直接测汞仪测定尿中总汞

【目的】建立以直接测汞仪测定尿汞的方法?【方法】利用DMA80型直接测汞仪对尿样进行分析测定?【结果】该方法在1.0~200.0 ng具有良好的线性关系?该方法检出限为0.4μg/L?样品测定精密度为0.38%~1.68%?回收率为92.6%~96.9%?【结论】该方法可以作为尿中总汞的日常检测方法?     

尿中汞的热分解齐化原子吸收法

目的直接使用测汞仪,建立测定尿汞含量的新方法。方法采用热分解齐化法原子吸收法,直接测定尿中汞的含量。结果回归方程:A=0.046 62C;相关系数:R=0.999 9;线性范围0.20～12.5 ng;精密度1.2%～6.5%;样品加标回收率为92.8%;对尿汞标准物质测定9次,平均值为(32.0±0.8)μg/L,结果均在证书给出的不确定度范围内;对实际样品测定,进样量0.1 ml时,其结果均0.46μg/L。结论该方法操作简便快速,各项指标可满足尿汞的测定。     

DMA-80直接测汞仪与冷原子吸收仪测定尿汞的对比研究

目的:使用DMA-80直接测汞仪和冷原子吸收测汞仪对尿汞的测定进行对比研究。结果:两种仪器在尿汞含量为0.0~50.0μg/L的范围内线性关系良好;直接测汞仪方法检出限为0.3μg/L,RSD为1.68%~7.99%,平均回收率为99.6%~110.0%;冷原子吸收测汞仪方法检出为0.5μg/L,RSD为0.84%~4.67%,平均回收率为108.0%~114.0%。结论:用统计软件对两种仪器测定的84组样本检测结果进行分析,差异无统计学意义。     

食品中汞的热分解齐化原子吸收测定法

目的使用直接测汞仪,建立测定食品中汞含量的新方法。方法采用热分解齐化原子吸收法,直接测定食品中汞的含量。结果回归方程为A=0.043 0 Hg+0.0160相关系数为R=0.999 5,线性范围为0.00～10.00 ng,精密度为0.62%～17.2%,回收率为85.8%～105.8%,检出限为0.03 ngHg。结论该方法操作简便快速,各项指标均可满足食品中汞的测定要求。     

DMA-80直接测汞仪测定尿中总汞

目的:采用DMA-80直接测汞仪建立尿中总汞含量的直接测定方法。结果:方法在0~500 ng范围内线性良好,检出限为0.3μg/L,RSD为0.83%~2.46%,加标回收率为99.6%~107.0%,对质控样进行检测,结果满意。结论:该方法简便、快速、灵敏度高、结果准确,适用于对尿中总汞的测定。     

热分解齐化原子吸收法直接检测疑似汞中毒病例尿汞含量

目的建立以直接测汞仪采用热分解齐化原子吸收法测定尿汞含量的方法,并检测疑似汞中毒病例尿汞含量。方法利用DMA80型固液相自动测汞仪对尿样直接进行检测。结果在质量浓度0.02~0.10mg/L范围内,汞含量和吸光度呈良好线性,相关系数r=0.999 8。加标回收率为99.6%~101.8%,标准偏差为2.9%。2015年累计检测113份尿样,尿汞合格率88.50%。尿汞质量浓度为0.04~252.80μg/L,经校正含量为0.000~0.37mg/g肌酐。结论采用直接测汞仪检测尿汞含量,样品不需进行预处理和化学法还原,操作简便、快捷,无废物处置,结果可靠,可在临床实验室进行推广。     

直接测汞仪测定尿中的汞

[目的]建立尿中汞含量的直接测定方法。[方法]采用DMA80直接测汞仪测定尿中汞含量并与冷原子吸收法进行比较。[结果]该方法的线性范围为2．00～40．00μg／L,线性方程夕=0．019x＋0．006,r=0．9995,检出限为0．05ng,精密度试验相对标准偏差为2．2％～8．7％,加标回收率范围为97．5％～102．6％。[结论]该法与冷原子吸收分光光度法测定尿中汞含量结果相比较,差异无统计学意义。     

直接测汞仪法测定尿中汞国标方法的研制

目的 建立一种快速简便、能满足生物监测国家标准要求的尿中汞的测定方法。 方法 采用直接测汞仪对尿中汞的测定情况进行考察和试验。 结果 尿中汞含量在1.6~100 μg/L时测得的峰面积和汞浓度之间呈良好的线性关系,相关系数>0.999。方法检出限为0.5 μg/L,方法定量下限为1.6 μg/L。批间、批内测定的相对标准偏差均小于5%。对10、30、60 μg/L三个浓度水平的尿样,加入与原浓度相近的汞浓度的加标回收率为91.6%~99.9%,对有证参考物质的测定及与冷原子吸收法的比对结果满意。 结论 直接测汞仪法作为一种简单、快速的测定方法能满足生物材料中化学物质测定方法的要求,可以用于职业接触者尿中汞的测定。     

测定鲜食用菌中总汞含量的直接测汞仪法

目的 建立鲜食用菌中总汞快速准确的测量方法。方法 使用HydraⅡ型测汞仪,样品直接进样,对50份样品进行测定。结果 结果表明,在1.0～200 ng范围内线性良好,相对标准偏差为1.40%～5.56%,回收率在93.3%～106.5%之间,最低检出限为0.218μg/kg,满足实验要求。结论 使用测汞仪直接测定鲜食用菌中总汞含量,具有灵敏度高、方便快捷,无须前处理等优点,便于推广,适用于鲜食用菌中总汞的快速测定。     

尿中甲基汞测定的直接测汞仪法

目的建立尿中甲基汞的溶剂提取-直接测汞仪测定方法。方法尿样水解后, 甲基汞经甲苯萃取, 再由L-半胱氨酸溶液反萃取出来, 直接加入到直接测汞仪中测定。结果尿中甲基汞浓度在0.2～ 50.0 μg/L线性关系良好, 相关系数为0.999 9。方法批内精密度相对标准偏差(RSD)为5.04%～ 6.64%, 批间精密度RSD为5.65%～8.11%, 平均回收率分别为85.4%～95.5%, 检出限为0.048 2 μg/L, 定量下限为0.160 7 μg/L。结论直接测汞仪测定尿中甲基汞的检出限低、灵敏度高、稳定性好、操作简便, 可用于尿中甲基汞的测定。     

农民炼汞所致大气汞污染和汞中毒

The article reports the results of the investigation on atmospheric pollution and mercury poisoning caused by the peasants mercury smelting. Mercury-smelting is a sideline occupation of the peasants in the mining area. They carried out the production in their homes, which were not protected. The equipment used was simple and the technological level low. Much was done during the slack seasons in farming. Before mercury-smelting was carried out the mercury concentration of air inside the house of the key household was 0.099 2 mg/m3, and outside 0.060 9 mg/m3. During mercury-smelting, near the stove, inside the house of the key household and the next door neighbour the concentrations were high, reaching 0.6463, 0.3160, 0.1717 mg/m3 respectively. At 10m, 30m, 100m, from the stove the figures were 0.0628, 0.0377 and 0.0079 mg/m3 respectively. 126 persons in 36 key households and their neighbours were given physical examinations and the incidence of chronic mercury poisoning of the operators, family members and their neighbours' family members were 75.00%, 13.79%, 3.57%, the mercury absorptivity were 12.50%, 34.48% and 21.43%, while the concentrations of mercury in the urine were 59.18, 18.21, 9.62 micrograms/L respectively. The mercury absorptivity of children under 15 was high 45.45%. The youngest age that absorbed mercury was 3. The characteristics of the harm that the peasants mercury smelting caused were discussed and suggestions proposed for their remedy.     

Elemental mercury in urine from workers exposed to mercury vapor

Summary Elemental mercury (Hg°) in urine samples from workers in thermometer manufacturing factories was determined. In a factory in which the mercury level in the ambient air averaged more than 0.1 mg Hg m^–3, the Hg° concentration in the workers' urine ranged between 0.05 and 1.7 g Hg 1^–1 and constituted less than 1% of the inorganic mercury (In-Hg) in urine. Higher amounts of Hg° could be detected in urine on the day of the filling operation when thermometer blanks were filled with metallic mercury and on the following day when compared with other days. During this operation, the workers were exposed to mercury vapor levels with as much as 0.47–0.67 mg Hg m^–3. Our findings suggest that Hg° appears in urine quite rapidly after the worker's exposure to unusually high mercury levels.     

Elemental mercury spills

Sources of elemental mercury (Hg0) include old natural gas regulators, manometers, sphygmomanometers, thermometers, and thermostats. Causes of Hg0 spills include improper storage, container breakage, children playing with Hg0, the breakage of devices containing Hg0, and ritualistic use of Hg0. Inhalation is the primary exposure route for Hg0. Mercury released into the environment can enter lakes and streams, where bacteria convert it into methylmercury, which bioaccumulates in fish. Chronic exposure to Hg0 vapors can damage the kidneys and neurologic system. Short-term exposure to high levels of Hg0 vapors may cause lung damage, nausea, vomiting, diarrhea, increases in blood pressure or heart rate, skin rashes, and eye irritation, among other effects. Minimizing Hg0 dispersal is important after an Hg0 spill. Tracking by shoes or apparel or vacuuming can spread Hg0, increasing airborne concentrations and cleanup costs. The Illinois Department of Public Health's response to an Hg0 spill depends on the size of the spill. Airborne concentrations after large spills are mapped with a mercury vapor analyzer (MVA). The cleanup begins with the spill site and any hot spots that were identified with the MVA. Hard surfaces can usually be cleaned, but contaminated porous items must be discarded. Leaving marginally contaminated items outdoors for a month or more during warm weather may dissipate the Hg0. After a cleanup, clearance sampling is conducted to determine if further cleanup is needed. The best way to prevent Hg0 spills is reduce its use. Key words: cleanup, elemental mercury, health effects, mercury, prevention, remediation, spill, spill management.     

Atmospheric mercury in Changbai Mountain area, northeastern China II. The distribution of reactive gaseous mercury and particulate mercury and mercury deposition fluxes

Reactive gaseous mercury (RGM) and particulate mercury (Hgp) concentrations in ambient air from a remote site at Changbai Mountain area in northeastern China were intermittently monitored from August 2005 to July 2006 totaling 93 days representing fall, winter-spring and summer season, respectively. Rainwater and snow samples were collected during a whole year, and total mercury (THg) in rain samples were used to calculate wet depositional flux. A throughfall method and a model method were used to estimate dry depositional flux. Results showed mean concentrations of RGM and Hgp are 65 and 77 pg m⁻³. Compared to background concentrations of atmospheric mercury species in Northern Hemisphere, RGM and Hgp are significantly elevated in Changbai area. Large values for standard deviation indicated fast reactivity and a low residence time for these mercury species. Seasonal variability is also important, with lower mercury levels in summer compared to other seasons, which is attributed to scavenging by rainfall and low local mercury emissions in summer. THg concentrations ranged from 11.5 to 15.9 ng L⁻¹ in rainwater samples and 14.9-18.6 ng L⁻¹ in throughfall samples. Wet depositional flux in Changbai area is calculated to be 8.4 μg m⁻² a⁻¹, and dry deposition flux is estimated to be 16.5 μg m⁻² a⁻¹ according to a throughfall method and 20.2 μg m⁻² a⁻¹ using a model method.