Dioxin concentration in milk and tissues of cows and sheep related to feed and soil contamination.

If cows or sheep are grazing on areas known for a higher dioxin level of the soil, respectively, dry cows are fed with feedstuffs produced on such areas, the dioxin concentration in food, in this case in cows' milk and livers of sheep could reach or exceed maximum levels. Furthermore large amounts of polychlorinated dibenzo-p-dioxins/polychlorinated dibenzo-p-furans (PCDD/F) can be excreted with the faeces. But there are chances for farmers to prevent or at least to minimize the dioxin load of feed and with it of food (including the harvesting technique and the feeding strategy).

PCDDs/PCDFs, PCBs, and organochlorine pesticides in eggs of Eurasian sparrowhawks (Accipiter nisus), hobbies (Falco subbuteo), and northern goshawks (Accipiter gentilis) collected in the area of Berlin-Brandenburg, Germany.

Concentrations of polychlorinated dibenzo-p-dioxins (PCDDs), polychlorinated dibenzofurans (PCDFs), polychlorinated biphenyls (PCBs), and organochlorine (OC) pesticides were measured in unsuccessfully hatched eggs of three different kinds of predatory birds: 3 eggs of sparrowhawks, 7 eggs of hobbies, and 16 eggs of goshawks collected in the German region of Berlin-Brandenburg. Using toxic equivalency factors for birds, eggs of hobbies contained mean concentrations of 478 pg TEQ/g fat and 551 pg TEQ/g fat contributed by PCDD/Fs and coplanar PCBs, respectively. For sparrowhawks the respective TCDD equivalents were 424 and 1278 pg/g fat; those for goshawks were 211 and 935 pg/g fat. The mean value of the summed concentrations of the PCB congeners 28, 52, 101, 138, 153, and 180 amounted to 11 microg/g fat in eggs of hobbies, 9.5 microg/g fat for sparrowhawks, and 16.1 microg/g fat for goshawks. Of the analyzed organochlorine pesticides the concentration of p,p'-DDE was highest (up to 273 microg/g); the concentration of the other OCs, with the exception of methoxychlor in eggs of goshawks (highest level of 10.6 microg/g fat), were negligible. In all cases the calculated toxicity of the coplanar PCBs surpassed the toxicity of the PCDD/Fs, at least by a factor of two. Due to the higher concentration of the coplanar PCB 77 compared to PCB 126 in eggs of hobbies, it is concluded that its metabolic excretion in this species is much lower than in sparrowhawks and goshawks.

Results of an "emergency quality control study" as confirmation of a PCDD/PCDF-contamination of milk and butter samples.

Elevated PCDD/F levels in four butter samples and one milk sample had to be confirmed under considerable time pressure. These samples should demonstrate a raising dioxin contamination in different regions of Germany caused by the use of Brazilian citrus pulp as feedstuff. Above all, the increase of 2,3,7,8-TCDD and 1,2,3,7,8-PeCDD had to be confirmed. Thus, an "emergency quality control study" was performed including five laboratories from the official food control in Germany. The results had to be reported about two to three weeks after the first announcement of the samples (including time for shipment). The five laboratories applied different extraction and clean-up methods, used different GC-columns and GC/MS-equipment and different standard solutions. The results are in a good agreement. Slightly different results for most individual congeners were of minor importance. A difference was observed only in the 2,3,7,8-TCDF content of one laboratory which was not relevant for the evaluation of the increase of the dioxin contamination in milk and dairy products. The laboratory's individual methods proved to give correct results even under a very tight schedule.

PCDDs/PCDFs and coplanar PCBs in eels (Anguilla anguilla) from different areas of the rivers Havel and Oder in the state of Brandenburg (Germany).

In 1996 forty-nine eels were caught from different locations along the rivers Oder (Hohenwutzen and Schwedt) and from 11 locations along the Havel river. They were analysed for PCDDs/PCDFs and the coplanar PCBs (PCB 77, PCB 126, PCB 169). Their contribution to 2,3,7,8-TCDD equivalents were estimated. In case of PCDDs/PCDFs these amounted between 1.8 and 15.2 pg/g fat (mean 6.1 pg/g; median 5.2 pg/g), in case of coplanar PCBs between 2.4 and 170.5 pg/g fat (mean 47.7 pg/g; median 36.1 pg/g). Lakes which are associated with but not directly located at the main stream of the river Havel contributed much less to contamination of the eels than the river segments situated in the more urbanised or industrialised sites along the main river.

Assessment of biological activities of mixtures of polychlorinated dibenzo-p-dioxins (PCDDs) and their constituents in human HepG2 cells.

Dose-response curves of the induction of P4501A1-dependent 7-ethoxyresorufin O-deethylase (EROD) were analyzed in human hepatoma HepG2 cells treated with defined mixtures of polychlorinated dibenzo-p-dioxins (PCDDs) and their 2,3,7,8-substituted constituents, similar to previous studies with rat hepatocytes and H4IIE cells (Schrenk et al. 1991). PCDDs appear to act less potent in human HepG2 cells in comparison with rat cells. For example, EC50 values of 2,3,7,8-Cl4DD were 8-fold and 19-fold higher than in rat H4IIE cells and hepatocytes, respectively. EC50 values of PCDDs were compared with that of 2,3,7,8-Cl4DD and expressed as 2,3,7,8-Cl4DD equivalents (TEs). Although the rank order of PCDD potencies was similar, TEs for some PCDDs (1,2,3,7,8-Cl5DD; TE = 0.75 and 1,2,3,7,8-Cl6DD; TE = 0.61) were found to be higher than in the rat system. In contrast to rat cells no significant induction of EROD could be detected with Cl8DD in HepG2 cells up to its limit of solubility. Experimentally determined TEs of PCDD mixtures containing 49 constituents were found to be largely due to additive effects of their 2,3,7,8-substituted constituents.

Assessment of biological activities of mixtures of polychlorinated dibenzo-p-dioxins: comparison between defined mixtures and their constituents.

As a first step to assess biological activities of complex mixtures of polychlorinated dibenzo-p-dioxins (PCDDs), induction of 7-ethoxyresorufin O-deethylase (EROD) by defined mixtures and their constituents has been analysed in vitro. Two cell systems have been compared: primary hepatocyte cultures and hepatoma H4IIE cells. EC50 values of PCDDs were compared with that of the most potent compound, 2,3,7,8-Cl4DD (2,3,7,8-tetrachlorodibenzo-p-dioxin) and expressed as 2,3,7,8-Cl4DD equivalents (TEs). TEs for three defined mixtures containing up to 49 PCDDs could be predicted from the sum of TEs for the 2,3,7,8-substituted congeners. Efficacies (maximal enzyme induction) of less potent PCDDs (1,2,3,4-Cl4DD, Cl8DD and of a mixture containing 86% Cl8DD and of benz(a)anthracene were lower in hepatocytes (by 33%) and in H4IIE cells (by 50%). The results suggest that biological activities of complex PCDD mixtures are largely due to additive effects of their 2,3,7,8-substituted constituents.

Persistence of various polychlorinated dibenzo-p-dioxins and dibenzofurans (PCDDs and PCDFs) in hepatic and adipose tissue of marmoset monkeys.

A defined mixture of polychlorinated dibenzo-p-dioxins and dibenzofurans (PCDDs and PCDFs) was subcutaneously administered to marmoset monkeys (Callithrix jacchus). Tissue concentrations in hepatic and adipose tissue were measured at different times after treatment (1-28 weeks). One week after application high concentrations could be detected for the 2,3,7,8-substituted congeners only. The percent of the administered dose in whole liver differed for the various 2,3,7,8-substituted congeners, ranging from 24.5 +/- 4.5% for 2,3,7,8-TCDD to 74.1 +/- 4.9% for 2,3,4,6,7,8-H6CDF. Therefore, the concentration ratio (liver/adipose tissue) was also very different, ranging from about 1 (2,3,7,8-T4CDD or 2,3,7,8-T4CDF) to greater than 10 in the case of some higher chlorinated PCDDs and PCDFs. Half-lives of PCDDs and PCDFs were very different for the various 2,3,7,8-substituted congeners. For the most toxic compound (2,3,7,8-T4CDD) a t/2 of about 8 weeks in hepatic tissue and about 11 weeks in adipose tissue was found when calculated from data obtained later than 6 weeks after injection. For 2,3,7,8-T4CDD and 1,2,3,7,8-P5CDD the decreases in hepatic concentrations were much faster during the first 6 weeks after administration (t/2 of 4 weeks). This was apparently due to redistribution phenomena. Half-life increased with increasing degrees of chlorination. In some cases (e.g. OCDD, OCDF) no significant decrease in tissue concentrations could be observed after 28 weeks. The shortest t/2 was determined for 2,3,7,8-T4CDF: shorter than 6 days in hepatic tissue and about 10 days in adipose tissue. Calculation of the body burden of the non-2,3,7,8-substituted PCDDs/PCDFs 1 week after injection revealed that all groups of isomers were present at less than 5%. Consequences of these findings for the use of TCDD-toxic-equivalency factors are discussed and a change in strategy is suggested.

Transfer of various polychlorinated dibenzo-p-dioxins and dibenzofurans (PCDDs and PCDFs) via placenta and through milk in a marmoset monkey.

A defined mixture of polychlorinated dibenzo-p-dioxins and dibenzofurans (PCDDs and PCDFs) was subcutaneously administered to a pregnant marmoset monkey (Callithrix jacchus) 11 weeks prior to delivery. Transfer of PCDDs and PCDFs via placenta and mother's milk was investigated by measurement of concentrations in a newborn 1 day after birth and in an infant of the same litter after a lactation period of 33 days. Furthermore, comparative measurements were performed in different tissues of the mother at the end of the lactation period, and in addition, in two groups of four adult monkeys each 1 and 6 weeks after treatment. Deposition of the PCDDs and PCDFs into fetal liver was very low for most of the 2,3,7,8-substituted congeners. Highest deposition was observed for 2,3,7,8-T4CDD and 1,2,3,7,8-P5CDD. For all other compounds concentrations in the hepatic tissue of newborn shortly after birth were lower than one tenth of corresponding concentrations in adults. Especially for PCDFs, prenatal deposition in fetal liver was extremely low. Fetal liver is apparently largely unable to accumulate PCDDs/PCDFs. In contrast to liver, concentrations of 2,3,7,8-substituted PCDDs/PCDFs in adipose tissue of the newborn were at least one third of the levels in adults. However, concentrations of OCDD and OCDF were about three times higher in the newborn than in adult adipose tissue. Transfer of some of the 2,3,7,8-substituted PCDDs and PCDFs to the offspring via mother's milk was considerable, leading to hepatic concentrations in the suckled infant at the end of the 33-day nursing period well above corresponding concentrations in the dam. When hepatic concentrations in the infant and dam were compared 2- to 4-fold higher concentrations were found in the infant's liver for 2,3,7,8-T4CDD/F and for 1,2,3,7,8-P5CDD. In the case of the 2,3,7,8-substituted H6CDDs, P5CDFs, and most of the H6CDFs, hepatic concentrations in the infant and dam were in the same range at the end of the suckling period. In contrast to this, less than one tenth the concentration of OCDD was found in the infant's liver when compared with adult liver. A corresponding phenomenon was observed for PCDFs. At the maximum absorption, 1 week after injection, for almost all 2,3,7,8-substituted congeners highest concentrations were measured in hepatic tissue of adult monkeys. This is especially true for those substances with six and more chlorine atoms. Besides adipose tissue, comparatively high levels were found in thymus and also in lung tissue.(ABSTRACT TRUNCATED AT 400 WORDS)

Elimination of various polychlorinated dibenzo-p-dioxins and dibenzofurans (PCDDs and PCDFs) in rat faeces.

A defined mixture (of a composition characteristic of that present in incinerator fly ash) of polychlorinated dibenzo-p-dioxins and -furans (PCDDs and PCDFs) was subcutaneously administered to rats and the elimination of the unchanged congeners via faeces was measured. 1) All congeners administered could be found in faeces. 2) The rates of elimination via faeces were rather different for the different congeners. 3) The most toxic congeners, 2378-T4CDD and 12378-P5CDD, were present in unmetabolized form in faeces to less than 4% and less than 8% of the administered dose within the first week. Thus, parenteral administration clearly minimizes contamination of the animal quarters when compared with corresponding oral dosing. 4) The rate of unchanged elimination was apparently especially pronounced for the higher chlorinated PCDDs and PCDFs. The highest excretion rate was found for 1234678-H7CDD (up to 30% of administered dose). 5) No obvious differences were observed in the rates of elimination of the unchanged substances via faeces of the 2378-substituted or the non-2378-substituted isomers.

Absorption and tissue distribution of various polychlorinated dibenzo-p-dioxins and dibenzofurans (PCDDs and PCDFs) in the rat.

A defined mixture of polychlorinated dibenzo-p-dioxins and dibenzofurans (PCDDs and PCDFs) was parenterally administered to rats and absorption and tissue distribution were measured: 1) Toluene/DMSO (1 + 2; v/v) proved to be a convenient vehicle for the subcutaneous administration of the various PCDDs and PCDFs. Seven days after application the rate of absorption was 90% of the administered dose or even higher for almost all of the PCDDs/PCDFs in the mixture. In a few cases only (e.g. OCDD) the rate was found to be 84-89%; 2) Seven days after subcutaneous administration all 2378-substituted congeners were found in the liver, whereas only a few non-2378-substituted congeners could be measured in minor quantities. The 2378-substituted congeners also predominated in adipose tissue; however, most of the non-2378-substituted congeners were also detected; 3) The amount deposited within the liver as percentage of the administered dose differed for the various 2378-substituted PCDDs and PCDFs, ranging from less than 10% for OCDD or 2378-T4CDF, and between 60 and close to 100% for 12378-P5CDD or the H6CDDs. Therefore, the concentration ratio (liver/adipose tissue) was also found to be very different, ranging from less than 3 in the case of 2378-T4CDD or 2378-T4CDF to greater than 40 in the case of 1234678-H7CDD, 23478-P5CDF, 123678-H6CDF, or 1234678-H7CDF; 4) Studies performed at the time period of ongoing absorption (13-14 h after injection) provided the first evidence that some of the non-2378-substituted congeners do reach substantial concentrations in hepatic tissue shortly after administration; 5) Subsequent to intraperitoneal injection of the same PCDD/PCDF mixture the concentrations within the liver were found to be almost identical with that found after subcutaneous injection. In contrast, much higher concentrations of the congeners were found in (abdominal) adipose tissue; 6) In the liver of untreated rats of the same strain no T4CDDs/T4CDFs or P5CDDs/P5CDFs were detectable under our experimental conditions.