流动注射在线萃取—火焰原子吸收光谱法测定人发中微量镉和铅

本文建立了一个流动注射在线萃取－火焰原子吸收测定人发中微量镉和铅的方法，对含Ｃｄ和Ｐｂ分别为０．０２μｇ／ｍｌ和０．２０μｇ／ｍｌ的溶液，其相对标准偏差分别为３．４％和３．８％（ｎ＝９），Ｃｄ和Ｐｂ的灵敏度分别提高２１倍和２３倍，分析速度达３６次／ｈ，Ｃｄ和Ｐｂ的回收率分别在８７．３％－９７．０％和９１．９％－１０７．３％之间，文中还详细研究了各种实验参数的选择，测定人发样的结果与文献值相符。     

电镀废水中铜锌铬镍对农业环境的影响

电镀废水排水河涌会污染农业环境,以广东省南,海市平洲地区为例,农田灌溉水中Ｃｕ,Ｚｎ,Ｎｉ的含量超过允许限值１－１４倍,河涌底泥Ｃｕ,Ｚｎ,Ｃｒ,Ｎｉ超标１２－３７倍,土壤超标０．５－２．９倍,作物超标０．３－８倍。进入河涌的Ｃｕ,Ｚｎ,Ｃｒ,Ｎｉ能较快沉积于底泥中。     

九龙江口桐花树红树林对重金属的吸收与累积

探讨了福建九龙江口桐花树红树林对ＣＵ、Ｐｈ、Ｚｎ、Ｃｄ、Ｍｎ元素的吸收、累积及分布．结果表明：该林地土壤５种元素的储量关系为Ｍｎ＞Ｚｎ＞Ｐｈ＞ＣＵ≥Ｃｄ；植物体不同部位，各元素含量有着明显的差异，含量范围分别为Ｃｈ１．５１～５．７０、Ｐｂ１．３０～１０．７０、Ｚｎ１８．０～１００．１、Ｃｄ０．０４～０．２３和Ｍｎ１５．５～２３７．５（ｗ／１０－６）；植物对土壤元素的富集系数大小依次为Ｃｄ＞Ｚｎ＞Ｍｎ＞Ｃｕ＞Ｐｈ；群落现存生物量中，ＣＵ、Ｐｂ、Ｚｎ、Ｃｄ、Ｍｎ元素的现存累积量分别为１６．５６、６３．３０、４４５．０５、１．１４和１６５６．９３（ρＡ／ｍｇ·ｍ－２）．其中，地下部分别占７０．２％、８１．８％、７６．２％、７２．２％和８２．１％；林地残留物相应元素的储量分别为２１１．１１、１８４．００、１９４１．６９、６．１９和２２２４８．３１（ρＡ／μｇ·ｍ－２）．     

电感耦合等离子体—质谱法测定成人脏器样品中痕量稀土元素的研究

本文采用ＩＣＰ－ＭＳ法对成人脏器样品中痕量稀土元素进行了研究，选择了测定的最佳仪器参数，检查了测定中的各种干扰和影响；用铼（Ｒｅ）为内标元素补偿基体抑制效应和灵敏度的漂移。方法对稀土元素各分量的检出限为０．００５－０．０２６ｎｇ．ｍ１＾－１，标准回收率为９２．９－１１１．３％，精密度为０．９６－３．０７％。在严格分析质量控制的基础上用混合酸消解样品，不须分离富集，直接对成人的心、脾、肝、肾、肺肉中     

PCDDs在氯仿溶液中的紫外光解

使用ＮＤＣ－３型化学反应仪、３００Ｗ汞灯和１５ｍｌ反应管，于４３℃进行了２，３，７，８－ＴＣＤＤ，１，２，３，７，８－Ｐ５ＣＤＤ，１，２，３，４，７，８－ＨｘＣＤＤ，１，２，３，４，６，７，８－ＨｐＣＤＤ和ＯＣＤＤ在氯仿溶中的紫外光解，其一级反应速率常数测得值依次为０．５４，０．２９，０．１５，０．１５和０．１９ｍｉｎ＾－１，反应半衰期ｔ１／２均在５ｍｉｎ以内，还原脱氯是主要的光解途径，并有大量低     

城市垃圾堆肥制备专用肥对蔬菜生产和环境的效应

通过小区和大田试验方法，研究了城市生活垃圾肥制备有机。无机复合专用肥对蔬菜和土壤环境的效应。结果表明，施用该专用肥的辣椒、蕃茄或茄子、莴笋和青莱的小区和大田的产量，与对照相比分别增加２７．０％－８８．８％和２０．７％－９５．４％，其增产在Ｐ０．０１水平上达到显著，且蔬菜中一些营养成分的含量增加．而重金属Ｃｄ、Ｃｒ、Ｐｂ、Ａｓ元素的含量均未超有关卫生标准。长期施用，可补充土壤中有机质，且肥料中重金属元素不会引起菜地环境的污染。     

胡椒养分含量状况的研究

胡椒大、中量元素的含量在不同树龄中有所不同，幼龄期以氮最高，其Ｎ：Ｐ２Ｏ３：Ｋ２Ｏ：Ｃａ：Ｍｇ为１：０．１５：０．５３－０．９：０．２２－０．３８：０．１５－０．３０；成年龄则以Ｋ２Ｏ最高，Ｎ：Ｐ２Ｏ３：Ｋ２Ｏ：Ｃａ：Ｍｇ为１：０．１３：１．３２：０．４４：０．１６．在不施微肥的情况下，胡椒叶片缺Ｂ、Ｍｏ、Ｚｎ．成年龄胡椒各养分含量都是从萌芽期（收获后）开始，随生育期的进展而增加，到果实成熟期下降．一株中产胡椒Ｎ、Ｐ２Ｏ５、Ｋ２Ｏ总吸收量为２８２．４ｇ，其比例为１：０．１９：０．９．     

红球藻水生748株（Haematococcus sp.HB748）培养基的选择…

比较了红球藻ＨＢ７４８株在ＭＣＭ，ＢＢＭ及ＢＧ－１１，３种培养基中的生长，结果表明：ＨＢ７４８在这３种培养基中前４ｄ的平均生长速率分别为０．９７ｄ＾－１，０．７７ｄ＾－１和０．６３ｄ＾－１存在显著差异，然而在ＢＢＭ和ＢＧ－１１中添加ＭＣＭ中所含等量ＶＢ１２后，７４８株在３种培养基中的生长速率趋于一致，表明ＶＢ１２是ＨＢ７４８维持较好的前期生长的必需成分，在ＶＢ１２的需求满足后，３种培养基无机组分的     

中国癌症与土壤中钼元素的关系

利用土壤中钼元素资料１１０ ３７６个数据，癌死亡调查资料７８７０８０例，研究了胃 癌、食管癌、肝癌、宫颈癌、肺癌、大肠癌、白血病、鼻咽癌、乳腺癌死亡率与人群生存区土壤环境中钼元素的关系。结果表明，胃癌、食管癌、宫劲癌死亡率与钼元素有相关性，等级相关系数分别为－０．４２４６（Ｐ〈０．０２５），－０．５４５３（Ｐ〈０．００２５），－０．３３６９（Ｐ〈０．０５）。     

流动注射荧光分析法用于土壤及水系沉积物中铈（Ⅲ）含量的测定

研究表明Ｃｅ＾３＋在ｐＨ〈６．２ＫＣｌ介质中以２５４．０ｎｍ紫外光激发时，在３５２．０ｎｍ处发出具有恒定强度的荧光。因而可选择ｐＨ５－６作为测定酸度条件，利用Ａｌ２（ＳＯ４）３消除Ｆｅ＾３＋等离子的干扰，建立起Ｃｅ＾３＋的流动注射荧光分析法。方法的线性范围是２．０×１０＾－７—２．０×１０＾－６ｍｏｌ／ｌ，一元回归方程△Ｆ＝６６３６００Ｃ－０．０４１（ｎ＝１０，ｒ＝０．９９９７），检测限６．０×１     

Nitrite and Freshwater Fish

Nitrite occurs naturally in fresh waters as a result of nitrification of ammonia and denitrification of nitrate, and its concentration can be enhanced by partial oxidation of ammoniacal discharges. Nitrite is toxic to vertebrates including fish and a principal effect is the conversion of haemoglobin to methaemoglobin which is incapable of oxygen transport although there are circulatory and tissue effects as well. The toxic species is the nitrite ion (NO₂) which is believed to enter the blood via the branchial chloride/bicarbonate exchange and fish such as salmonids with high chloride uptake rates are more susceptible than those with low chloride uptake rates, for example carp. Nitrite toxicity is strongly aleviated by chloride and the concentration ratio of these ions is of great importance in assessing toxicity. Short term and long term toxicity data for a variety of fish species are presented. There are no field data on fish populations in waters where nitrite was the only pollutant. However extensive field surveys indicated that, waters with a mean chloride concentration of 25 mg l^-1 in good salmon fisheries were associated with concentrations of nitrite below 50 μg l^-1 N · NO₂, good coarse fisheries below 100 μg l^-1 N · NO₂.     

Fish wars and cooperation maintenance

In this paper, a discrete-time game model related to a bioresource management problem (fish catching) is considered. We divide a fishery into regions, which are exploited by single players. The center (referee) shares a reservoir between the competitors. The players (countries), which harvest the fish stock are the participants of this game.We assume that there are migratory exchanges between the regions of the reservoir. Therefore, the stock in one region depends not only on the previous stock and catch in the region, but also on the stock and catch in neighboring regions. We derive the Nash and cooperative equilibria for an infinite planning horizon.We consider two ways to maintain the cooperation: incentive equilibrium and time-consistent imputation distribution procedure. We investigate the cooperative incentive equilibrium in the case when the center punishes players for a deviation.Also we consider the case when the center is a player and find the Shapley value and time-consistent imputation distribution procedure. We introduce a new condition which offers an incentive to players to keep cooperating.     

Fish school density and volume

All the fish in a school occupy a volume estimated as N·BL³, where N is the number of fish and BL is their mean body length. We present extensive data from our experiments on cruising schools of saithe (Pollachius virens), herring (Clupea harengus) and cod (Gadus morhua) to validate this formula. Two methods of calculating the volumes of schools are described. One method is aggregative and depends on measuring the envelope of free space around a schooling fish, whereas the other is based on the dimensions of the school as a whole. The whole-school method is more reliable since it includes lacunae between the sub-units which exist in schools. For this method, we derive a computation which eliminates bias from outliers. The most realistic theoretical aggregative packing model predicts a volume per fish of 0.6 BL³. In saithe, the envelope of free space is approximately an ellipsoid, which, although it becomes more compressed at higher swimming speeds, yields a volume close to 0.7 BL³. From the whole-school method we calculate average volumes of 1.4 BL³ for saithe and 0.7 BL³ for herring. Increase in swimming speed produces more compact schools in saithe, but changes in arousal level can generate equally large differences. Changes in volume were not adequately explained by changes in nearest neighbour distance, giving support to the whole-school method.     

Fish in larger shoals find food faster

Summary Experiments on shoaling cyprinids hunting for food on patches in tanks demonstrate and advantage of foraging in a group. Individual goldfish (Carassius auratus) and minnows (Phoxinus phoxinus) in a shoal of conspecifics located food more rapidly as shoal size increased from 2 to 20. although shoaling minnows form polarised schools more readily than goldfish, which rarely do so, both species benefited from the trend of speedier food location with increasing group size.     

用连续提取法研究芘在鱼鳃表面的结合形态

建立了研究鱼鳃表面芘的结合状态的四步连续提取方法．分别用H2O、CaCl2、CH3OH和n-C6H14+CH2Cl2(1:1, v/v)混合液提取经暴露的鱼鳃．操作定义的前3步分别提取松散附着在鳃表的鱼鳃黏液中的芘,紧密附着在鳃表的鱼鳃黏液中的芘以及直接吸着在鱼鳃表皮上的芘,第4步则用来提取鱼鳃组织吸收的芘．其提取的芘分别占总量的 4．0％、12．1％、45．2％和38．7％．经3 h暴露,进入鳃组织的芘仅为总测定量的三分之一强,因此大部分芘并未进入鳃组织．单独进行的五步CH3OH连续提取实验结果证明,CH3OH提取步骤能有效地解吸鳃表吸着的芘,但不会导致鳃组织中芘的释放．动态实验结果表明,黏液结合态芘在暴露1h左右即达到平衡,而鳃表吸着态和鳃组织吸收态芘在暴露3h内含量迅速上升,3 h后显著趋缓．     

Water Quality Criteria for European Freshwater Fish

1. For water pollution control purposes, the concentration-addition model for describing the joint effects of mixtures of toxicants on aquatic organisms is appropriate; in this model the contribution of each component in the mixture is expressed as a proportion of the aqueous concentration producing a given response in a given time (e.g. p 96-h LC50).

2. Examination of available data using this model shows that for mixtures of toxicants found in sewage and industrial effluents, the joint acutely-lethal toxicity to fish and other aquatic organisms is close to that predicted, assuming simple addition of the proportional contribution from each toxicant. The observed median value for the joint effect of these toxicants on fish is 0.95 of that predicted, and the corresponding collective value for sewage effluents, river waters, and a few industrial wastes, based on the toxicity of their constituents, is 0.85, while that for pesticides is 1.3.

3. The less-than-predicted effect of commonly-occurring toxicants in some mixtures may be partly attributable to small fractions of their respective LC50 values having a less-than-additional effect. However, recent research has shown that for some organic chemicals which have a common quantitative structure-activity relationship (QSAR), their joint action as determined by acute toxicity is additive at all concentrations.

4. The few (unpublished) data available for the long-term lethal joint effect on fish of toxicants in mixtures suggest that they may be markedly more than additive, a phenomenon that needs confirmation and further investigation.

5. In the few studies on the sub-lethal effects on fish (eg growth), the joint effect of toxicants has been consistently less-than-additive which suggests that as concentrations of toxicants are reduced towards the levels of no effect, their potential for addition is also reduced. There appear to be no marked and consistent differences between the response of different species to mixtures of toxicants.

6. Field studies have shown that reasonably accurate toxicity predictions based on chemical analysis can be made if the waters which are polluted are acutely lethal to fish, and that a fish population of some kind can exist where the median 2 p t LCSOs (rainbow trout) is < 0.2. It is not known whether this condition is equivalent to a C p NOEC of 4.0 (ie the sum of the individual fractions of the NOEC for the species present), or to a NOEC of < 1.0 for each individual toxicant (i.e. fractions of the NOEC are not summed).

7. In general, the joint effect of the common toxicants on lethal and sub-lethal responses of fish is not explained by variations in the uptake of the individual toxicants concerned; this may not apply for those chemicals with a common QSAR, although there is little experimental evidence in this field.

8. There is an immediate need for more empirical studies on the joint effect of mixtures of toxic units of individual components, and the relation between long- and short-term lethal and non-lethal joint effects. This applies to mixtures of commonly occurring toxicants as well as to mixtures of organic chemicals with a common QSAR. The data obtained should be reinforced by studies on the mechanisms of interaction of toxicants. More field studies which relate water quality to the structure and productivity of fish populations are also required, involving direct measurements of fractional toxicity of the river water wherever possible.

9. The concentration-addition model appears to be adequate to describe the joint effect of commonly-occurring constituents of sewage and industrial wastes, and for tentative predictions of the joint effect on fish populations of toxicants present at concentrations higher than the EIFAC recommended values. However, concentrations lower than the EIFAC recommended values may make an increasingly lesser contribution to the toxicity of mixtures of toxicants and there may be a need to adjust the tentative water quality criteria downwards where two or more toxicants are present at concentrations close to these values. For toxicants with a common QSAR, their additive joint action may necessitate the setting of water quality criteriafor this group as a whole and not on the basis of individual compounds. However, too little is known of their precise joint action where the combined concentration produces a sub-lethal response.