Formaldehyde exposure in a gross anatomy laboratory--personal exposure level is higher than indoor concentration.

GOAL, SCOPE AND BACKGROUND: Cadavers for gross anatomy laboratories are usually prepared by using embalming fluid which contains formaldehyde (FA) as a principal component. During the process of dissection, FA vapors are emitted from the cadavers, resulting in the exposure of medical students and their instructors to elevated levels of FA in the laboratory. The American Conference of Governmental Industrial Hygienists (ACGIH) has set a ceiling limit for FA at 0.3 ppm. In Japan, the Ministry of Health, Labour and Welfare has set an air quality guideline defining two limit values for environmental exposure to FA: 0.08 ppm as an average for general workplaces and 0.25 ppm for specific workplaces such as an FA factory. Although there are many reports on indoor FA concentrations in gross anatomy laboratories, only a few reports have described personal FA exposure levels. The purpose of the present study was to clarify personal exposure levels as well as indoor FA concentrations in our laboratory in order to investigate the relationship between them. METHODS: The gross anatomy laboratory was evaluated in the 4th, 10th and 18th sessions of 20 laboratory sessions in total over a period of 10 weeks. Air samples were collected using a diffusive sampling device for organic carbonyl compounds. Area samples were taken in the center and four corners of the laboratory during the entire time of each session (4-6 hours). Personal samples were collected from instructors and students using a sampling device pinned on each person's lapel, and they were 1.1 to 6 hours in duration. Analysis was carried out using high performance liquid chromatography. RESULTS AND DISCUSSION: Room averages of FA concentrations were 0.45, 0.38 and 0.68 ppm for the 4th, 10th and 18th sessions, respectively, ranging from 0.23 to 1.03 ppm. These levels were comparable to or relatively lower than the levels reported previously, but were still higher than the guideline limit for specific workplaces in Japan and the ACGIH ceiling limit. The indoor FA concentrations varied depending on the contents of laboratory sessions and seemed to increase when body cavity or deep structures were being dissected. In all sessions but the 4th, FA levels at the center of the room were higher than those in the corners. This might be related to the arrangement of air supply diffusers and return grills. However, it cannot be ruled out that FA levels in the corners were lowered by leakage of FA through the doors and windows. Average personal exposure levels were 0.80, 0.45 and 0.51 ppm for instructors and 1.02, 1.08 and 0.89 ppm for students for the 4th, 10th and 18th session, respectively. The exposure levels of students were significantly higher than the mean indoor FA concentrations in the 4th and 10th sessions, and the same tendency was also observed in the 18th session. The personal exposure level of instructors was also significantly higher than the indoor FA level in the 4th session, while they were almost the same in the 10th and 18th sessions. Differences in behavior during the sessions might reflect the differential personal exposure levels between students and instructors. CONCLUSION: The present study revealed that, if a person is close to the cadavers during the gross anatomy laboratory, his/her personal exposure level is possibly 2 to 3-fold higher than the mean indoor FA concentration. This should be considered in the risk assessment of FA in gross anatomy laboratories. RECOMMENDATION AND OUTLOOK: If the risk of FA in gross anatomy laboratories is assessed based on the indoor FA levels, the possibility that personal exposure levels are 2 to 3-fold higher than the mean indoor FA level should be taken into account. Otherwise, the risk should be assessed based on the personal exposure levels. However, it is hard to measure everyone's exposure level. Therefore, further studies are necessary to develop a method of personal exposure assessment from the indoor FA concentration.

Distributions and chemical forms of arsenic after intravenous administration of dimethylarsinic and monomethylarsonic acids to rats.

The observed toxicity of arsenic is highly dependent on animal species and differences in metabolism. Rats are one of the most tolerant species, and the metabolic pathway is quite different in some aspects from those of other mammals. The distinct metabolic pathway including the preferential accumulation in red blood cells (RBCs) has been explained, whereby allowing an effective use of rats as an animal model for the arsenic metabolism. In the present study, distributions of arsenic among organs/tissues/body fluids and their chemical forms were studied after intravenous injection of arsenic in the forms of dimethylarsinic (DMA(V)) and monomethylarsonic acids (MMA(V)) to rats. DMA(V) and MMA(V) were mostly excreted into urine immediately after the injection as the intact forms, and both forms were taken up less effectively by organs/tissues than arsenite. The methylated arsenics distributed in organs/tissues were excreted directly into urine and excreted before being redistributed in RBCs. DMA(V) and MMA(V) taken up by the liver were transformed to metabolites not yet identified, accumulated transiently in the liver, and then they disappeared from the liver. The unidentified metabolites were assumed to be transformed from dimethylarsinic acid (DMA(III)) following the consecutive metabolic reactions [MMA(V) --> monomethylarsonous acid (MMA(III)) --> DMA(V) --> DMA(III)]. The unidentified metabolites were excreted not into the bile but into the bloodstream. Injections of DMA(V) and MMA(V) induced a biliary excretion of arsenic but only at 0.2-0.3% of the dose, the arsenic in the bile being their intact free forms.

Dimethylthioarsenicals as arsenic metabolites and their chemical preparations.

Two unidentified arsenic metabolites were detected in the liver of rats on a gel filtration column by HPLC inductively coupled argon plasma mass spectrometry after an injection of dimethylarsinic (DMA(V)), dimethylarsinous (DMA(III)), monomethylarsonic (MMA(V)), or monomethylarsonous (MMA(III)) acid. The same arsenicals were also produced in vitro by incubation of DMA(III) in the liver supernatant but not by DMA(V). The two arsenic metabolites eluted at the same retention times as those of the two arsenicals prepared by reaction of DMA(V) with either thiosulfate plus disulfite or hydrogen sulfide or sodium sulfide plus sulfuric acid. The faster and slower eluting products on a gel filtration column were assigned as dimethyldithioarsinic acid (dimethylarsinodithioic acid) (DMTA(V)) and dimethylthioarsinous acid (DMTA(III)) from mass spectrometric data at m/z = 170 and 138 by electrospray ionization mass spectrometry with negative and positive ion modes, respectively. They were prepared selectively by reacting DMA(V) with hydrogen sulfide or sodium sulfide plus sulfuric acid under different reaction conditions. DMA(III) but not DMA(V) was transformed to DMTA(III) and DMTA(V) in the presence of sodium sulfide in vitro, suggesting that DMA(V) is reduced to DMA(III) with hydrogen sulfide, thiolated to DMTA(III), and then further thiolated oxidatively to DMTA(V). Metabolically, it is assumed that DMA(III) is transformed to DMTA(III) in the presence of sulfide ions, and then, DMTA(III) is oxidatively thiolated to DMTA(V). As the chemical species produced by reduction with the Reay and Asher method are DMTA(III) and DMTA(V), and different from DMA(III), the studies carried out with DMA(III) with the Reay and Asher method have to be reexamined.

[Volatile organic compounds of the tap water in the Watarase, Tone and Edo River system].

OBJECTIVES: The chlorination of river water in purification plants is known to produce carcinogens such as trihalomethanes (THMs). We studied the river system of the Watarase, Tone, and Edo Rivers in regard to the formation of THMs. This river system starts from the base of the Ashio copper mine and ends at Tokyo Bay. Along the rivers, there are 14 local municipalities in Gunma, Saitama, Ibaragi and Chiba Prefectures, as well as Tokyo. This area is the center of the Kanto plain and includes the main sources of water pollution from human activities. We also analyzed various chemicals in river water and tap water to clarify the status of the water environment, and we outline the problems of the water environment in the research area (Fig. 1). METHODS: Water samples were taken from 18 river sites and 42 water faucets at public facilities in 14 local municipalities. We analyzed samples for volatile organic compounds such as THMs, by gas chromatography mass spectrometry (GC-MS), and evaluations of chemical oxygen demand (COD) were made with reference to Japanese drinking water quality standards. RESULTS: Concentrations of THMs in the downstream tap water samples were higher than those in the samples from the upperstream. This tendency was similar to the COD of the river water samples, but no correlation between the concentration of THMs in tap water and the COD in tap water sources was found. In tap water of local government C, trichloroethylene was detected. CONCLUSIONS: The current findings suggest that the present water filtration plant procedures are not sufficient to remove some hazardous chemicals from the source water. Moreover, it was confirmed that the water filtration produced THMs. Also, trichloroethylene was detected from the water environment in the research area, suggesting that pollution of the water environment continues.

Acute effects of ozone exposure on lung function in mice sensitized to ovalbumin.

Pulmonary responses to ozone exposure (1.0 ppm) were investigated in mice sensitized to ovalbumin compared with control mice receiving saline. Pulmonary function parameters were measured by pneumotachography. Arterial blood gases and the concentrations of soluble intercellular adhesion molecule-1 (sICAM-1) and tumor necrosis factor-alpha (TNF-alpha) in bronchoalveolar lavage fluid were analyzed. Ozone exposure, when compared with filtered air exposure, caused significantly larger decreases in dynamic compliance (P<0.05) and minute ventilation (P<0.05) in ovalbumin-sensitized mice but not in control mice. Moreover, the decrease in minute ventilation in response to ozone exposure was significantly greater (P<0.01) in ovalbumin-sensitized mice than in control mice. Ozone exposure caused a significant decrease in PaO2 in ovalbumin-sensitized mice but not in control mice. PaO2 after ozone exposure tended to be smaller in ovalbumin-sensitized mice than in control mice. The concentration of sICAM-1 in bronchoalveolar lavage fluid increased in ovalbumin-sensitized mice, but effects of ozone exposure were not observed. These results indicated that sensitization of the immune system to ovalbumin might be a risk factor which aggravates the effects of ozone exposure on the respiratory system.