolescent↗