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Testes of rats, which had been injected with a single dose of 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) (0.3 micrograms/kg-25 micrograms/kg body weight [BW]), were studied after 7 days using morphological and histochemical means. Light and electron microscopic examination revealed that TCDD affected testicular morphology in a dose-dependent manner. TCDD led to decreased intercellular contact, indicated by wide intercellular spaces between Sertoli cells between and Sertoli cells and neighbouring germ cells. Morphological alaterations in rat testes after TCDD administration included the sloughing off of premature spermatids into the tubular lumen and numerical increase of necrotic germ cells, in particular pachytene spermatocytes. Compared with control animals, Sertoli cells of treated rats exhibited an increased amount of lipid droplets and phagolysosomes. Vacuolization of the cytoplasm and fragmentation of the Sertoli cells occurred frequently. Examination of the different spermatogenic stages revealed that no stage was specifically susceptible to TCDD. In Leydig cells a decrease in enzyme activity of 3 beta- and 17 beta-hydroxysteroid dehydrogenases became evident by histochemical investigation. This effect on steroidogenesis was already found at a dose of 1 microgram/kg BW TCDD, whereas morphological effects were seen in the germinal epithelium for the first time at 3 micrograms/kg BW.

Possible effects on the next generation after long-term exposure (subcutaneous administration) of male rats to very high doses of 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) were studied. Two dose regimes were applied: TCDD-25 (initial dose: 25 micrograms/kg body wt; maintenance dose: 5 micrograms/kg body wt, once weekly) and TCDD-75 (initial dose: 75 micrograms/kg body wt; maintenance dose: 15 micrograms/kg body wt). Male rats were treated for 10 weeks before mating and then throughout the entire 12 week mating period. They were mated to unexposed virgin females. One group of pregnant females was used for teratological evaluations, and another group was allowed to deliver. No significant differences were observed in the number of implantations or fetuses per litter, and resorption rate, and fetal weight between the controls and TCDD-treated groups. No gross-structural anomalies occurred in any of the fetuses sired by TCDD-treated males. In the TCDD-25 group an increased frequency of two types of variations was observed which also occur in controls: incompletely ossified fingers (TCDD-25 = 5.1%, controls = 2.6%), and incompletely ossified ossa zygomatica (TCDD-25 = 1.8%, controls = 0.5%). In the TCDD-25 group a slight but statistically significant increase was observed in the rate of stillbirths (TCDD-25 = 1.3%, controls = 0.1%), apparently due to an unusually low frequency occurring in the controls (overall historical controls = 0.6%). There was no difference in postnatal mortality (TCDD-25 = 1.3%, controls = 1.3%). Taken together, despite the very high doses of TCDD used, the data do not provide evidence for biologically significant paternally-mediated developmental toxicity in the fetuses and newborn.

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)

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.

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.

(Bis[tri-n-butyltin])oxide (TBTO) was studied for its toxic potential on prenatal development. The effect of this substance on limb differentiation (mouse embryos) in organ culture was evaluated. In the organ culture system using mouse limb buds, TBTO interfered with morphogenetic differentiation at doses as low as 0.03 microgram/ml (5 X 10(-8)M). This is one of the lowest concentrations of a substance ever found to be active in this in vitro system. The in vitro studies suggest a high embryotoxic potential of TBTO. The low embryotoxicity found in the in vivo studies may be due to limited exposure of the embryos by the original unmetabolized substance.

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.

Concentrations of 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) in rat liver and adipose tissue, and hepatic ethoxyresorufin O-deethylase (EROD) activity were studied subsequent to a single subcutaneous injection of TCDD. Two types of experiments were performed to study: (a) time-dependent changes following a single injection of 300 ng TCDD/kg body wt (points 1-4), and (b) dose-dependent changes measurable after 7 days following a single injection (points 5-7). 1. Absorption of TCDD following a single subcutaneous injection was about 90% after 3 days and 98% after 5 days. 2. Following a single dose of 300 ng TCDD/kg body wt peak concentrations were: liver (after 3 days): 4.7 +/- 0.9 ng/g wet wt, and adipose tissue (after 7 days): 0.82 +/- 0.07 ng/g wet wt. 3. T1/2 of TCDD in liver was 13.6 days over the total experimental period (from day 10 to 91 of the study), apparently with an initial faster phase: 11.5 days (from day 10 to 49), and a slower period at the end of the experiment: 16.9 days (from day 49 to 91); in adipose tissue the t1/2 was 24.5 days (from day 14 to 91 of the study). 4. Maximum induction of EROD in the liver was observed (14-fold at 300 ng TCDD/kg body wt) 3-7 days following the injection; the activity was decreased to about one third of the maximum 3 weeks after the injection; increase in total cytochrome P-450 at this dose was only about 1.4-fold at the induction maximum. 5. The ratio of the TCDD concentrations in liver and adipose tissue increased considerably between doses of 3 ng TCDD/kg body wt (ratio: about 0.74) and 3000 ng TCDD/kg body wt (ratio: about 7.7). 6. The extent of EROD induction in the liver increased dose dependently. A significant effect was first observed with a dose of 3 ng TCDD/kg body wt (activity about +32% above control activity). The corresponding tissue concentration was about 10 pg TCDD/g liver wet wt. 7. An almost perfect linear relationship exists (when using a double-log plot) between the hepatic TCDD concentration and the EROD activity for tissue concentrations ranging from 40 to 30,000 pg TCDD/g wet wt.

Wistar rats were treated initially with very high single doses of 14C-2,3,7,8-TCDD (either 75 or 25 micrograms/kg body wt) followed by weekly maintenance doses of 15 and 5 micrograms/kg body wt, respectively. 14C-radioactivity was measured in various organs over a period of 22 weeks. 1) 75 micrograms TCDD/kg body wt (followed by the maintenance doses) was lethal for all the rats within a period of 9 weeks. While the concentration of 14C-TCDD equivalents in liver and thymus stayed reasonably constant during this period in the surviving rats, the concentration in adipose tissue and kidneys clearly increased in the same animals. 2) The dose of 25 micrograms TCDD/kg body wt (followed by weekly doses of 5 micrograms/kg body wt) proved to be a just tolerable dose over a period of 22 weeks for our strain of rats. 3) Within the individual variabilities the TCDD concentrations in the investigated organs showed no clear-cut decline, indicating that the animals were exposed to fairly constant levels of TCDD throughout the study. Thus, this dosing regime is suitable for maintaining constant TCDD exposure during long-term studies.

A study on the reproductive toxicity of 14C-TCDD in male rats was performed. Two dose regimes were applied subcutaneously: TCDD-25 (initial dose: 25 micrograms/kg body wt; maintenance dose: 5 micrograms/kg body wt) and TCDD-75 (initial dose: 75 micrograms/kg body wt; maintenance dose: 15 micrograms/kg body wt); the maintenance dose was administered once weekly. The rats were treated for 10 weeks before they were mated and throughout the entire mating period. The dose regime TCDD-75 led to a mortality rate of 93% within a period of 16 weeks. The first animals died during 4 weeks, and an LD50 was reached after 8 weeks. The dose regime TCDD-25 did not cause any mortality over a period of 12 weeks; but an LD10 was reached within 13-20 weeks. The body weight was significantly decreased in both groups treated with TCDD after 1 week of treatment. It stabilized in the TCDD-25-group 4 weeks after treatment and stayed at this level until the end of the treatment period. The most significant finding is the delayed fertilization by the treated males; 15% of the males were found to be sterile. The mating index (84%) and fertility index (14 +/- 11 days) of the TCDD-25-group were lower when compared with controls (95%, 8 +/- 5), but the pregnancy index was not reduced. Application of the chosen TCDD doses led to clear-cut morphological changes of the testes. The Sertoli cells were changed (increased occurrence of vacuoles, swelling of endoplasmatic cavities), and the contact between the Sertoli cells and spermatogonia was disturbed, which might indicate an inhibited maturation of spermatozoa precursors.

Examples of a combined approach using in vivo as well as in vitro methods for the assessment of prenatal toxicity are presented. The topics discussed include the analysis of the possible embryotoxic potential of valproic acid (VPA), female sex hormones, bis(tri-n-butyltin) oxide (TBTO), and acyclovir and the problem of supplementing in vitro systems with drug-metabolizing activity.