Splenic and lymph node lymphocytes from Balb/C mice were activated in vitro by the heavy metal cations, Zn⁺⁺ and Hg⁺⁺, as noted by the several-fold increases in ³H-thymidine incorporation at 144 hours of culture. Optimal mitogenic concentrations of Zn⁺⁺ and Hg⁺⁺ were 200 μM and 10 μM, respectively. Data from experiments in which three different methods were used to enrich for either T or B splenic lymphocytes, i.e. cell passage over nylon wool columns, use of athymic Nu/Nu mouse spleen cells, or cell lysis with monoclonal anti-Thy-1 antibody plus complement, suggested that Zn⁺⁺ and Hg⁺⁺ were mitogens for T cells. Removal of macrophages from spleen cells by treatment with carbonyl iron followed by cell passage through nylon wool eliminated the lymphocyte responses to Zn⁺⁺ and to Hg⁺⁺. Moreover, addition of these macrophage-depleted lymphocytes to monolayers of resident peritoneal macrophages restored the lymphocyte responses to these mitogens. Both Zn⁺⁺ and Hg⁺⁺ activated splenic lymphocytes to display lectin-dependent cytotoxicity and to produce gamma interferon. Furthermore, Zn⁺⁺ induced low levels of natural killer activity in spleen cells. In contrast to spleen and lymph node cells, thymocytes and bone marrow lymphocytes did not respond to either cation under standard culture conditions. However, when cultured in the presence of E. coli-derived lipopolysaccharide (LPS) and 2-mercaptoethanol for 144 hours, thymocytes were activated by Zn⁺⁺ (200 μM) but not by Hg⁺⁺. Quantities of LPS as low as 1.0 ng/ml satisfied this culture requirement. Purified interleukin 1 could not replace the helping activity mediated by LPS. Thymocyte subpopulation studies showed that Zn⁺⁺ activated enriched peanut lectin receptor-negative mature thymocytes, but LPS was required for the response. Spleen cells from mice, intraperitoneally injected with ZnCl₂ for 7 to 14 days, were not activated in vivo as assessed by ³H-thymidine incorporation in vitro, nor did they display enhanced responses to T-cell or B-cell mitogens. However, zinc administration had negative effects by decreasing spleen cell numbers by 31% and thymic weight by 59%. A theoretical model is presented in which Zn⁺⁺ and Hg⁺⁺ may mediate their stimulating effects in vitro by altering histocompatibility "self" structures on the surface of lymphocytes and macrophages via interactions with sulfhydryl groups on these structures to which T lymphocytes with receptors for "altered self" structures respond with proliferation or cytotoxicity.

published_or_final_version / Geography and Geology / Master / Master of Philosophy

M. Tech. (Chemical Engineering, Faculty of Engineering and Technology), Vaal University of Technology| / The co-existence of organic acids and toxic heavy metals in natural water creates harmful effects on human, plants and animals. Therefore, it is necessary to treat organic acids and toxic heavy metal contaminated wastewater prior to its discharge to the environment. The aim of this study was to apply co-treatment of industrial wastewater containing citric acid and toxic heavy metals in single and binary systems using photocatalysis process. The hydrothermal method was used to synthesise dandelion-like TiO2 structures. Modifications of the dandelion-like TiO2 by deposition of gold nanoparticles and immobilisation on calcium alginate were done using deposition precipitation and one-step encapsulation methods, respectively. Dandelion-like TiO2 and dandelion-like TiO2 immobilised on calcium alginate (Alg/TiO2) were used as photocatalysts for Cr(VI), Hg(II) and citric acid removal from water. The results showed that the production of dandelion-like TiO2 structures strongly depends on the reaction time and synthesis temperature as key process parameters. The characterisation of the dandelion-like TiO2 by X-ray diffraction (XRD), transmission electron microscope (TEM), scanning electron microscopy (SEM), energy-dispersive X-ray (EDX) and Brunauer-Emmett-Teller (BET) revealed the crystal structure, morphology, chemical composition and surface area. It was found that the efficiency of photocatalytic process depends on the type of pollutants, initial pH of the solution, photocatalyst dosage, contact time, substrate initial concentration, UV wavelength and light intensity. The reduction efficiency of Cr(VI) ion and citric acid increased with decreasing the initial pH values and initial concentration. On the other hand, Hg(II) reduction efficiency increased with increasing the initial pH values and initial concentration. In a binary system, the reduction of Cr(VI) and Hg(II) was found to be faster than in the single and ternary systems. The relationship of the chemical reaction rate of Cr(VI), Hg(II) and citric acid were expressed by the pseudo-first-order kinetic equation. Addition of ferric ions to Cr(VI)-citric acid complex and Hg(II)-citric acid complex enhanced the reduction of Cr(VI) and Hg(II), a complete reduction was accomplished within 30 and 60 minutes (min) of irradiation time, respectively. The reduction efficiency of both Cr(VI) and Hg(II) in the presence of citric acid in a solution was still significant after four times of Alg/TiO2 reuse. These results indicated that the UV/TiO2 photocatalysis process can be considered as a suitable method to reach a complete reduction of Cr(VI) and Hg(II) in the presence of citric acid in a solution.

by Lau Tsz Chun. / Thesis (M.Phil.)--Chinese University of Hong Kong, 2000. / Includes bibliographical references (leaves 134-143). / Abstracts in English and Chinese. / Acknowledgements --- p.i / Abstract --- p.ii / Contents --- p.vi / List of Figures --- p.xi / List of Tables --- p.xv / Chapter 1. --- Introduction --- p.1 / Chapter 1.1 --- Reviews --- p.1 / Chapter 1.1.1 --- Heavy metals in the environment --- p.1 / Chapter 1.1.2 --- Heavy metal pollution in Hong Kong --- p.3 / Chapter 1.1.3 --- Electroplating industries in Hong Kong --- p.7 / Chapter 1.1.4 --- "Chemistry, biochemistry and toxicity of selected metal ions: copper, nickel and zinc" --- p.8 / Chapter a. --- Copper --- p.10 / Chapter b. --- Nickel --- p.11 / Chapter c. --- Zinc --- p.12 / Chapter 1.1.5 --- Conventional physico-chemical methods of metal ions removal from industrial effluent --- p.13 / Chapter a. --- Ion exchange --- p.14 / Chapter b. --- Precipitation --- p.14 / Chapter 1.1.6 --- Alternative for metal ions removal from industrial effluent: biosorption --- p.15 / Chapter a. --- Definition of biosorption --- p.15 / Chapter b. --- Mechanisms involved in biosorption of metal ions --- p.17 / Chapter c. --- Criteria for a good metal sorption process and advantages of biosorption for removal of heavy metal ions --- p.19 / Chapter d. --- Selection of potential biosorbent for metal ions removal --- p.20 / Chapter 1.1.7 --- Procedures of biosorption --- p.23 / Chapter a. --- Basic study --- p.23 / Chapter b. --- Pilot-scale study --- p.25 / Chapter c. --- Examples of commercial biosorbent --- p.27 / Chapter 1.1.8 --- Seaweed as a potential biosorbent for heavy metal ions --- p.27 / Chapter 1.2 --- Objectives of study --- p.30 / Chapter 2. --- Materials and Methods --- p.33 / Chapter 2.1 --- Collection of seaweed samples --- p.33 / Chapter 2.2 --- Processing of seaweed biomass --- p.33 / Chapter 2.3 --- Chemicals --- p.33 / Chapter 2.4 --- Characterization of seaweed biomass --- p.39 / Chapter 2.4.1 --- Moisture content of seaweed biomass --- p.39 / Chapter 2.4.2 --- Metal ions content of seaweed biomass --- p.39 / Chapter 2.5 --- Characterization of metal ions biosorption by seaweed --- p.39 / Chapter 2.5.1 --- Effect of biomass weight and selection of biomass --- p.39 / Chapter 2.5.2 --- Effect of pH --- p.40 / Chapter 2.5.3 --- Effect of retention time --- p.41 / Chapter 2.5.4 --- Effect of metal ions concentration --- p.41 / Chapter 2.5.5 --- Effect of mix-cations and mix-anions on the removal capacity of selected metal ions by Ulva lactuca --- p.43 / Chapter 2.5.6 --- Recovery of adsorbed metal ions from Ulva lactuca (I): screening for suitable desorbing agents --- p.44 / Chapter 2.5.7 --- Recovery of adsorbed metal ions from Ulva lactuca (II): multiple adsorption-desorption cycles of selected metal ions --- p.45 / Chapter 2.5.8 --- Removal and recovery of selected metal ions from electroplating effluent by Ulva lactuca --- p.45 / Chapter 2.6 --- Statistical analysis of data --- p.46 / Chapter 3. --- Results --- p.47 / Chapter 3.1 --- Effect of biomass weight and selection of biomass --- p.47 / Chapter 3.1.1 --- Effect of biomass weight --- p.47 / Chapter 3.1.2 --- Selection of biomass --- p.58 / Chapter 3.2 --- Effect of pH --- p.58 / Chapter 3.2.1 --- Cu2+ --- p.58 / Chapter 3.2.2 --- Ni2+ --- p.61 / Chapter 3.2.3 --- Zn2+ --- p.61 / Chapter 3.2.4 --- Determination of optimal condition for biosorption of Cu2+ ，Ni2+ and Zn2+ by Ulva lactuca --- p.67 / Chapter 3.3 --- Effect of retention time --- p.67 / Chapter 3.4 --- Effect of metal ions concentration --- p.73 / Chapter 3.4.1 --- Relationship of removal capacity with initial concentration of metal ions --- p.73 / Chapter 3.4.2 --- Langmuir adsorption isotherm --- p.73 / Chapter 3.4.3 --- Freundlich adsorption isotherm --- p.77 / Chapter 3.5 --- Effect of mix-cations and mix-anions on the removal capacity of selected metal ions by Ulva lactuca --- p.81 / Chapter 3.5.1 --- Effect of mix-cations --- p.81 / Chapter 3.5.2 --- Effect of mix-anions --- p.85 / Chapter 3.6 --- Recovery of adsorbed metal ions from Ulva lactuca (I): screening of suitable desorbing agents --- p.91 / Chapter 3.6.1 --- Cu2+ --- p.91 / Chapter 3.6.2 --- Ni2+ --- p.91 / Chapter 3.6.3 --- Zn2+ --- p.91 / Chapter 3.7 --- Recovery of adsorbed metal ions from Ulva lactuca (II): multiple adsorption-desorption cycles of selected metal ions --- p.94 / Chapter 3.8 --- Removal and recovery of selected metal ions from electroplating effluent by Ulva lactuca --- p.97 / Chapter 4. --- Discussion --- p.106 / Chapter 4.1 --- Effect of biomass weight and selection of biomass --- p.106 / Chapter 4.1.1 --- Effect of biomass weight --- p.106 / Chapter 4.1.2 --- Selection of biomass --- p.107 / Chapter 4.2 --- Effect of pH --- p.109 / Chapter 4.3 --- Effect of retention time --- p.112 / Chapter 4.4 --- Effect of metal ions concentration --- p.114 / Chapter 4.4.1 --- Relationship of removal capacity with initial concentration of metal ions --- p.114 / Chapter 4.4.2 --- Langmuir adsorption isotherm --- p.114 / Chapter 4.4.3 --- Freundlich adsorption isotherm --- p.115 / Chapter 4.4.4 --- Insights from isotherm study --- p.117 / Chapter 4.5 --- Effect of mix-cations and mix-anions on the removal capacity of selected metal ions by Ulva lactuca --- p.118 / Chapter 4.5.1 --- Effect of mix-cations --- p.118 / Chapter 4.5.2 --- Effect of mix-anions --- p.120 / Chapter 4.6 --- Recovery of adsorbed metal ions from Ulva lactuca (I): screening of suitable desorbing agents --- p.122 / Chapter 4.7 --- Recovery of adsorbed metal ions from Ulva lactuca (II): multiple adsorption-desorption cycles of selected metal ions --- p.124 / Chapter 4.8 --- Removal and recovery of selected metal ions from electroplating effluent by Ulva lactuca --- p.126 / Chapter 5. --- Conclusion --- p.131 / Chapter 6. --- Summary --- p.134 / Chapter 7. --- References --- p.134 / Chapter 8. --- Appendixes --- p.144

by Ma Suet-yee. / Thesis (M.Phil.)--Chinese University of Hong Kong, 2002. / Includes bibliographical references (leaves 119-131). / Abstracts in English and Chinese. / Acknowledgment --- p.i / Abstract --- p.ii / 摘要 --- p.iv / Table of Contents --- p.vi / List of Tables --- p.x / List of Figures --- p.xii / Chapter Chapter 1 --- Introduction --- p.1 / Chapter 1.1 --- Ganoderma lucidum --- p.1 / Chapter 1.1.1 --- History of Ganoderma lucidum --- p.1 / Chapter 1.1.2 --- Classification --- p.1 / Chapter 1.1.3 --- Macroscopic and microscopic structure --- p.2 / Chapter 1.1.4 --- Ganoderma lucidum as a pathogen --- p.3 / Chapter 1.1.5 --- Availability of tree hosts in Hong Kong --- p.4 / Chapter 1.1.6 --- Medicinal effects --- p.5 / Chapter 1.2 --- Study of Populations in Fungi --- p.6 / Chapter 1.2.1 --- Definition of Population --- p.6 / Chapter 1.2.2 --- Study of Fungal Populations --- p.7 / Chapter 1.2.3 --- Techniques for Population Studies in Fungi --- p.7 / Chapter 1.2.3.1 --- Somatic Incompatibility Test / Chapter 1.2.3.2 --- Isozyme Analysis / Chapter 1.2.3.3 --- Restriction Fragment Length Polymorphisms (RFLPs) / Chapter 1.2.3.4 --- Polymerase Chain Reaction (PCR) Amplification / Chapter 1.3 --- Mitochondrial DNA (mt-DNA) in Fungi --- p.14 / Chapter 1.3.1 --- Inheritance in mt-DNA --- p.15 / Chapter 1.3.2 --- Mitochondrial DNA in Population Studies --- p.15 / Chapter 1.3.2.1 --- Mitochondrial small-subunit (mt-SSU) rDNA / Chapter 1.3.2.2 --- Cytochrome oxidase 3 (cox3) / Chapter 1.4 --- Biodiversity study on Ganoderma species --- p.19 / Chapter 1.5 --- Environment Pollutants in Hong Kong --- p.20 / Chapter 1.5.1 --- Air quality in Hong Kong --- p.20 / Chapter 1.5.2 --- Soil quality in Hong Kong --- p.20 / Chapter 1.5.3 --- Toxicity of pollutants --- p.23 / Chapter 1.5.4 --- Accumulation of heavy metals by G. lucidum --- p.26 / Chapter 1.6 --- Objectives of Study --- p.27 / Chapter 1.7 --- Project Strategies --- p.28 / Chapter 1.7.1 --- Survey on distribution and collection of Ganoderma lucidum in Hong Kong --- p.28 / Chapter 1.7.2 --- Genetic divergences of G. lucidum mitochondrial genes --- p.28 / Chapter 1.7.3 --- Contaminations on field collected G. lucidum --- p.29 / Chapter 1.8 --- Significance of Study --- p.29 / Chapter Chapter 2 --- Materials and Methods --- p.30 / Chapter 2.1 --- Collection of Ganoderma lucidum in Hong Kong --- p.30 / Chapter 2.2 --- Tissue Isolation --- p.30 / Chapter 2.3 --- Somatic Incompatibility Test --- p.36 / Chapter 2.4 --- Molecular Identification --- p.40 / Chapter 2.4.1 --- Extraction of DNA --- p.40 / Chapter 2.4.2 --- Gel electrophoresis --- p.41 / Chapter 2.4.3 --- Strain authentication by arbitrarily primed polymerase chain reaction (APPCR) --- p.41 / Chapter 2.4.4 --- PCR of mt-SSU rDNA and --- p.43 / Chapter 2.4.5 --- Sequencing of mt-SSU rDNA and cox3 --- p.44 / Chapter 2.4.6 --- Comparison of G. lucidum complex with other Ganoderma and related species / Chapter 2. 4.7 --- Phylogenetic analyses --- p.46 / Chapter 2.5 --- Investigation of pollutants in Ganoderma lucidum collected in Hong Kong --- p.46 / Chapter 2.5.1 --- Metal analysis --- p.48 / Chapter 2.5.1.1 --- Acid digestion / Chapter 2.5.1.2 --- Statistical analysis / Chapter 2.5.2 --- Organic pollutant analysis --- p.49 / Chapter Chapter 3 --- Result --- p.52 / Chapter 3.1 --- Collection of Ganoderma lucidum in Hong Kong --- p.52 / Chapter 3.1.1 --- Field observation --- p.52 / Chapter 3.1.2 --- Macroscopic characteristics --- p.52 / Chapter 3.1.3 --- Microscopic characteristics --- p.53 / Chapter 3.2 --- Somatic Incompatibility Test --- p.56 / Chapter 3.3 --- DNA fingerprints by Arbitrarily-Primed PCR --- p.57 / Chapter 3.4 --- Sequencing of mt-SSU rDNA region of G. lucidum and related species --- p.60 / Chapter 3.4.1 --- Genetic variability in mt-SSU rDNA region of G. lucidum --- p.60 / Chapter 3.4.2 --- mt-SSU rDNA region of G. lucidum and other related species --- p.61 / Chapter 3.4.3 --- Phylogenetic analysis of mt-SSU rDNA region --- p.61 / Chapter 3.5 --- Sequencing of cox3 region --- p.71 / Chapter 3.5.1 --- Genetic variability in cox3 region of G. lucidum --- p.71 / Chapter 3.5.2 --- cox3 region of G. lucidum and other related species --- p.72 / Chapter 3.5.3 --- Phylogenetic analysis of cox3 region --- p.72 / Chapter 3.6 --- Metal content of field G. lucidum --- p.82 / Chapter 3.7 --- Organic pollutants in field collected G. lucidum --- p.90 / Chapter Chapter 4 --- Discussion --- p.93 / Chapter 4.1 --- Collection of Ganoderma lucidum in Hong Kong --- p.93 / Chapter 4.1.1 --- Differentiation of G. lucidum and related species in the G lucidum species complex --- p.93 / Chapter 4.1.2 --- Field observation --- p.94 / Chapter 4.2 --- Biodiversity of populations of G. lucidum in Hong Kong --- p.95 / Chapter 4.2.1 --- Individualism of G. lucidum --- p.95 / Chapter 4.2.2 --- Genetic variability in mt-SSU rDNA region of G. lucidum --- p.96 / Chapter 4.2.3 --- Genetic variability in cox3 region of G. lucidum --- p.98 / Chapter 4.2.4 --- Lineages of G. lucidum collected in Hong Kong --- p.100 / Chapter 4.2.5 --- Cryptic phylogenetic species --- p.101 / Chapter 4.3 --- Contamination of field collected Ganoderma lucidum in Hong Kong --- p.106 / Chapter 4.3.1 --- Metal contents in field collected G. lucidum in Hong Kong --- p.106 / Chapter 4.3.1.1 --- Metal contents of G. lucidum fruiting bodies collected at each site / Chapter 4.3.1.2 --- General discussion of metals / Chapter 4.3.1.3 --- Consumption of field collected G. lucidum fruiting bodies / Chapter 4.3.2 --- Comparison of metal contents between field collected Hong Kong G. lucidum with other mushrooms collected from other places --- p.112 / Chapter 4.3.3 --- Survey of organic pollutants in field collected G. lucidum in Hong Kong --- p.113 / Chapter Chapter 5 --- Conclusion --- p.116 / Chapter Chapter 6 --- Further investigation --- p.118 / Chapter Chapter 7 --- Reference --- p.119

Thesis (MSc. Agriculture (Soil Science)) -- University of Limpopo, 2019 / Global shortage of fresh quality water has led to the use of treated wastewater in arid and semi-arid regions. Although, the treated wastewater has proven to be the best solution in ameliorating pressures brought by water shortage, it contains toxic heavy metals, some in high concentrations that could possibly pose health risks and degrade soil quality. Therefore, the objectives of the study were to determine the vertical and horizontal distribution of bioavailable heavy metals on virgin, cultivated and fallowed fields and to investigate the bioremediation abilities of selected soil microbes on non-essential heavy metals in cultivated and fallowed soils following irrigation with treated wastewater at University of Limpopo (UL) Experimental Farm. Three fields, namely, virgin field (VF), cultivated field (CF) and fallowed field (FF), each being 6.4 ha, were each divided into 40 equal grids, equivalent to 40 m × 40 m, which were used in vertical assessment of heavy metals. Soil profiles were established inside each grid and soil samples collected at 0-20; 20-40 and 40-60 cm soil depth for further laboratory analysis. The soil samples were analyzed for basic soil physico-chemicals, namely, particle size distribution, soil pH (H20 and KCl), electrical conductivity (EC), reduction potential (Eh), organic carbon (OC) and cation exchange capacity (CEC). Five essential heavy metals namely zinc (Zn), iron (Fe), copper (Cu), cobalt (Co), manganese (Mn) and five non-essential heavy metals, namely, arsenic (As), chromium (Cr), lead (Pb), aluminium (Al), and cadmium (Cd), were also extracted from the soil samples. Heavy metal resistant Gram-negative (–) and Gram-positive (+) bacteria were isolated from the soil and identified as Providencia rettgeri (–), Enterobacter cloacae (–), Bacillus cereus (+) and Arthrobacter aurescens (+). xix The isolated bacteria were cultured and inoculated in heavy metal-contaminated soils and incubated for 12 weeks to bioremediate the non-essential heavy metals. Results obtained suggested that the treatments had no significant (P ≤ 0.05) effects on vertical distribution of all the essential and non-essential heavy metals among the three fields. However, on average Co was above the permissible level at 53 mg/kg in CF at 0-20 cm and although all the other essential heavy metals increased, they were still within the permissible levels. The concentration of As was also above the permissible levels in CF with an average concentration of 4.30 mg/kg. Cadmium levels were also above the permissible levels in CF with an average concentration of 1.146 mg/kg in CF and this increased by 0.46 units from VF which had an average value of 1 mg/kg. However, fallowing reduced Cd to 0.51 mg/kg which was below or within the expected limits in soil previously irrigated with treated waste water. Gram-positive bacteria reduced more concentrations of non-essential heavy metals separately and combined, especially in the fallowed field. Irrigation with treated wastewater has shown to have both negative and positive effects on the concentration of essential and non-essential heavy metals in cultivated and fallowed fields. Bioremediation coupled with fallowing has been proven to be the best solution in ameliorating heavy metal toxicity while naturally improving the quality of the soil. / National Research Foundation (NRF)

Graduation date: 1993

Doctorat en Sciences / info:eu-repo/semantics/nonPublished

M.Sc. / The Vaal Dam subcatchment is located in the upper reaches of the Vaal River. As a result the water quality is reasonably good. In contrast the Vaal River Barrage catchment includes the PWV area, resulting in poorer water quality. During this study, a fish Health Assessment Index (HAI) successfully tested in previous studies on the Olifants River System was applied to the Vaal River System. The aim was to determine if the HAI could distinguish between the Vaal Dam and Vaal River Barrage with regards to water quality. Surveys were conducted bimonthly from November 1998 to February 2000. Physical water quality variables were measured. Water and sediment samples were also collected and analyzed (Institute for Water Quality Studies, Department of Water Affairs and Forestry) to verify the HAI results. Rand Water Board and the Department of Water Affairs and Forestry also made water quality data available. Twenty sharptooth catfish, Clarias gariepinus, were collected from both localities with the aid of gill nets. Fish were checked for external parasites on the boat. On land fish were weighed and measured, after which blood was drawn and slime smears made. Blood and slime smears were examined under a light microscope for parasites. The HAI examination was performed after severing the spinal cord. Internal parasite numbers were recorded. From the parasite data collected infestation statistics were calculated. Four variations of the Parasite Index (PI) were incorporated in the HAI and results compared. During each survey gill arch, gill filament, muscle, skin and liver tissues were collected from each fish. These were analyzed for strontium, aluminium, chromium, manganese, iron, lead, copper, zinc and nickel concentrations using atomic absorption spectrophotometry. Differences in water and sediment trace metal concentrations between localities were small. Metal concentrations in fish tissues recorded from both localities were also almost identical. Possible explanations for this trend were discussed in the relevant section. Highest metal concentrations were generally recorded in gill tissue followed by liver, skin and muscle. Physical water quality variables (salinity and conductivity), and macro water analysis (e.g. phosphate and nitrate) indicated that water quality at the Vaal River Barrage was poorer. The HAI confirmed this. Higher index values were recorded from the Vaal River Barrage, with the converse being true for the Vaal Dam. Regression analysis indicated that plasma protein, haematocrit and the index value obtained using the Inverted Parasite Index, most successfully predicted (70 %) from where a randomly chosen fish were collected. When viewing index values obtained using the four versions of the PI, all four distinguished between localities. The discriminatory ability of the Inverted PI was slightly higher than that of the other PI's. It is concluded that the HAI distinguished successfully between the Vaal Dam and Vaal River Barrage on the grounds of water quality. Poor fish health correlated with decreasing water quality (salinity and eutrophication).

Heavy metal pollution in water and soil is a serious concern to human health and the associated environment. Some heavy metals have bio-importance but the bio-toxic effects of many of them in human health are of great concern. Hence, there was a need for proper understanding of the concentration levels of these heavy metals in ground water and soil around the community residing in the vicinity of the defunct mine. Mining has become prominent in this area because of the existence of copper lodes, veins and veinlets. It was therefore necessary to assess these selected metals associated with copper mining as their concentration has a tendency to affect the environment and human health. The objective of this study was to establish the levels of lead (Pb)-zinc (Zn)-copper (Cu)-arsenic (As)-nickel (Ni) metals in ground water and soil associated with an old copper mine in the vicinity of the township and to compare them with the South African and international standards in order to safeguard the health of the community using such water for drinking purpose. Clean sampling plastic bottles were used to collect water from five water boreholes being used at present. Water samples were filtered using membrane filtration set LCW (0.45 μm). The samples were digested sequentially with different procedures for the total metal concentration. Concentrations of four metals commonly associated with Cu mining were examined at five different water boreholes which are used for drinking and industrial purposes. Flame Atomic Absorption Spectrophotometer (Perkin Elmar S/n 000003F6067A, Singapore) was used to analyze metals in water samples at Eskom Ga-Nala Laboratory: pH, electrical conductivity and turbidity were analyzed using an auto titrator meter (AT- 500,Japan), conductivity meter (Cole-parmer® YO-19601-00) and turbidity meter (AL 250TIR, Agua lytic, German) respectively. Soil samples were collected from the selected areas where human health is of a serious concern, and a hand held auger drill was used to recover samples, while shovels were used to prepare the sampling area. The samples were sieved up to 63.0 μm particle size and digested with aqua-regia. Flame Atomic Absorption Spectrophotometer (Model: AA400; Year: 2008; Manufacturer: Perkin Elmer; Germany; Serial no: 201S6101210) was used at the University of Venda Laboratory to analyze soil from the study area for possible heavy metal contamination due to the defunct Cu mine in the area. v The results showed variation of the investigated parameters in water samples as follows: pH, 6.0 to 7.51; EC, 70.0 to 96.40 μS/cm and turbidity, 1.05 to 4.56 NTU. The mean concentration of the metals increased in the followed order: Pb<Cu<As<Ni. Ni is the most abundant in the ground water determined with value of (6.49 μg/g). The observations have confirmed that most ground water contains an appreciable quantity of Ni. The mean value of As in water is (4.20 to 4.84 μg/g), Pb and Cu have (2.13 to 2.58 μg/g) and (1.52 to 2.52 μg/g) respectively. For soil samples, the mean concentration of the metals increased in the following order: Pb<Cu<Zn<As<Ni. Pb ranged from (0.023 to 0.036 μg/g) followed by Cu (0.28 to 0.45 μg/g) then Zn (0.026 to 0.053 μg/g), the mean range of As in soil ranged from (0.054 to 0.086 μg/g). However, some studies show much higher contamination of As from the natural sources and Ni with (0.057 to 0.144 μg/g) lastly. Accumulation of heavy metals in soil is of concern due to their toxic effects on human and animals. The quality of ground water from the five boreholes studied was satisfactory with turbidity (T), electrical conductivity (EC) and heavy metals (HM’s) below the WHO limit. The water therefore may, according to the WHO Standards be safely used as a drinking water. The concern lies on pH which was slightly (0.5) below the standard. There is a serious need to monitor the ground water which is now used for drinking purposes. This study revealed that heavy metal pollution in soil from the abandoned Cu mine in Musina is a threat to the health of the community. Although pollution was between medium and low in the contamination index, it is therefore important for the Musina Municipality or mine owner of Musina (TVL) Development Co Ltd copper mine to advocate possible remedial actions which will safeguard the environment and human health. The tailing at Musina’s old Cu mine have high pH and they lack normal soil stabilization processes, as a result the tailing does not develop a good plant cover. Pollution of the ground water resources is also evident in the study area where there is seepage or ingress of polluted water to the underground aquifers. Small-scale mining in Musina is causing further degradation to the environment but it supports the South African Waste Hierarchy by promoting the reuse and recycling of the tailing and mine dumps for the production of bricks. Mine workers are exposed to the above mentioned toxic heavy metals daily. Medicine will not help stop the poisoning. The only way to stop the metal poisoning is to stop being exposed to the heavy metals. / Environmental Sciences / M. Sc. (Environmental Management)