流动注射在线富集分离-火焰原子吸收光谱法测定水体中的铬(Ⅲ)和铬(Ⅵ)

内装活性氧化铝（碱式）和阴离子交换树脂的微型柱流动注射在线富集分离水体中的铬（Ⅲ）和铬（Ⅵ），火焰原子吸收法直接检测。微型住可同时富集两种价态的离子，分别用1mol／L的NH4NO3和HNO3洗脱Cr（Ⅵ）和Cr（Ⅲ）于喷雾器中。进样时间25s，铬（Ⅵ）和铬（Ⅲ）的富集倍数分别为11倍和20倍，实际水样的加标回收率在90％～106％之间；分析速率为50个样／h；铬（Ⅵ）、铬（Ⅲ）的检出限（3δ）分别为1．5μg／L和0．7μg／L；相对标准偏差（50μg／L）分别为1．9％和2．6％。     

在线还原富集-导数火焰原子吸收光谱法测定环境水样中铬(Ⅲ)和铬(Ⅵ)的形态

采用单阀双阳离子交换树脂微柱并联，设计了双路采样逆向洗脱在线分离富集系统，该系统与原子吸收导数测量技术相结合，实现了在线分离富集．导数火焰原子吸收光谱法同时测定水中Cr（Ⅲ）和Cr(Ⅵ），导数仪用2mV／min档位，富集lmin时，分析速度为60样/h，测定Cr（Ⅲ）和Cr(Ⅵ）的特征浓度分别为0．448μg/L和0．793μg/L(相当于1％导数吸收度)，线性范围分别为0-90和0-180μg/L；对浓度分别为10、20μg/LCr（Ⅲ）和Cr(Ⅵ）测定的相对标准偏差分别为2．85％和2．85％；检出限分别为0．855和1．7lμg/L．该法对实际水样加标回收率在94．7％．104％之间。     

在线还原富集火焰原子吸收光谱法测定环境水样中Cr(Ⅲ)和Cr(Ⅵ)的形态

采用单阀双阳离子交换树脂微柱并联，设计了双路采样逆向洗脱在线分离富集系统，该系统与原子吸收测量技术相结合，实现了在线分离富集-火焰原子吸收光谱法同时测定水中Cr(Ⅲ)和Cr(Ⅵ)，富集1min时，分析速度为60样/h，测定Cr(Ⅲ)和Cr(Ⅵ)的特征浓度分别为6．08μg/L和11．58μg/L(相当于1％吸收)，线性范围分别为0～1．0μg/mL和0～2．0μg/mL，对质量浓度为100μg/L的Cr(Ⅲ)和Cr(Ⅵ)测定的相对标准偏差分别为2．9％和3．0％、检出限分别为8．70和10．8μg/L。该法对实际水样加标回收率在94．5％～104．3％之间。     

活性氧化铝微柱分离富集-电感耦合等离子体原子发射光谱法在线测定水中铬（Ⅲ）和铬（Ⅵ）

研究了活性氧化铝对Cr(Ⅲ)和Cr(Ⅵ)分离富集的性能，建立了流动注射(FI)-在线微柱分离富集-电感耦合等离子体原子发射光谱(ICP-AES)法测定水中微量Cr(Ⅲ)和Cr(Ⅵ)的分析方法。优化了流动注射测定的条件，进样频率为60/h；检出限(3σ)：Cr(Ⅲ)为0．8μg/L，Cr(Ⅵ)为0．6μg/L；线性范围为5-600μg/L;相对标准偏差小于2．4％；回收率为94．0％-102％。     

流动注射-火焰原子吸收光谱法测定水样中铬(Ⅲ)和铬(Ⅵ)

应用编结反应器(KR)在线富集,提出了测定水样中痕量铬(Ⅲ)和铬(Ⅵ)的流动注射-火焰原子吸收光谱法。取2份水样与络合剂吡咯烷二硫代氨基甲酸铵(APDC)溶液在线混合,分别与样品中铬(Ⅲ)及铬(Ⅵ)形成络合物并吸附于KR的内壁上,引入空气除去残留的溶液。泵入乙醇-盐酸(9+1)混合溶液将吸附于KR内壁上的络合物洗脱。按仪器工作条件测定洗脱液的吸光度(A_s)。另取1份水样,预先用抗坏血酸将其中铬(Ⅵ)还原为铬(Ⅲ),再按上述条件操作并测得吸光度(A_(Cr))。基于铬(Ⅲ)和铬(Ⅵ)富集系数的差异,推导了铬(Ⅲ)及铬(Ⅵ)含量的计算公式,将所测数据代入公式进行计算。所提出方法对铬(Ⅲ)及铬(Ⅵ)的检出限(3S/N)依次为8.9,5.3μg·L~(-1),相对标准偏差(n=5)分别为5.6%和2.8%。用标准加入法测得回收率在95.9%～98.9%之间。     

磷酸三丁酯棉纤维在线分离富集流动注射-火焰原子吸收光谱法测定铬(Ⅲ)和铬(Ⅵ)的量

用TBP-棉纤维吸附实现铬(Ⅵ)与铬(Ⅲ)的在线分离富集,并用流动注射(FI)-火焰原子吸收光谱法(FAAS)分别测定其含量。将TBP-棉纤维小球填入自制的锥形柱并组装在FI系统中作为分离单元。将预先调至pH 0.75的样品溶液,以4mL·min-1流量注入FI系统中,并在锥形柱中富集分离160s。此时铬(Ⅵ)被TBP-棉纤维吸附,而铬(Ⅲ)随流出液流出。收集流出液测定铬(Ⅲ)量。用水以2.6mL·min-1流量过锥形柱洗脱铬(Ⅵ),洗脱液引入FAAS,测定铬(Ⅵ)含量。铬质量浓度在0.100~0.900mg·L-1以内呈线性。对与0.02μg铬(Ⅲ)共存的0.10μg铬(Ⅵ)溶液作7次测定,计算得到铬(Ⅵ)测定值的相对标准偏差为6.4%。添加0.500mg·L-1铬(Ⅵ)及0.100mg·L-1铬(Ⅲ)溶液,计算得到铬(Ⅵ)及铬(Ⅲ)的平均回收率依次为119%和107%。     

流动注射在线富集分离—火焰原子吸收光谱法测定水体中的铬（Ⅲ）和铬（Ⅳ）

内装活性氧化铝（碱式）和阴离子交换树脂的微型柱流动注射在线富集分离水体中的铬（Ⅱ）和铬（Ⅳ），火焰原子吸收法直接检测，微型柱可同时富集两种价态的离子，分别用１ｍｏｌ／Ｌ的ＮＨ４ＮＯ３和ＨＮＯ３洗脱Ｃｒ（Ⅳ）和Ｃｒ（Ⅲ）于喷雾器中，进样时间２５ｓ，铬（Ⅳ）和铬（Ⅲ）的富集倍数分别为１１倍和２０倍，实际水样的加标回收率在９０％～１０６％之间，分析速率为５０个样／ｈ，铬（Ⅳ），铬（Ⅲ）的检出限（３δ）分     

流动注射光度法测定铬(Ⅵ)

铬（Ⅵ）可干扰很多重要的酶的活性，损害肝脏和肾脏，是一种潜在的致癌物质，因此测定环境样品中的铬（Ⅵ）具有极其重要的意义。测定铬（Ⅵ）的方法主要有二苯基碳酰二肼分光光度法、原子吸收光谱法、流动注射分析法，而流动注射分析法又分为流动注射原子吸收光谱法、流动注射分光光度法、流动注射化学发光法。     

活性氧化铝富集火焰原子吸收法测定铬（Ⅲ）和铬（Ⅵ）

研究了内装活性氧化铝的微型柱流动注射富集分离火焰原子吸收光谱法（Ｆｌ－ＦＡＡＳ）测定水体中μｇ／Ｌ级的Ｃｒ（Ⅲ）、Ｃｒ（Ⅵ）。用０．２ｍｏｌ／Ｌ氨水将活性氧化铝转为碱式以吸附Ｃｒ（Ⅲ），１ｍｏｌ／Ｌ硝酸洗脱；用０．０１ｍｏｌ／Ｌ的硝酸将活性氧化铝转为酸式以吸附Ｃｒ（Ⅵ），０．２ｍｏｌ／Ｌ的氨水洗脱，洗脱液直接送到喷雾器中。进样３０ｓ，浓度富集２５倍。两种价态离子的校正曲线浓度范围在１～５０μｇ／Ｌ之间，检测限分别为０．６和０．７μｇ／Ｌ，样品分析速率为６０样／ｈ。研究了共存离子的干扰情况，实际水样中的加标回收率在８５％～１０５％之间。     

紫外-可见吸光光度法同时测定铬(Ⅲ)和铬(Ⅵ)

关于铬 (Ⅲ )和铬 (Ⅵ )测定有若干报道 ,但大多数是分离后分别进行测定[1,2 ] ,或先测定出铬 (Ⅲ )或者铬 (Ⅵ ) ,然后通过氧化或还原测出铬的总量 ,再用差减法求出另一个价态铬的含量[3 ] ,这些方法比较麻烦 ,且在处理过程中易导致价态的改变 ,文献 [4]曾研究利用铬 (Ⅲ )与ＥＤＴＡ反应 ,可在铬 (Ⅲ )存在下光度法测定铬 (Ⅵ ) ,并指出同时测定铬 (Ⅲ )和铬(Ⅵ )的可能。文献 [5 ]也对此进行了研究 ,采用先进仪器 ,用最小二乘法 ,建立了多元校正 紫外 可见吸光光度法同时测定铬 (Ⅲ )和铬 (Ⅵ )的方法。此法虽解决了吸收光谱重叠问题 ,…     

Biotechnology of Cr(VI) transformation into Cr(III) complexes

The dose-dependent formation of Cr(III) complexes and uptake of chromium by Arthrobacter oxydans — a Gram-positive bacterium from contaminated Columbian basalt rocks (USA) — were studied along with the testing under aerobic conditions of two bacterial strains of Arthrobacter genera isolated from the polluted basalts from the Republic of Georgia. Instrumental neutron activation analysis (INAA) was used to track the accumulation of chromium in the bacterial cells. To monitor and identify Cr(III) complexes in these bacteria, electron spin resonance (ESR) spectrometry was employed.     

Fluorimetric Cr(VI) and Cr(III) Speciation With Crystal Violet

Abstract

A simple fluorimetric determination of Cr(VI) in the presence of Cr(III) is described. This determination is based on the fluorescence, produced from the ion-association complex between the Crystal violet cation and the anionic complex, formed between Cr(VI) and excess of I^?. This fluorescence is not observed when Cr(III) is used instead of Cr(VI). The fluorescence intensity is linear over the concentration range of 0–60 μg/1. The method was applied in potable and sea waters.     

Cr(III) and Cr(VI) speciation measurements in environmental reference materials

The production of reference materials for quality control of Cr(III) and Cr(VI) speciation in environmental samples is described. It concerns in the first place two lyophilized solutions containing Cr(III) and Cr(VI) at different concentrations, respectively representative for drinking water and filter leaching solutions, and in the second place filters loaded with welding dust. Twenty-four laboratories with experience in the field participated in an intercomparison exercise organized to validate the suitability of the reference materials and to gauge the state-of-the-art of Cr speciation throughout Europe. The outcome of this exercise is discussed.     

Prediction of Stability Constants for Cr(III) and Cr(II) Complexes

Regression analysis was used to derive equations for estimaing thermodynamic stability constants for complexes of Cr²⁺ (log^° ₁[Cr²⁺L] = 0.53log^° _n [H _n L]) and Cr³⁺ (log^° ₁[Cr³⁺L] = 0.88log^° _n [H _n L]) from the known protonation constants of H _n L ligands and for determining stability constants of Cr²⁺ and Cr³⁺ complexes from the available stability constants of Cu²⁺ complexes (log^° ₁[Cr²⁺L] = 0.76log^° ₁[Cu²⁺L] and log^° ₁[Cr²⁺L] = 0.60log^° ₁[Cr³⁺L], respectively). Parameters of the Panteleon–Ecka equation for calculating stability constants of Cr²⁺ complexes ( = 0.57) and Cr³⁺ complexes ( = 0.69) with two and three bidentate ligands were also determined. The ratio of logarithmic stability constants for complexes with the same metals but with different metal ionic charges was found to be approximately equal to the ratio of charges on the central ions. The stability constant of Cr(II) sulfate complex was calculated.     

Adsorption Studies of Cr(III) & Cr(VI) on Lead Sulphide,Copper Sulphide & Zinc Sulphide-Determination Cr(III) in the Presence of Cr(VI)

Abstract

The adsorption studies of Cr(VI) in presence of Cr(III) on the sulphide of Lead, Zinc and Copper has been studied. It has been found that in case of lead sulphide 100% adsorption of Cr(VI) took place at pH 4.0 and of Cr(III) at pH 7.0. While in case of zinc sulphide the 100% adsorption of Cr(VI) took place at pH 4.5 and of Cr(III) at pH 6.5. In case of copper sulphide 100% adsorption of Cr(VI) took place at pH 5.0 and of Cr(III) at pH 7.0. This difference in adsorption at different pH values forms the basis for the determination of these ions. The method is accurate.     

Amperometric Determination of Cr(III) and Cr(VI) by Flow Injection Analysis

Speciation of Cr(III) and Cr(VI) can be attained by flow injection analysis with amperometric detection. Cr(VI) is reduced in an acidic medium to Cr(III) with a glassy carbon electrode at —0.1 V vs. Ag/AgCl and the current is recorded. Cr(III) is oxidised on-line to Cr(VI) with alkaline hydrogen peroxide solution. From the difference of the total chromium and Cr(VI), the amount of Cr(III) was obtained. A linear calibration curve for Cr(VI) was obtained for the concentration ranges 0.01-5.0ppm of Cr(VI) and we have calculated the limit of determination to be about 0.5ppb. We have studied the degree of reproducibility obtained using the solid electrodes under various conditions. The influence of flow rate, coil length, interfenences and the extent of reaction were studied.     

Protocol for Extraction and Determination of Cr(VI) in Solid Materials with a High Cr(III)/Cr(VI) Ratio Using EDDS as a Leaching Agent for Cr(VI) and a Masking Agent for Cr(III)

A sensitive and selective protocol for the extraction of all forms of Cr(VI) from solid materials followed by determination by catalytic adsorptive stripping voltammetry has been elaborated. Cr(VI) was leached to a solution with 0.2 mol L^?1 (NH₄)₂SO₄/NH₄OH+0.1 mol L^?1 EDDS (pH 9.5) and simultaneously Cr(III) was transferred to a nonactive electrochemical complex with EDDS. The method allows for Cr(VI) determination in solid samples containing even a 1000–2000 fold excess of extractable Cr(III) without its noticeable influence. The effects of several experimental variables such as the composition and pH of the extractant, the time and temperature of the solid sample mixing with the extractant were studied. At the optimized conditions more than 95% of total Cr(VI) recoveries from solid samples were achieved. The validation of the proposed procedure was carried out by Cr(VI) determination in certified reference material CRM 019 Ash, spiked and unspiked with Cr(III), and by comparing the obtained results with those obtained using other common extraction procedures.     

石墨炉原子吸收光谱法测定土壤中可交换态Cr(Ⅲ)和Cr(Ⅵ)

提出了流动注射离子交换石墨炉原子吸收光谱法测定土壤中可交换态Cr(Ⅲ）和Cr(Ⅵ）的分析方法，优化了提取方法、分离富集条件和流路参数等。分析速度为20样/h，Cr(Ⅲ）和Cr(Ⅵ）的检出限（3σ）分别为24pg和4.0pg，相对标准偏差（n=10)分别为4.7%和5.9%。     

Determination of Cr(VI) and Cr(III) by Using Activated Carbon-Atomic Absorption Spectrometry

A method for the separation and preconcentration of Cr(III) and Cr(VI) on activated carbon in presence of diethyldithiocarbamate as a complexing reagent was optimized. The method makes it possible to achieve 200- to 500-fold Cr(VI) concentrating depending on the initial volume of the solution to be analysed and the final volume eluted. The Cr(VI) concentration in the background solution determined with RSD 30% was equal to 1.5 g L. The limit of Cr(VI) determination was equal to 0.9 g L.