Ravidomycin is a yellow antitumor antibiotic produced by Streptomyces ravidus. Ravidomycin shows strong antitumor activity against P388 lymphocytic leukemia, the colon 38 tumor, and the CD8Fl mammary tumor. It is also very active against Gram positive bacteria. Biosynthetic studies have shown that the aglycone unit comes from the folding of a polyketide chain with the vinyl unit arising from propionic acid. Since this vinyl functionality is believed to playa role in the antitumor activity of the antibiotic, it is of interest to elucidate the stereochemical selectivity in its formation from propionic acid. The synthesis of (R) and (S)-L2-²H₁ j propionate, incorporation of the labelled material, and chemical analysis of the resulting antibiotic was be used to determine the stereochemistry of formation of the vinyl side chain. It was found that propionate was incorporated with ravidomycin with stereospecific loss of the 2-(pro-R)-proton. / Master of Science

Thesis (MTech (Chemistry))--Cape Peninsula University of Technology, 2016. / Polycyclic aromatic hydrocarbons (PAHs) are an alarming group of organic substances for humans and environmental organisms due to their ubiquitous presence, toxicity, and carcinogenicity. They are semi-volatile substances which result from the fusion of carbon and hydrogen atoms and constitute a large group of compounds containing two to several aromatic rings in their molecule. Natural processes and several anthropogenic activities involving complete or incomplete combustion of organic substances such as coal, fossil fuel, tobacco and other thermal processes, generally result in the release of the PAHs into the environment. However, the fate of the PAHs is of great environmental concern due to their tendency to accumulate and their persistence in different environmental matrices and their toxicity. Animal studies have revealed that an excessive exposure to PAHs can be harmful. Evidence of their carcinogenic, mutagenic, and immune-suppressive effects has been reported in the literature. In the soil environment, they have the tendency to be absorbed by plants grown on soil being contaminated by the PAHs. It is, therefore, important to evaluate their occurrence levels in different environmental matrices such as soil concentrations.

Canadian bitumen is mainly transported in a diluted form via pipeline and train, all posing a risk as they can lead to the release of diluted bitumen (dilbit) in the environment. In the summer of 2018, a collaborative large-scale field experiment was conducted at the International Institute for Sustainable Development - Experimental Lakes Area (IISD-ELA), a world-renowned aquatic research facility. The research objectives of the Boreal lake Oil Release Experiment by Additions to Limnocorrals (BOREAL) project were to understand the fate, behaviour, and potential toxic effects of dilbit in a freshwater Boreal lake to inform evidence-based management strategies for the transport of dilbit. A range of controlled dilbit spills was performed in seven 10 m diameter limnocorrals (~100,000 L of water) resulting in environmentally realistic dilbit:water dilutions ranging from 1:69,200 to 1:504, representing the upper half of the distribution of oil spill sizes in North America in the last decade. Additionally, two limnocorrals not treated with dilbit were studied as controls. This thesis identifies the bioaccumulating compounds derived from naturally weathered dilbit in adult giant floater mussels (Pyganodon grandis), to determine the rates at which they were accumulated and excreted. More specifically, the bioaccumulation potential and toxicokinetic parameters of polycyclic aromatic compounds (PACs) and various metals were assessed in mussels exposed ex situ for 41 days (25 days of exposure and 16 days of depuration) to water from the limnocorrals. These compounds have shown to be toxic, carcinogenic, and mutagenic to aquatic organisms. Mussels exposed to dilbit-contaminated water experienced significantly greater TPACs concentrations (0.40 – 0.90 µg L-1, n=12) compared to mussels from the Control (0.017 µg L-1, n=4). Furthermore, dilbit-contaminated water had a higher proportion of alkylated PACs compared to their parent counterpart, demonstrating petrogenic PAC profiles. We detected significantly greater TPACs concentrations in mussels exposed to dilbit-contaminated water (25.92 – 27.79 µg g-1, ww Lipid, n=9, at day 25 of the uptake phase) compared to mussels from the Control (average of 2.62 ± 1.95 µg g-1, ww Lipid; ±SD, n=17). Alkylated PACs represented 96.4 ± 1.8%, ±SD, n=12 of TPACs in mussels from dilbit-contaminated treatments at day 25 of the uptake phase, indicating the importance of conducting a more inclusive assessment of petrochemical mixtures as most studies only focus on parent PACs. From first-order one-compartment models derived from nonlinear curve fitting of the accumulation phase or sequential modelling method, uptake (0.66 – 24.65 L g-1 day-1, n=87) and depuration (0.012 – 0.37 day-1, n=87) kinetic rate constants, as well as bioconcentration factors (log values from 3.85 – 6.12 L kg-1, n=87) for the 29 PACs that bioaccumulated in mussels suggested that alkylated PACs have greater bioaccumulation potential compared to their parent PAC counterpart. Results from this study also demonstrated that giant floater mussels could be used to biomonitor PAC contamination following oil spills as PACs accumulated in mussel tissue and were still present following the 16 day depuration phase. The results of this study are the largest, most comprehensive set of toxicokinetic and bioaccumulation information of PACs (44 analytes) in freshwater mussels obtained to date. Metal contamination following the controlled dilbit spill was minimal, but mussels exposed to water contaminated with naturally weathered dilbit experienced elevated concentrations of dissolved zinc (30.26 – 38.26 µg L-1, n=12) compared to the mussels in the uncontaminated water (6.75 ± 3.31 µg L-1, n=4), surpassing the Canadian water quality guidelines for the protection of aquatic life. However, it is not clear if dilbit contamination caused elevated zinc concentrations in the water as other factors, such as limnocorral building materials and/or galvanized minnow traps used in the limnocorrals, could have contributed to zinc contamination. Nonetheless, giant floater mussels did not accumulate zinc in their tissues.

Polycyclic (or polynuclear) aromatic hydrocarbons (PAHs) are environmental pollutants produced during the incomplete combustion of organic matter. Since many of these compounds have been shown to be mutagenic and/or carcinogenic, an investigation was initiated into determining the PAH content and mutagenicity of the ash that remains after sugar cane crop burning, and the soot deposited on toll booths by vehicle exhaust emissions. Due to the large amount of sugar cane farming in the Natal coastal region and that the favoured method of disposing unwanted leafy trash is crop burning, concern was expressed as to the nature of the residue that is formed. PAHs have been identified in the residues from combusted wood and straw and, due to their intrinsic similarity to sugar cane, it was considered that the burning of sugar cane could generate PAHs. It is well documented that vehicle exhaust emissions exhibit mutagenic properties and PAHs have been identified as the major contributors of this observed mutagenicity. Since a toll plaza is an area of high traffic density, it was considered to be an ideal location for an investigation into the build-up of particles emitted by the passing vehicles, and to study to what extent the operators are exposed to harmful compounds. In addition, this sample acted as a control, since the detection of PAHs and mutagenic activity in the soot would be an indication that the correct experimental techniques were being employed. Samples were collected on site. The sugar cane ash was collected off a field immediately after burning had taken place, and the soot was collected either by scraping the toll booth walls and surrounding areas or by wiping the surfaces with cotton wool swabs. The organic portion of the samples was separated from the inorganic and carbonaceous substances by extraction into a suitable solvent; the use of both acetone and dichloromethane was investigated. The extracts were divided into two portions - one was used for the analysis of PAHs and the other for determining mutagenic activity. Analysis for PAHs involved subjecting the extracts to a sample clean-up routine and the use of a number of analytical techniques to characterise the components. The mutagenic properties of the samples were investigated by means of two bacterial mutagenicity tests: the Salmonella typhimurium assay (the Ames test) and a new commercially available test kit, the SOS Chromotest. A number of PARs were identified in the extracts by means of reverse phase high performance liquid chromatography (HPLC) with both ultraviolet and fluorescence detection, the latter being the more sensitive method. Mutagenic activity was detected for both samples in the Ames test and for the toll booth soot in the SOS Chromotest, and this observed mutagenicity was attributed to the presence of the PAHs. / Thesis (M.Sc.)-University of Natal, Durban, 1992.

by Chan Sze Sze. / Thesis (M.Phil.)--Chinese University of Hong Kong, 2005. / Includes bibliographical references (leaves 193-218). / Abstracts in English and Chinese. / Acknowledgements --- p.i / Abstracts --- p.ii / 摘要 --- p.v / Contents --- p.viii / List of figures --- p.xv / List of tables --- p.xix / Abbreviations --- p.xxii / Chapter 1 --- Introduction --- p.1 / Chapter 1.1 --- The North Tsing Yi Abandoned Shipyard area --- p.1 / Chapter 1.2 --- Polycyclic aromatic hydrocarbons (PAHs) in the site --- p.3 / Chapter 1.2.1 --- Characteristics of PAHs --- p.3 / Chapter 1.2.2 --- Sources of PAHs --- p.8 / Chapter 1.2.3 --- Environmental fates of PAHs --- p.9 / Chapter 1.2.4 --- Biodegradation of PAHs --- p.10 / Chapter 1.2.5 --- Toxicity of PAHs --- p.13 / Chapter 1.2.6 --- PAHs contamination in Hong Kong --- p.14 / Chapter 1.2.7 --- Soil decontamination assessment in Hong Kong --- p.16 / Chapter 1.2.8 --- Environmental standards of PAHs --- p.18 / Chapter 1.2.9 --- Remediation technology of PAHs --- p.21 / Chapter 1.2.9.1 --- Bioremediation --- p.22 / Chapter 1.3 --- Heavy metals in the site --- p.28 / Chapter 1.3.1 --- "Characteristics of copper, lead and zinc" --- p.29 / Chapter 1.3.2 --- "Sources of copper, lead and zinc" --- p.32 / Chapter 1.3.3 --- "Environmental fates of copper, lead and zinc" --- p.34 / Chapter 1.3.4 --- "Toxicities of copper, lead and zinc" --- p.36 / Chapter 1.3.5 --- "Copper, lead and zinc contamination in Hong Kong" --- p.39 / Chapter 1.3.6 --- "Environmental standards of copper, lead and zinc" --- p.40 / Chapter 1.3.7 --- Remediation technology of heavy metal --- p.42 / Chapter 1.3.7.1 --- Chemical method --- p.42 / Chapter 1.3.7.2 --- Biological method --- p.43 / Chapter 1.3.7.3 --- Stabilization and Solidification --- p.45 / Chapter 1.4 --- Aim of study --- p.47 / Chapter 1.5 --- Objectives --- p.47 / Chapter 1.6 --- Research Strategy --- p.47 / Chapter 1.7 --- Significance of study --- p.48 / Chapter 2 --- Materials and Methods --- p.49 / Chapter 2.1 --- Soil Collection --- p.49 / Chapter 2.2 --- Characterization of soil --- p.49 / Chapter 2.2.1 --- Sample preparation --- p.49 / Chapter 2.2.2 --- "Soil pH, electrical conductivity & salinity" --- p.50 / Chapter 2.2.3 --- Total organic carbon contents --- p.51 / Chapter 2.2.4 --- Soil texture --- p.51 / Chapter 2.2.5 --- Moisture --- p.53 / Chapter 2.2.6 --- Total nitrogen and total phosphorus --- p.53 / Chapter 2.2.7 --- Available nitrogen --- p.53 / Chapter 2.2.8 --- Available phosphorus --- p.54 / Chapter 2.2.9 --- Soil bacterial and fungal population --- p.54 / Chapter 2.2.10 --- Extraction of PAHs and organic pollutants --- p.55 / Chapter 2.2.10.1 --- Extraction procedure --- p.55 / Chapter 2.2.10.2 --- GC-MS condition --- p.56 / Chapter 2.2.10.3 --- Preparation of mixed PAHs stock solution --- p.56 / Chapter 2.2.11 --- Oil and grease content --- p.57 / Chapter 2.2.12 --- Total Petroleum Hydrocarbons (TPH) --- p.57 / Chapter 2.2.13 --- Total heavy metal analysis --- p.58 / Chapter 2.2.14 --- Toxicity characteristic leaching procedure (TCLP) --- p.59 / Chapter 2.2.15 --- Extraction efficiency --- p.59 / Chapter 2.3 --- Production of mushroom compost --- p.60 / Chapter 2.4 --- Characterization of mushroom compost --- p.62 / Chapter 2.4.1 --- Enzyme assay --- p.62 / Chapter 2.4.1.1 --- Laccase assay --- p.62 / Chapter 2.4.1.2 --- Manganese peroxidase assay --- p.62 / Chapter 2.5 --- Addition of mushroom to soil on site --- p.63 / Chapter 2.5.1 --- Transportation of mushroom compost to Tsing Yi --- p.63 / Chapter 2.5.2 --- Mixing of mushroom compost and soil --- p.64 / Chapter 2.6 --- Soil Monitoring --- p.64 / Chapter 2.6.1 --- On site air and soil measurements --- p.64 / Chapter 2.6.1.1 --- Air temperature and moisture --- p.64 / Chapter 2.6.1.2 --- Light intensity --- p.64 / Chapter 2.6.1.3 --- UV intensity --- p.65 / Chapter 2.6.1.4 --- Rainfall --- p.65 / Chapter 2.6.1.5 --- Soil temperature --- p.65 / Chapter 2.6.2 --- Soil chemical characteristic --- p.65 / Chapter 2.6.3 --- Relative residue pollutant (%) --- p.65 / Chapter 2.7 --- Toxicity of treated soil --- p.66 / Chapter 2.7.1 --- Seed germination test --- p.66 / Chapter 2.7.2 --- Indigenous bacterial toxicity test --- p.67 / Chapter 2.7.3 --- Fungal toxicity test --- p.68 / Chapter 2.7.3.1 --- Preparation of ergosterol standard solution --- p.70 / Chapter 2.8 --- Soil Washing --- p.70 / Chapter 2.8.1 --- Optimization of soil washing --- p.70 / Chapter 2.8.1.1 --- Effect of hydrochloric acid concentration --- p.70 / Chapter 2.8.1.2 --- Effect of incubation time --- p.71 / Chapter 2.9 --- Phytoremediation --- p.71 / Chapter 2.10 --- Mycoextraction --- p.72 / Chapter 2.11 --- Integrated bioextraction --- p.72 / Chapter 2.12 --- Cementation --- p.73 / Chapter 2.13 --- Glass encapsulation --- p.73 / Chapter 2.14 --- Statistical analysis --- p.74 / Chapter 3 --- Results --- p.75 / Chapter 3.1 --- Characterization of soil --- p.75 / Chapter 3.2 --- Characterization of mushroom compost --- p.78 / Chapter 3.2.1 --- Enzyme activity --- p.78 / Chapter 3.2.2 --- Total nitrogen and total phosphorus contents --- p.78 / Chapter 3.3 --- Soil monitoring --- p.79 / Chapter 3.3.1 --- Initial pollutant content in biopile and fungal treatment soils --- p.79 / Chapter 3.3.2 --- On site air and soil physical characteristics --- p.81 / Chapter 3.3.2.1 --- Soil temperature and air temperature --- p.81 / Chapter 3.3.3 --- Soil chemical characteristic --- p.84 / Chapter 3.3.3.1 --- Effect of type of treatment on total petroleum hydrocarbon content --- p.85 / Chapter 3.3.3.2 --- Effect of type of treatment on oil and grease content --- p.87 / Chapter 3.3.3.3 --- Soil pH --- p.89 / Chapter 3.3.3.4 --- Moisture --- p.91 / Chapter 3.3.3.5 --- Electrical conductivity --- p.92 / Chapter 3.3.3.6 --- Salinity --- p.93 / Chapter 3.3.3.7 --- Microbial population --- p.95 / Chapter 3.3.3.8 --- Removal of organopollutant PAHs in biopile and fungal treatment --- p.98 / Chapter 3.3.3.9 --- Effect of type of treatment on residual PAHs at Day 4 --- p.104 / Chapter 3.3.3.10 --- Effect of type of treatment on residual PAHs at peak levels --- p.107 / Chapter 3.3.3.11 --- Effect of type of treatment on residual organopollutants at the end of treatments --- p.109 / Chapter 3.3.3.12 --- Effect of type of treatment on total nitrogen and phosphorus contents --- p.111 / Chapter 3.3.3.13 --- Effect of type of treatment on physical and chemical properties of soil --- p.113 / Chapter 3.4 --- Toxicity of treated soil --- p.116 / Chapter 3.4.1 --- Seed germination test --- p.116 / Chapter 3.4.2 --- Indigenous bacterial toxicity test --- p.120 / Chapter 3.4.3 --- Fungal toxicity test --- p.125 / Chapter 3.5 --- Soil washing --- p.129 / Chapter 3.5.1 --- Optimisation of soil washing --- p.129 / Chapter 3.5.1.1 --- The effect of hydrochloric acid concentration --- p.129 / Chapter 3.5.1.2 --- The effect of incubation time --- p.134 / Chapter 3.6 --- Mycoextraction --- p.139 / Chapter 3.7 --- Phytoextraction and integrated bioextraction --- p.146 / Chapter 3.8 --- Cementation --- p.153 / Chapter 3.9 --- Glass encapsulation --- p.158 / Chapter 4 --- Discussion --- p.160 / Chapter 4.1 --- Characterization of soil --- p.160 / Chapter 4.2 --- Characterization of mushroom compost --- p.162 / Chapter 4.2.1 --- Enzyme activity --- p.162 / Chapter 4.2.2 --- Total nitrogen and total phosphorus contents --- p.163 / Chapter 4.3 --- Soil monitoring --- p.163 / Chapter 4.3.1 --- Initial pollutant content in biopile and fungal treatment soil --- p.163 / Chapter 4.3.2 --- On site air and soil physical characteristics --- p.164 / Chapter 4.3.3 --- Soil chemical characteristic --- p.164 / Chapter 4.3.3.1 --- Soil pH --- p.164 / Chapter 4.3.3.2 --- Moisture --- p.165 / Chapter 4.3.3.3 --- Electrical conductivity --- p.165 / Chapter 4.3.3.4 --- Salinity --- p.166 / Chapter 4.3.3.5 --- Microbial population in biopile and fungal treatments --- p.166 / Chapter 4.3.3.6 --- Removal of organopollutant PAHs in biopile and fungal treatments --- p.168 / Chapter 4.3.3.7 --- Effect of type of treatment on residual PAHs at peak levels --- p.170 / Chapter 4.3.3.8 --- Effect of type of treatment on residual oil and grease and TPH contents --- p.171 / Chapter 4.3.3.9 --- Effect of type of treatment on total nitrogen and phosphorus contents --- p.172 / Chapter 4.3.3.10 --- Effect of type of treatment on physical and chemical properties of the soil --- p.173 / Chapter 4.4 --- Toxicity of treated soil --- p.174 / Chapter 4.5 --- Summary of Pleurotus pulmonarius mushroom compost on organopollutant remediation --- p.177 / Chapter 4.6 --- Soil washing --- p.178 / Chapter 4.7 --- Mycoextraction --- p.180 / Chapter 4.8 --- Phytoextraction and integrated bioextraction --- p.182 / Chapter 4.9 --- Cementation --- p.184 / Chapter 4.10 --- Glass encapsulation --- p.185 / Chapter 4.11 --- "Summary of physical, chemical and biological heavy metal removal treatments" --- p.186 / Chapter 4.12 --- Future studies --- p.187 / Chapter 5 --- Conclusion --- p.190 / Chapter 6 --- References --- p.193

Zou, Huiling. / Thesis submitted in: November 2008. / Thesis (M.Phil.)--Chinese University of Hong Kong, 2009. / Includes bibliographical references (leaves 159-176). / Abstracts in English and Chinese. / Abstract --- p.i / Acknowledgements --- p.vi / Table of contents --- p.viii / List of tables --- p.x / List of figures --- p.xiii / Abbreviations --- p.xv / Chapter Chapter 1 --- Introduction / Chapter 1.1 --- Background --- p.1 / Chapter 1.1.1 --- Physicochemical properties of polycyclic aromatic hydrocarbons --- p.1 / Chapter 1.1.2 --- Sources of PAHs --- p.4 / Chapter 1.1.3 --- Toxicity of PAHs --- p.5 / Chapter 1.1.4 --- Fate of PAHs in environment --- p.6 / Chapter 1.1.5 --- Soil physicochemical and microbiological properties --- p.16 / Chapter 1.1.6 --- Geography and climate of Hong Kong --- p.17 / Chapter 1.1.7 --- Traffic status in Hong Kong --- p.17 / Chapter 1.1.8 --- Research status in Hong Kong --- p.18 / Chapter 1.2 --- "Significant, objectives and outline of this study" --- p.18 / Chapter 1.2.1 --- Research significance --- p.18 / Chapter 1.2.2 --- Research objectives and thesis outline --- p.19 / Chapter Chapter 2 --- PAH concentrations and their seasonal variations in roadside soils in Hong Kong / Chapter 2.1 --- Introduction --- p.20 / Chapter 2.2 --- Materials and methods --- p.22 / Chapter 2.2.1 --- Soil sampling --- p.22 / Chapter 2.2.2 --- Soil physicochemical properties analysis --- p.24 / Chapter 2.2.3 --- Soil PAH analysis --- p.25 / Chapter 2.2.3.1 --- Extraction of PAHs --- p.25 / Chapter 2.2.3.2 --- Cleanup and concentration of the extract --- p.25 / Chapter 2.2.3.3 --- Determination of PAHs --- p.26 / Chapter 2.2.3.4 --- Calibration standards and recovery --- p.26 / Chapter 2.2.4 --- Statistical analysis --- p.28 / Chapter 2.3 --- Results and discussion --- p.29 / Chapter 2.3.1 --- Soil PAH contents and their relationships with soil physicochemical properties and AADT --- p.29 / Chapter 2.3.1.1 --- Soil PAHs --- p.29 / Chapter 2.3.1.2 --- Soil physicochemical properties --- p.38 / Chapter 2.3.1.3 --- Relationships of PAH contents with soil physicochemical properties and AADT --- p.39 / Chapter 2.3.2 --- Seasonal variations of PAH contents of roadside soils --- p.50 / Chapter 2.4 --- Conclusion --- p.56 / Chapter Chapter 3 --- "PAH concentrations in roadside vegetation, dusts and soils" / Chapter 3.1 --- Introduction --- p.58 / Chapter 3.2 --- Materials and methods --- p.59 / Chapter 3.2.1 --- Sampling --- p.59 / Chapter 3.2.2 --- Soil physicochemical properties analysis --- p.60 / Chapter 3.2.3 --- PAHs analysis --- p.60 / Chapter 3.2.3.1 --- Extraction of PAHs --- p.60 / Chapter 3.2.3.2 --- Cleanup and concentration of the extract --- p.60 / Chapter 3.2.3.3 --- Determination of PAHs --- p.61 / Chapter 3.2.3.4 --- Calibration standards and recovery --- p.61 / Chapter 3.2.4 --- Statistical analysis --- p.61 / Chapter 3.3 --- Results and discussion --- p.62 / Chapter 3.3.1 --- Soil physicochemical properties --- p.62 / Chapter 3.3.2 --- PAH concentrations --- p.62 / Chapter 3.3.2.1 --- Soil PAHs --- p.62 / Chapter 3.3.2.2 --- Dust PAHs --- p.65 / Chapter 3.3.2.3 --- Vegetation PAHs --- p.71 / Chapter 3.3.3 --- PAH profile --- p.80 / Chapter 3.3.4 --- PAH sources --- p.83 / Chapter 3.3.5 --- PCA and HCA --- p.88 / Chapter 3.3.6 --- "Relationships of PAH contents between vegetation, dust and soil, and soil physicochemical properties and AADT" --- p.99 / Chapter 3.4 --- Conclusion --- p.124 / Chapter Chapter 4 --- Vertical and horizontal distribution of PAHs in roadside soil and their influences on soil microbial characteristics / Chapter 4.1 --- Introduction --- p.126 / Chapter 4.2 --- Materials and methods --- p.127 / Chapter 4.2.1 --- Sampling --- p.127 / Chapter 4.2.2 --- Soil physicochemical properties analysis --- p.128 / Chapter 4.2.3 --- Soil microbial biomass carbon analysis --- p.128 / Chapter 4.2.4 --- Soil microbial community analysis --- p.128 / Chapter 4.2.5 --- Soil enzyme activity analysis --- p.129 / Chapter 4.2.6 --- Soil PAH analysis --- p.130 / Chapter 4.2.7 --- Statistical analysis --- p.130 / Chapter 4.3 --- Results and discussion --- p.131 / Chapter 4.3.1 --- Vertical distribution --- p.131 / Chapter 4.3.2 --- Horizontal distribution --- p.137 / Chapter 4.3.3 --- Influences of roadside soil PAH on microbial characteristics --- p.142 / Chapter 4.4 --- Conclusion --- p.153 / Chapter Chapter 5 --- General conclusion / Chapter 5.1 --- Summary of findings --- p.155 / Chapter 5.2 --- Limitations of the study --- p.157 / Chapter 5.3 --- Implications for further studies --- p.158 / References --- p.159

Polycyclic aromatic hydrocarbons (PAHs) and nitrogen-containing polycyclic aromatic compound (N-PAC) are widespread toxic pollutants in environments. The fate of PAHs and N-PACs are of great concern because some of these compounds were identified as caricinogenic, mutagenic and teratogenic compounds. As described in literature, dissolved organic matter (DOM) is an important factor in control of their fate; however, the binding behaviors between these compounds and DOM are still not fully understood. The binding constants (KDOC) between humic substances and one selected N-PAC, benzo[h]quinoline, were measured at varying pH levels using fluorescence quenching (FQ) method. As fluorescence characteristics of benzo[h]quinoline change with pH, determination required two optimum sets of excitation and emission wavelength pairs. A simple mixing model was proposed and used to eliminate the inherent fluorescence interference between benzo[h]quinoline (BQ) and its protonated form, benzo[h]quinolinium (BQH+), and to deduce Kmix which represents the overall binding as the sum of that for the individual analogs. The characteristics of humic substances, especially their hydrophobicity and aromaticity, established by principal components analysis of structural and elemental compositions, were the main determinants of their binding affinity with both benzo[h]quinoline and benzo[h]quinolinium (KBQ and KBQH+) across a range of pH values. Hydrophobic interaction is likely to control the binding between humic substance and benzo[h]quinoline and benzo[h]quinolinium, in lower and higher pH ranges (pH<3, pH>6). In contrast, cation exchange seems to control on the binding affinity of benzo[h]quinolinium in the middle range of pH. Determination of PAH concentration is quite essential for investigating the fate of PAHs in environments. Microwave-assisted headspace solid-phase microextraction (MA-HS-SPME) with a polydimethylsiloxane/divinylbenzene (PDMS/DVB) fiber was applied as a single step prior to determination of PAH concentrations in water using GC-MS. To optimize the extraction efficiency of PAHs by MA-HS-SPME, the influence of various parameters, including temperature, duration of thermal desorption, microwave irradiation power and duration, and the temperature of the circulating cooling water system, was studied. The proposed method was demonstrated applicable to environmental water samples. In addition, DOM matrix effect did not influence the determination and extraction efficiency of PAHs. Although the proposed simple mixing model can eliminate the fluorescent interference of hydrophobic organic compounds with acid-base pair forms, it is still limited in using for correcting the KDOC measurement of more than two fluorescent compounds simultaneously. A new alternative protocol, complexation-flocculation combined with MA-HS-SPME/GC-MS method, was proposed to determine the binding constants of seleted PAHs to humic substances. The results obtained are comparable with KDOC data reported in literatures. CF-MA-HS-SPME/GC-MS provides some advantages over other methods, such as applicable not limited to fluorescent compounds, faster in determination and capable in measuring varieties of compounds simultaneously.

Thesis (Ph. D.)--Oregon State University, 2007. / Printout. Includes bibliographical references (leaves 102-117). Also available on the World Wide Web.

In recent years the nitrated polycyclic aromatic hydrocarbons (nitroPAH's) have been recognized as powerful mutagens in the Ames Salmonella test. Most nitroPAH’s are direct-acting mutagens in the Ames test i.e. they induce mutation in the absence of S9, and appear to be activated through nitroreduction by bacterial enzymes. Others, however, such as 3-nitroperylene, are indirect-acting mutagens and show maximum activity only when S9 is present. Studies using the Ames test have indicated that the cytochrome P-450-dependent mixed function oxidase system of S9 is responsible for the activation of 3-nitroperylene to mutagenic species. However, the pattern of P-450 isozymes involved in this process appears to be different from that involved in the conversion of most PAH's, such as the standard indirect-acting mutagen benzo(a)pyrene (B(a)P), to proximate mutagens. 6-NitroB(a)P, in contrast, behaves in an analogous manner to its parent hydrocarbon. Using appropriate Salmonella mutants, the activation of 3-nitroperylene was found to require bacterial involvement, although the nature of the bacterial contribution has yet to be determined. Studies with other mutants have indicated that nitroreduction, at least as a primary activation step, does not appear to be important. Incubation of 3-nitroperylene with high concentrations of S9 led to the formation of a number of metabolites, of which phenolic derivatives were prominent. In addition, S9-derived microsomes were able to catalyse the conversion of 3-nitroperylene to species which were able to bind to protein and DNA. Under the conditions employed in these binding studies, 3-nitroperylene appears to be acting like a simple PAH, and such experiments with very high concentrations of liver protein may be unrepresentative of the processes responsible for the mutagenesis of the compound. / Thesis / Master of Science (MSc)

Since 2008, large numbers of Nile crocodile (Crocodylus niloticus) carcasses were found in the Kruger National Park (KNP), South Africa. Most of the crocodile carcasses were found in the Olifants Gorge, which is situated below the Letaba and Olifants river confluence, before the Mozambique border and Massingir Dam. The Massingir Dam is an important resource and it plays a significant role in the welfare of the local Mozambican population. Autopsies performed on the crocodiles indicated that the adipose tissue colour changed from normal white to yellow and this is usually a sign of pansteatitis. Pansteatitis is caused by lipid peroxidation in an organism and it is characterised by the lack of vitamin E. This disease is recognisable by the hardening of the fatty tissue and yellow discolouration, and is mostly associated with aquatic organisms from polluted ecosystems. There are speculations that the crocodile fatalities may be associated with the Massingir Dam that backed up into the Olifants Gorge after flooding. After the dam was reconstructed, it flooded the Olifants Gorge, causing it to act like a localised sediment trap as the water flow slowed down and as a result, caused pollutants to build-up. Sediment samples were collected from selected rivers and ponds within the KNP. These samples were analysed for selected elements, persistent organic pollutants (POPs), and polycyclic aromatic hydrocarbons (PAHs). The sediment samples were analysed in Norway for POPs and PAHs with the use of a high-resolution gas chromatography/mass spectrometry (GC/MS) and the heavy metals were analysed in South Africa with the use of inductively-coupled plasma mass spectrometry (ICP/MS). In order to identify which elements may have affected the health of the crocodiles, a series of sediment quality indices were used. These indices made it possible to determine which elements may have been involved. The order of probability of heavy metals causing harm was Se>As>Ni>Cr>Cu>I>V>Mn>Co>Fe>Cd>Hg>Zn>Pb>Ba>U. The data was compared to selected international guidelines. All the information was used to determine which of the sampled sites had the highest contamination. The sites sampled with the highest concentrations were in the Crocodile, Nkomati, Olifants, and Letaba Rivers. Concentrations of the elements, POPs, and PAHs were also quantifiable in the Olifants Gorge. The following elements (Fe, Co, Cu, Cr, Pb, V, As, and Ni) were quantified at elevated levels and may therefore have caused negative effects on the crocodiles in the Olifants Gorge. These elevated concentrations, in combination with the dramatic change in the physical environment due to the dam, could have added additional stress that may have contributed to the observed crocodile mortalities in the Olifants Gorge. / MSc (Environmental Sciences), North-West University, Potchefstroom Campus, 2015