Polybrominated diphenyl ethers (PBDE) are used in high amounts as flame retardants in plastic materials and textiles. Due to their persistence, their accumulation in the food chain and their toxic properties they have been integrated in the human biomonitoring program of the Baden-Württemberg State Health Office since 2002. In repeated cross-sectional studies in winter 2002/03 (n=162), 2004/05 (n=194), 2005/06 (n=411) and 2008/09 (n=770) blood samples of 9-11-year-old pupils were taken, pooled and analysed for PBDE after extraction and purification by silica gel using HRGC/HRMS. Samples were pooled according to region, gender, and breast feeding. PBDE in the pooled samples ranged from 1.9 to 12.5 ng/g blood fat (sum of all PBDE). Mean concentrations of PBDE, calculated for the four investigation periods, were 6.2 ng/g (2002/03), 5.4 ng/g (2004/05), 7.8 ng/g (2005/06) and 6.7 ng/g (2008/09). While the concentration of the decabrominated diphenyl ether (BDE-209) increased, the concentration of other congeners (BDE-47, BDE-99, BDE-100, BDE-153, BDE-154, BDE-183) decreased slightly or remained at the same level. Consistent differences with respect to gender and breast-feeding were not recognizable. Concentrations of PBDE in children range on the same level as in adults and do not seem to be critical from the toxicological point of view. Because of the slight increase of BDE 209, the internal concentrations of BDE should be monitored in the future. The strong variations in PBDE concentration between the different pooled samples indicate that, apart from ingestion, other routes of exposure (dermal, inhalation) and additional sources (textiles, building materials) must be taken into consideration.

The present study shows the results of investigations for the daily intake of DEHP of three groups of test subjects living in different DEHP burdened housings. The daily intake of DEHP was calculated on the basis of the concentration of the sum of the DEHP metabolites MEHP, 4-OH-MEHP, 5-OH-MEHP, 5-Oxo-MEHP and 5-Carboxy-MEPP in morning urine. This calculated daily intakes were compared to the DEHP concentrations in house dust and indoor air. For a first group of test subjects, six test persons aged between 4 and 58 years, the concentrations of the DEHP metabolites were determined. The results showed substantial daily variations of the concentration of the DEHP metabolites and thus widely varying DEHP intakes. Within the test period five single incidents were detected with daily intakes of more than 2,500 mu g DEHP. The two other groups of test persons had been pupils of two different boarding schools. Boarding school A showed several floorings which could be identified as large-area DEHP sources. Wheras boarding school B showed only few large-area DEHP sources. Based on the calculated daily DEHP-intake and the German conventions for the intake of house dust and indoor air in average less than 5 % of the daily DEHP intake can be attributed to house dust and indoor air. The present data show no correlation of DEHP-metabiltes with the DEHP in house dust. The present results also gave hints that a cumulative enrichment of DEHP is not probable.

The paper presents the results of Polybrominated Diphenyl Ethers (PBDE) in house dust in comparison with blood. The participants of the biomonitoring investigations are living in one of 111 flats, where samples of house dust were collected. The concentrations of PBDE in the blood samples of 15 persons living in various flats with higher PBDE-concentrations in house dust (PBDE in average 7,500 mg/kg) are compared to the concentration of PBDE in blood samples of 12 test persons living in houses with low PBDE-concentrations in house dust (in average 150 mg/kg). The results prove that neither the total PBDE-concentration (sum of eight PBDE-congeners) nor the pattern of the PBDE-congeners gives any hint for a relation between the concentration of PBDE in house dust and blood. In both collectives test persons with low (< 2 pg PBDE/g blood fat) and high PBDE-contents (> 10 pg PBDE/g blood fat) in blood are to be found. The pattern of the PBDE-congeners in blood differs substantially from the pattern of DBPE in house dust. Main- or lead-congener in house dust, with a portion of about 90%, is PBDE 209. Only in few samples PBDE 47, PBDE 153 can be detected in relevant portions of the total PBDE-content. In blood usually other PBDE congeners like PBDE 47, PBDE 153 are dominating besides PBDE 209. The PBDE-pattern in blood shows no difference between test persons living in housings with either higher or lower PBDE-concentrations in house dust.

Although PCB and PCB-containing materials are not processed for a long time, PCB is under discussion again and again caused by the pollution of indoor environments. To objectify the discussion, the dates of the PCB-biomonitoring, the organochlorine-compounds (DDE, HCB, &beta;-/&gamma; -HCH, PCDD/PCDF) and the polybrominated biphenyl ethers concerning the investigations within the project "Sentinel Health Departments" in Baden-Wurttemberg are represented. Additionally results from children from Kazakhstan (Aral-Sea area) and from teachers which are working in PCB polluted schools as well as from a long term investigated test person are reported. Blood concentrations of the following compounds decreased from 1996/97 to 2002/03: the sum of the concentration of PCB 138,153 and 180 decreased from 0,46 &mu; g/L to 0,20 &mu; g/L, DDE from 0,32 &mu; g/L to 0,17 &mu; g/, HCB from 0,20 &mu; g/L to 0,08 &mu; g/L, &beta;-HCH below the level of detection, I-TEQ NATO to 4,8 pg/g blood fat, TEQWHO (without PCB) to 5,5 pg/g blood fat, PCB 126 to 18,8,pg/g blood fat and PCB 169 to 12,8 pg/g blood fat. The influence of breast feeding and the gender on the level of the pollution is conspicious. No local correlations were found in Baden-Wurttemberg, but they were found in comparison with the results of Kazakhstan (Aral-Sea area). The difficulty to produce time series while the analyzing pollutants are more and more decreasing, as well as the change of the calculation base of the summation of parameters like I-TEQ NATO to TEQ WHO are discussed.

Although PCB and PCB-containing materials are not processed for a long time, PCB is under discussion again and again caused by the pollution of indoor environments. To objectify the discussion, the dates of the PCB-biomonitoring, the organochlorine-compounds (DDE, HCB, beta-/gamma -HCH, PCDD/PCDF) and the polybrominated biphenyl ethers concerning the investigations within the project "Sentinel Health Departments" in Baden-Wurttemberg are represented. Additionally results from children from Kazakhstan (Aral-Sea area) and from teachers which are working in PCB polluted schools as well as from a long term investigated test person are reported. Blood concentrations of the following compounds decreased from 1996/97 to 2002/03: the sum of the concentration of PCB 138,153 and 180 decreased from 0.46 microg/L to 0.20 microg/L, DDE from 0.32 microg/L to 0.17 microg/, HCB from 0.20 microg/L to 0.08 microg/L, beta-HCH below the level of detection, I-TEQ NATO to 4.8 pg/g blood fat, TEQ WHO (without PCB) to 5.5 pg/g blood fat, PCB 126 to 18,8,pg/g blood fat and PCB 169 to 12.8 pg/g blood fat. The influence of breast feeding and the gender on the level of the pollution is conspicious. No local correlations were found in Baden-Wurttemberg, but they were found in comparison with the results of Kazakhstan (Aral-Sea area). The difficulty to produce time series while the analyzing pollutants are more and more decreasing, as well as the change of the calculation base of the summation of parameters like I-TEQ NATO to TEQ WHO are discussed.