Enrichment cultures of microorganisms separated from soil contaminated with pentachlorophenol and creosote were able to grow on and degrade phenol (300 mg 2-chlorophenol (100 mg L⁻¹), or 4-chlorophenol (100 mg L⁻¹) when added as the sole carbon source, but were unable to degrade 3-chlorophenol (100 mg L⁻¹) even after more than 127 days of incubation. Phenol biodegradation by enrichment cultures was completely inhibited by temperatures at or above 37 °C or phenol concentrations greater than 1,200 mg L⁻¹. Phenol degradation rates were reduced in the absence of an inorganic nitrogen source. Two species of gram-negative bacterial isolates from this soil degraded 300 mg L⁻¹ phenol in three to twelve days. A yeast isolate degraded 300 mg L⁻¹ phenol more quickly, in one to three days. No isolates were found that degraded any of the chlorinated compounds. Phenol biodegradation by the yeast was completely inhibited by substrate concentrations greater than 1,000 mg L⁻¹; it was partly inhibited by low dissolved-oxygen concentrations, substrate concentrations greater than 500 mg L⁻¹, and the presence of alternative carbon sources such as acetate or glucose. Acetate also inhibited yeast growth in the presence of phenol, while glucose stimulated it. The addition of yeast extract or thiamin stimulated yeast growth and phenol degradation by the yeast. In enrichment cultures, growth factors were provided to yeast by other microorganisms. Maximum rates of phenol degradation by yeast and enrichment cultures were comparable, often greater than 300 mg L⁻¹ phenol per day. Doubling times for yeast growing on phenol were generally from three to five hours. The rapid rates of growth and phenol degradation by isolates and enrichments suggest that biodegradation of phenol in the subsurface should not be substrate limited. Rather the transport of dissolved oxygen by advection/dispersion or vertical diffusion should limit phenol degradation by aerobic metabolic pathways in groundwater.

One of the consequences of the social and economIc change due to industrialisation is the generation of industrial wastewater which requires treatment before being released into the natural aquatic environment. The municipality has wastewater treatment plants which were initially designed for the treatment of domestic wastewater. The presence of industrial wastewater in these treatment plants introduces various difficulties in the treatment process due to the complex and varying nature of the industrial wastewater. A means needs to be developed, that will allow the municipality to evaluate if a wastewater treatment plant can adequately treat a particular composition or type of wastewater to a quality suitable for release to the environment. Developing a simulation model for a wastewater treatment plant and calibrating it against plant operating data will allow the response of the wastewater treatment plant to a particular wastewater to be evaluated. In this study a model for the Mariamidge Wastewater Treatment Plant is developed in the WEST (Worldwide Engine for Simulation, Training and Automation) software package. The sources of data for modelling were laboratory experiments, historical data from the municipal laboratory and modelling of experiments. Dynamic input files representing the properties of the influent wastewater were generated by characterising the influent wastewater through the use of batch respirometric tests and flocculation filtration on composite samples of wastewater. Kinetic and stoichiometric coefficients of the model were determined from batch respirometric tests on wastewater and activated sludge, and simulation of the batch respirometric experiment. To make the model plant-specific it is calibrated against plant operating data. Influent characterisation and reliable ASM3 model parameters were determined from the respirometric batch test and modelling of experiments. The resulting plant model was able to closely predict the trends of the effluent COD concentration in the plant. Hence it was concluded that the use of laboratory experiments, historical data from the municipal laboratory and modelling of experiments in order to generate information for the modelling of wastewater treatment plants makes up a methodology which can be adopted and improved by additional experiments. / Thesis (M.Sc.Eng.)-University of KwaZulu-Natal, Durban, 2008.

Submitted in fulfillment for the Degree of Masters of Applied Sciences (Biotechnology), Durban University of Technology, Durban, South Africa, 2016. / Activated sludge (AS) flocs are paramount in biological treatment of wastewater, are comprised of microbial consortia with organic and inorganic material bound together by extra polymeric substances (EPS). The filamentous bacteria play a vital role in the floc formation process by providing the necessary structural support. Presence of epiphytic attachment on selected filamentous bacteria is a commonly occurring phenomenon in activated sludge samples. Different theories have been proposed to describe this phenomenon; however, not much research has been carried out to explore the profundity of the attachment. In this study, an attempt has been made to elucidate the intrinsic nature of the epiphytic attachment between the bacterial rods and filamentous bacteria based on microscopic (morphological and structural) analysis. Characterization of these epiphytes were performed using fluorescence in situ hybridization (FISH) at group level using Alpha, Beta and Gamma Proteo-bacterial probes. Morphological characteristics of filament hosts and the bacterial rods at the interface region was assessed using scanning electron microscopy (SEM). The SEM micrographs indicated that the attachment was facilitated by more than the EPS layer. Further ultrastructural examination using transmission electron microscopy (TEM) indicated a possible cell-to-cell interaction between epiphytes and the selected filaments. Fibrillar structures resembling amyloid-like proteins were observed within the filament cell targeted by the epiphytes. An interaction was apparent between the amyloid like proteins and the epiphytes as exhibited by the direction of fibrillar structures pointing towards the approaching epiphytes. Common bacterial appendages such as pili and fimbria were absent at the interface and further noted was the presence of cell membrane extensions on the epiphytic bacteria protruding towards the targeted filamentous cell. The sheath of host filaments however, remained intact and unpenetrated, during colonization. Amyloid-like fibrils at interface may potentially play the role of attachment sites for the attaching epiphytes, as attachment facilitating appendages were not visualized. / M

In model reaction systems to test amino acids in chlorinated waste effluents, several amino acids were chlorinated at high chlorine doses. (2000-4000 mg/1). Amino acids present in municipal waste effluents before and after chlorination were concentrated and purified using cation exchange and Chelex resins. After concentration and cleanup of the samples, the amino acids were derivatized by esterification of the acid functional groups and acylation of the amine groups. Identification and quantification of the amino acids and chlorination products was carried out by gas chromatography/mass spectrometry, using a digital computer data system. Analysis of the waste products revealed the presence of new carbon-chlorine bonded derivatives of the amino acid tyrosine when the effluents were treated with heavy doses of chlorine.

Thesis (Master of Engineering in Chemical Engineering)--Cape Peninsula University of Technology, 2019. / A shortage of water has resulted in the need to enhance the quality of wastewater that is released into the environment. The advanced oxidation process (AOP) using heterogeneous catalysis is a promising treatment process for the management of wastewater containing recalcitrant pollutants as compared to conventional processes. As AOP is a reliable wastewater treatment process, it is expected to be a sustainable answer to the shortage of clean water. AOP using heterogeneous catalysis based on Co3O4 particles and PMS, in particular has been found to be a powerful procedure for the degradation and mineralization of recalcitrant organic contaminants. In addition, due to the growing application of Co3O4 in lithium batteries, large quantities of these particles will be recovered as waste from spent lithium batteries, so there is a need to find a use for them. Although this method has received some promising feedback, challenges still need to be addressed, such as the toxicity of cobalt particles, the poor chemical and thermal stability and particle aggregation, and the prompting of lower catalytic efficiency in long haul application. Furthermore, the removal of the catalyst after the treatment of pollutants is also an issue. In order to be applicable, a novel catalyst must be produced requiring the combination of Co3O4 with a support material in order to inhibit cobalt leaching and generate better particle stability. From the available literature, TiO2 was found to be the best support material because it not only provides a large surface area for well dispersed Co3O4, but it also forms strong Co-O-Ti bonds which greatly reduced cobalt leaching as compared to other support materials. Moreover, it also greatly encourages the formation of surface Co–OH complexes, which is considered a crucial step for PMS activation. Therefore, the issues cited above could be avoided by producing a Co3O4/TiO2 heterojunction catalyst.

by Li Sze Kwan. / Thesis (M.Phil.)--Chinese University of Hong Kong, 1990. / Bibliography: leaves 234-259. / ACKNOWLEDGEMENT --- p.i / ABSTRACT --- p.ii / CONTENTS : / Chapter CHAPTER 1: --- GENERAL INTRODUCTION --- p.1 / Chapter 1.1 --- Our Environment Is Polluted --- p.1 / Chapter 1.2 --- Heavy Metal Contamination --- p.3 / Chapter 1.3 --- The Effect of Cadmium and Some Related Metals on Environment --- p.5 / Chapter 1.4 --- The Uses of Microorganisms in Cleaning Up Environment --- p.9 / Chapter 1.5 --- Mechanisms of Cadmium Uptake in Cadmium Accumulating Strains --- p.10 / Chapter 1.6 --- Techniques for Cell Immobilization --- p.13 / Chapter 1.7 --- Prospect --- p.20 / Chapter CHAPTER 2: --- ISOLATION OF CADMUIM ACCUMULATNIG MICROORGANISMS --- p.22 / Chapter 2.1 --- Introduction --- p.22 / Chapter 2.2 --- Materials and Methods --- p.25 / Chapter 2.2.1 --- Recipes Used for Growing Various Organisms --- p.25 / Chapter 2.2.2 --- Methods Used for Collecting Organisms to be Tested --- p.27 / Chapter 2.2.3 --- Observation of Samples by Microscope --- p.28 / Chapter 2.2.4 --- Enrichment of Cadmium Resistant Microorganisms --- p.28 / Chapter 2.2.5 --- Selection and Isolation of Cadmium Resistant Microorganisms --- p.29 / Chapter 2.2.6 --- Purification of Microbial Colonies --- p.30 / Chapter 2.2.7 --- Preliminary Classification of Selected Microorganisms --- p.30 / Chapter 2.2.8 --- Screening of Cadmium Accumulating Strains --- p.30 / Chapter 2.2.9 --- Cadmium Analysis --- p.31 / Chapter 2.3 --- Result --- p.32 / Chapter 2.3.1 --- Selection of Cadmium Resistant --- p.32 / Chapter 2.3.2 --- Cadmium Resistance of Isolates --- p.36 / Chapter 2.3.3 --- Screening of Cadmium Accumulating Microorganisms --- p.38 / Chapter 2.4 --- Discussion --- p.39 / Chapter CHAPTER 3: --- GENERAL CHARACTERIZATION OF STRAIN 1000A --- p.43 / Chapter 3.1 --- Introduction --- p.43 / Chapter 3.1.1 --- Various Factors Affecting the Accumulation of Cadmium of Strain 1000A --- p.43 / Chapter 3.1.2 --- Identification --- p.44 / Chapter 3.2 --- Materials and Methods --- p.45 / Chapter 3.2.1 --- "Preparation of Solutions, Antibiotics and Reagents" --- p.45 / Chapter 3.2.2 --- Culture Media Used --- p.47 / Chapter 3.2.3 --- Growth Kenetics Determination --- p.48 / Chapter 3.2.4 --- Determination of the Effect of Cadmium Concentration on Cd-uptake in Free Cells --- p.49 / Chapter 3.2.5 --- Determination of the Effect of Phosphate Concentration on Cd-uptake in Free Cell --- p.49 / Chapter 3.2.6 --- Determination of the Cd-uptake in Free Cells in Continuous Cultures --- p.50 / Chapter 3.2.7 --- Determination of Antibiotic Resistance of Strain 1000A --- p.51 / Chapter 3.2.8 --- Dstermination of Relationship between Chloramphenicol Resistance and Cd-uptake --- p.52 / Chapter 3.2.9 --- Cadmium Analysis --- p.52 / Chapter 3.2.10 --- Determination of Inorganic Precipitation of Cadmium --- p.53 / Chapter 3.2.11 --- Assimilation Tests --- p.54 / Chapter 3.2.12 --- Identification of Strain 1000A --- p.55 / Chapter 3.3 --- Result --- p.55 / Chapter 3.3.1 --- Growth Kinetics of Strain 1000A in Cadmium Supplemented Peptone Medium --- p.55 / Chapter 3.3.2 --- Cd-uptake of Strain 1000A at Various Cadiuin Concentration --- p.65 / Chapter 3.3.3 --- Effect of Phosphate concentration on Cd-uptake of Strain 1000A --- p.65 / Chapter 3.3.4 --- Cd-uptake of Strain 1000A in Continuous Cultures --- p.70 / Chapter 3.3.5 --- Inorganic Precipitation of Cadmium Phosphate --- p.75 / Chapter 3.3.6 --- Determination of Antibiotic-Resistance of Strain 1000A --- p.78 / Chapter 3.3.7 --- Effect of Chloramphenicol on Cd-uptake and Cadmium Resistance of Strain 1000A --- p.82 / Chapter 3.3.8 --- Determination of the Effect of Tetracyclin --- p.85 / Chapter 3.3.9 --- Assimilation Tests --- p.94 / Chapter 3.3.10 --- Identification of Strain 1000A --- p.94 / Chapter 3.4 --- Discussion --- p.97 / Chapter CHAPTER 4: --- DETERMINATION OF CADMIUM UPTAKE MECHANISM IN P. PICKETTI 1000A --- p.102 / Chapter 4.1 --- Introduction --- p.102 / Chapter 4.2 --- Materials and Methods --- p.105 / Chapter 4.2.1 --- Preparation of Solutions and Reagents --- p.105 / Chapter 4.2.2 --- Preparation of Reagents for SDS-PAGE --- p.105 / Chapter 4.2.3 --- Recipes for Growing Cells --- p.107 / Chapter 4.2.4 --- Protein Determination --- p.108 / Chapter 4.2.5 --- Examination of Cadmium Accommodation in P. picketti 1000A by Transmission Electron Microscope --- p.108 / Chapter 4.2.6 --- SDS-polyacrylamide Gel Electrophoretic Determination of Protein Profiles --- p.109 / Chapter 4.2.7 --- Phosphate Assay --- p.111 / Chapter 4.2.8 --- Orthophosphate Estimation --- p.112 / Chapter 4.2.9 --- Sulphide Analysis --- p.112 / Chapter 4.2.10 --- Cadmium Analysis --- p.113 / Chapter 4.2.11 --- Cd-binding Determination through Column Separation --- p.113 / Chapter 4.2.12 --- Cd-binding Determinate ion through SDS Electrophoresis --- p.114 / Chapter 4.2.13 --- Determination of Cadmium Distribution of Cells --- p.115 / Chapter 4.3 --- Result --- p.116 / Chapter 4.3.1 --- SDS-PAGE Determination of Protein Profiles of P. picketti 1000A --- p.116 / Chapter 4.3.2 --- Determination of Cd-binding Protein of P. picketti 1000A --- p.121 / Chapter 4.3.3 --- "Determination of the Relationship of Cellular Cadmium, Sulphide and Phosphate" --- p.131 / Chapter 4.3.4 --- Examination of Cadmium Accumulation of P. picketti 1000A by Transmission Electron Microscope --- p.142 / Chapter 4.3.5 --- Cadmium Distribution of Cadmium-Accommodated Cells --- p.148 / Chapter 4.4 --- Discussion --- p.152 / Chapter CHAPTER 5: --- CORRELATION AMONG METALS IN HEAVY METAL UPTAKE --- p.158 / Chapter 5.1 --- Introduction --- p.158 / Chapter 5.2 --- Materials and Methods --- p.158 / Chapter 5.2.1 --- Preparation of Solutions --- p.159 / Chapter 5.2.2 --- "Determination of Effect of Zn+2 ," --- p.160 / Chapter 5.2.3 --- Determination of Effect of Cu+2 . --- p.161 / Chapter 5.2.4 --- "Correlation among Cd+2, Cu+2 and Zn+2" --- p.161 / Chapter 5.2.5 --- Growth Kenetics Determination --- p.162 / Chapter 5.2.6 --- Cell Sample Preparation --- p.162 / Chapter 5.2.7 --- Orthophosphate Estimation --- p.162 / Chapter 5.2.8 --- Metal Analysis --- p.163 / Chapter 5.3 --- Result --- p.163 / Chapter 5.3.1 --- Effect of Zn+2 --- p.163 / Chapter 5.3.2 --- Effect of Cu+2 --- p.173 / Chapter 5.3.3 --- "Correlation among Cd+2, Cu+2 and Zn+2" --- p.178 / Chapter 5.4 --- Discussion --- p.195 / Chapter CHAPTER 6: --- HEAVY METAL UPTAKE OF IMMOBILIZED CELL --- p.197 / Chapter 6.1 --- Introduction --- p.197 / Chapter 6.2 --- Materials and Methods --- p.199 / Chapter 6.2.1 --- Preparation of Solutions and Medium --- p.199 / Chapter 6.2.2 --- Harvesting of Cells --- p.199 / Chapter 6.2.3 --- Immobilization of Cells --- p.199 / Chapter 6.2.4 --- Determination of the Effect of Temperature --- p.200 / Chapter 6.2.5 --- Determination of Optimum Cell Concentration in Polyacrylamide Gel --- p.201 / Chapter 6.2.6 --- Determination of pH Effect on Cd-uptake --- p.201 / Chapter 6.2.7 --- Pretreatment with 70% Methanol --- p.202 / Chapter 6.2.8 --- Combined Pretreatment with Methanol and NaOH --- p.202 / Chapter 6.2.9 --- Effect of Phosphate on Cd-uptake of Immobilized Cell --- p.202 / Chapter 6.2.10 --- Comparison of Cadmium- and Copper-uptakes in Cells Immobilized in K-carrageenan and in Polyacrylamide --- p.203 / Chapter 6.3 --- Result --- p.204 / Chapter 6.3.1 --- Effect of Temperature on Cd-uptake --- p.204 / Chapter 6.3.2 --- Determination of Optimum Cell Concentration in Polyacrylamide Gel --- p.204 / Chapter 6.3.3 --- Effect of pH on Cd-uptake of Immobilized Cells --- p.207 / Chapter 6.3.4 --- Effect of Methanol on Cd-uptake --- p.210 / Chapter 6.3.5 --- Combined Effect of pH and Methanol on Cd-uptake --- p.213 / Chapter 6.3.6 --- Effect of Phosphate on Cd-uptake of Immobilized Cells --- p.213 / Chapter 6.3.7 --- Comparison between Cadmium- and Copper-uptake of Cells Immobilized in K-carrageenan and in Polyacrylamide --- p.220 / Chapter 6.4 --- Discussion --- p.228 / Chapter CHAPTER 7: --- CONCLUSION --- p.232 / REFERENCES --- p.234

by Tsui Wai-chu. / Thesis (M.Phil.)--Chinese University of Hong Kong, 2000. / Includes bibliographical references (leaves 161-171). / Abstracts in English and Chinese. / Acknowledgements --- p.i / Abstract --- p.ii / Abbreviations --- p.vii / Contents --- p.ix / Chapter 1. --- Introduction --- p.1 / Chapter 1.1 --- Literature review --- p.1 / Chapter 1.1.1 --- Metal pollution in Hong Kong --- p.1 / Chapter 1.1.2 --- Methods for removal of metal ions from industrial effluent --- p.4 / Chapter A. --- Physico-chemical methods --- p.4 / Chapter B. --- Biosorption --- p.7 / Chapter 1.1.3 --- Chitin and chitosan --- p.11 / Chapter A. --- History of chitin and chitosan --- p.11 / Chapter B. --- Structures and sources of chitin and chitosan --- p.12 / Chapter C. --- Characterization of chitin and chitosan --- p.17 / Chapter D. --- Applications of chitin and chitosan --- p.19 / Chapter 1.1.4 --- Factors affecting biosorption --- p.22 / Chapter A. --- Solution pH --- p.22 / Chapter B. --- Concentration of biosorbent --- p.24 / Chapter C. --- Retention time --- p.25 / Chapter D. --- Initial metal ion concentration --- p.26 / Chapter E. --- Presence of other cations --- p.26 / Chapter F. --- Presence of anions --- p.28 / Chapter 1.1.5 --- Regeneration of metal ion-laden biosorbent --- p.28 / Chapter 1.1.6 --- Modeling of biosorption --- p.29 / Chapter A. --- Adsorption equilibria and adsorption isotherm --- p.29 / Chapter B. --- Langmuir isotherm --- p.33 / Chapter C. --- Freundlich isotherm --- p.34 / Chapter 1.2 --- Objectives of the present study --- p.36 / Chapter 2. --- Materials and methods --- p.37 / Chapter 2.1 --- Biosorbents --- p.37 / Chapter 2.1.1 --- Production of biosorbents --- p.37 / Chapter 2.1.2 --- Pretreatment of biosorbents --- p.39 / Chapter 2.2 --- Characterization of biosorbents --- p.39 / Chapter 2.2.1 --- Chitin assay --- p.39 / Chapter 2.2.2 --- Protein assay --- p.40 / Chapter 2.2.3 --- Metal analysis --- p.41 / Chapter 2.2.4 --- Degree of N-deacetylation analysis --- p.43 / Chapter A. --- Diffuse reflectance Fourier transform infra-red spectroscopy --- p.43 / Chapter B. --- Elemental analysis --- p.43 / Chapter 2.3 --- Batch biosorption experiment --- p.44 / Chapter 2.4 --- Selection of biosorbent for metal ion removal --- p.45 / Chapter 2.4.1 --- Effects of pretreatments of biosorbents on adsorption of Cu --- p.45 / Chapter A. --- Washing --- p.45 / Chapter B. --- Pre-swelling --- p.46 / Chapter 2.4.2 --- "Comparison of Cu2+, Ni2+ and Zn2+ removal capacities among three biosorbents" --- p.46 / Chapter 2.4.3 --- Comparison of Cu2+ removal capacity of chitins with various degrees of N-deacetylation --- p.46 / Chapter 2.5 --- "Effects of physico-chemical conditions on Cu2+, Ni2+ and Zn2+ adsorption by chitin A" --- p.48 / Chapter 2.5.1 --- Solution pH and concentration of biosorbent --- p.48 / Chapter 2.5.2 --- Retention time --- p.48 / Chapter 2.5.3 --- Initial metal ion concentration --- p.49 / Chapter 2.5.4 --- Presence of other cations --- p.49 / Chapter 2.5.5 --- Presence of anions --- p.51 / Chapter 2.6 --- Optimization of Cu2+，Ni2+ and Zn2+ removal efficiencies --- p.53 / Chapter 2.7 --- "Recovery of Cu2+, Ni2+ and Zn2+ from metal ion-laden chitin A" --- p.53 / Chapter 2.7.1 --- Performances of various eluents on metal ion recovery --- p.53 / Chapter 2.7.2 --- Multiple adsorption and desorption cycle of metal ions --- p.54 / Chapter 2.8 --- Treatment of electroplating effluent by chitin A --- p.54 / Chapter 2.8.1 --- "Removal and recovery of Cu2+, Ni2+ and Zn2+ from electroplating effluent collected from rinsing baths" --- p.54 / Chapter 2.8.2 --- "Removal and recovery of Cu2+, Ni2+ and Zn2+ from electroplating effluent collected from final collecting tank" --- p.55 / Chapter 2.9 --- Data analysis --- p.56 / Chapter 3. --- Results --- p.58 / Chapter 3.1 --- Characterization of biosorbents --- p.58 / Chapter 3.1.1 --- Chitin assay --- p.58 / Chapter 3.1.2 --- Protein assay --- p.58 / Chapter 3.1.3 --- Metal analysis --- p.58 / Chapter 3.1.4 --- Degree of N-deacetylation analysis --- p.62 / Chapter A. --- Diffuse reflectance Fourier transform infra-red spectroscopy --- p.62 / Chapter B. --- Elemental analysis --- p.62 / Chapter 3.2 --- Selection of biosorbent for metal ion removal --- p.67 / Chapter 3.2.1 --- Effects of pretreatments of biosorbents on adsorption of Cu2+ --- p.67 / Chapter A. --- Washing --- p.67 / Chapter B. --- Pre-swelling --- p.67 / Chapter 3.2.2 --- "Comparison of Cu2+, Ni2+ and Zn2+ removal capacities among three biosorbents" --- p.67 / Chapter 3.2.3 --- Comparison of Cu2+ removal capacity of chitins with various degrees of N-deacetylation --- p.70 / Chapter 3.3 --- "Effects of physico-chemical conditions on Cu2+, Ni2+ and Zn2+ adsorption by chitin A" --- p.70 / Chapter 3.3.1 --- Solution pH and concentration of biosorbent --- p.70 / Chapter 3.3.2 --- Retention time --- p.78 / Chapter 3.3.3 --- Initial metal ion concentration --- p.80 / Chapter 3.3.4 --- Presence of other cations --- p.93 / Chapter 3.3.5 --- Presence of anions --- p.93 / Chapter 3.4 --- "Optimization of Cu2+, Ni2+ and Zn2+ removal efficiencies" --- p.104 / Chapter 3.5 --- "Recovery of Cu2+, Ni2+ and Zn2+ from metal ion-laden chitin A" --- p.104 / Chapter 3.5.1 --- Performances of various eluents on metal ion recovery --- p.104 / Chapter 3.5.2 --- Multiple adsorption and desorption cycle of metal ions --- p.109 / Chapter 3.6 --- Treatment of electroplating effluent by chitin A --- p.117 / Chapter 3.6.1 --- "Removal and recovery of Cu2+, Ni2+ and Zn2+ from electroplating effluent collected from rinsing baths" --- p.117 / Chapter 3.6.2 --- "Removal and recovery of Cu2+, Ni2+ and Zn2+ from electroplating effluent collected from final collecting tank" --- p.121 / Chapter 4. --- Discussion --- p.128 / Chapter 4.1 --- Characterization of biosorbents --- p.128 / Chapter 4.1.1 --- Chitin assay --- p.128 / Chapter 4.1.2 --- Protein assay --- p.129 / Chapter 4.1.3 --- Metal analysis --- p.129 / Chapter 4.1.4 --- Degree of N-deacetylation analysis --- p.130 / Chapter A. --- Diffuse reflectance Fourier transform infra-red spectroscopy --- p.130 / Chapter B. --- Elemental analysis --- p.132 / Chapter 4.2 --- Selection of biosorbent for metal ion removal --- p.133 / Chapter 4.2.1 --- Effects of pretreatments of biosorbents on adsorption of Cu2+ --- p.133 / Chapter A. --- Washing --- p.133 / Chapter B. --- Pre-swelling --- p.133 / Chapter 4.2.2 --- "Comparison of Cu2+, Ni2+ and Zn2+ removal capacities among three biosorbents" --- p.134 / Chapter 4.2.3 --- Comparison of Cu2+ removal capacity of chitins with various degrees of N-deacetylation --- p.136 / Chapter 4.3 --- "Effects of physico-chemical conditions on Cu2+, Ni2+ and Zn2+ adsorption by chitin A" --- p.137 / Chapter 4.3.1 --- Solution pH and concentration of biosorbent --- p.137 / Chapter 4.3.2 --- Retention time --- p.138 / Chapter 4.3.3 --- Initial metal ion concentration --- p.139 / Chapter 4.3.4 --- Presence of other cations --- p.141 / Chapter 4.3.5 --- Presence of anions --- p.143 / Chapter 4.4 --- "Optimization of Cu2+, Ni2+ and Zn2+ removal efficiencies" --- p.147 / Chapter 4.5 --- "Recovery of Cu2+, Ni2+and Zn2+ from metal ion-laden chitin A" --- p.148 / Chapter 4.5.1 --- Performances of various eluents on metal ion recovery --- p.148 / Chapter 4.5.2 --- Multiple adsorption and desorption cycle of metal ions --- p.149 / Chapter 4.6 --- Treatment of electroplating effluent by chitin A --- p.150 / Chapter 4.6.1 --- "Removal and recovery of Cu2+, Ni2+ and Zn2+ from electroplating effluent collected from rinsing baths" --- p.150 / Chapter 4.6.2 --- "Removal and recovery of Cu2+, Ni2+ and Zn2+ from electroplating effluent collected from final collecting tank" --- p.152 / Chapter 5. --- Conclusion --- p.154 / Chapter 6. --- Further studies --- p.156 / Chapter 7. --- Summary --- p.158 / Chapter 8. --- References --- p.161

Digitized by Kansas Correctional Industries

by Sze Kwok Fung Calvin. / Thesis (M.Phil.)--Chinese University of Hong Kong, 1996. / Includes bibliographical references (leaves 118-130). / Acknowledgement --- p.i / Abstract --- p.ii / Content --- p.iv / Chapter 1. --- Introduction --- p.1 / Chapter 1.1 --- Literature review --- p.1 / Chapter 1.1.1 --- Heavy metals in the environment --- p.1 / Chapter 1.1.2 --- Heavy metal pollution in Hong Kong --- p.2 / Chapter 1.1.3 --- Electroplating industry in Hong Kong --- p.6 / Chapter 1.1.4 --- Chemistry and toxicity of copper in the environment --- p.7 / Chapter 1.1.5 --- Methods of removal of heavy metal from industrial effluent --- p.9 / Chapter A. --- Physico-chemical methods --- p.9 / Chapter B. --- Biological methods --- p.9 / Chapter 1.1.6 --- Methods of recovery of heavy metal from metal-loaded biosorbent --- p.17 / Chapter 1.1.7 --- The physico-chemical properties of magnetites --- p.18 / Chapter 1.1.8 --- Magnetites for water and wastewater treatment --- p.19 / Chapter 1.1.9 --- Immobilized cell technology --- p.24 / Chapter 1.1.10 --- Stirrer-tank bioreactor --- p.26 / Chapter 1.2 --- Objectives of the present study --- p.28 / Chapter 2. --- Materials and Methods --- p.30 / Chapter 2.1 --- Selection of copper-resistant bacteria --- p.30 / Chapter 2.2 --- Culture media and chemicals --- p.30 / Chapter 2.3 --- Growth of the bacterial cells --- p.32 / Chapter 2.4 --- Immobilization of the bacterial cells on magnetites --- p.32 / Chapter 2.4.1 --- Effects of physical and chemical factors on the immobilization of the bacterial cells on magnetites --- p.34 / Chapter 2.4.2 --- Effects of pH on the desorption of bacterial cells from magnetites --- p.34 / Chapter 2.5 --- Copper ion uptake experiments --- p.35 / Chapter 2.6 --- Effects of physico-chemical and operational factors on the Cu2+ removal capacity of the magnetite-immobilized bacterial cells --- p.35 / Chapter 2.7 --- Transmission electron micrograph and scanning electron micrograph of Pseudomonas putida 5-X loaded with Cu2+ --- p.36 / Chapter 2.7.1 --- Transmission electron micrograph --- p.36 / Chapter 2.7.2 --- Scanning electron micrograph --- p.37 / Chapter 2.8 --- Copper ion adsorption isotherm of the magnetite-immobilized cells of Pseudomonas putida 5-X --- p.37 / Chapter 2.9 --- Recovery of adsorbed Cu2+ from the magnetite-immobilized cells of Pseudomonas putida 5-X --- p.38 / Chapter 2.9.1 --- Effects of eluents on the Cu2+ removal and recovery capacity of the magnetite-immobilized cells --- p.38 / Chapter 2.9.2 --- Batch type multiple adsorption-desorption cycles of Cu2+ using ethylenediaminetetra-acetic acid (EDTA) --- p.39 / Chapter 2.10 --- Removal and recovery of Cu2+ from the electroplating effluent by a bioreactor --- p.39 / Chapter 2.10.1 --- Batch type multiple adsorption-desorption cycles using the copper solution and electroplating effluent --- p.39 / Chapter 2.10.2 --- Continuous type bioreactor to remove and recover Cu2+ from copper solution and electroplating effluent --- p.40 / Chapter 2.11 --- Statistical analysis of data --- p.43 / Chapter 3. --- Results --- p.44 / Chapter 3.1 --- Effects of physical and chemical factors on the immobilization of the bacterial cells on magnetites --- p.44 / Chapter 3.1.1 --- Effects of cells to magnetites ratio --- p.44 / Chapter 3.1.2 --- Effects of pH --- p.44 / Chapter 3.1.3 --- Effects of temperature --- p.44 / Chapter 3.2 --- Effects of pH on the desorption of bacterial cells from magnetites --- p.49 / Chapter 3.3 --- Copper ion uptake experiments --- p.49 / Chapter 3.4 --- Effects of physico-chemical and operational factors on the Cu2+ removal capacity of the magnetite-immobilized bacterial cells --- p.49 / Chapter 3.4.1 --- Effects of pH --- p.49 / Chapter 3.4.2 --- Effects of temperature --- p.53 / Chapter 3.4.3 --- Effects of retention time --- p.53 / Chapter 3.4.4 --- Effects of cations --- p.53 / Chapter 3.4.5 --- Effects of anions --- p.57 / Chapter 3.5 --- Transmission electron micrograph of Pseudomonas putida 5-X loaded with Cu2+ --- p.62 / Chapter 3.6 --- Scanning electron micrograph of Pseudomonas putida 5-X loaded with Cu2+ --- p.62 / Chapter 3.7 --- Copper ion adsorption isotherm of the magnetite-immobilized cells of Pseudomonas putida 5-X --- p.68 / Chapter 3.8 --- Recovery of adsorbed Cu2+ from the magnetite-immobilized cells of Pseudomonas putida 5-X --- p.68 / Chapter 3.8.1 --- Effects of eluents on the Cu2+ removal and recovery capacity of the magnetite-immobilized cells --- p.68 / Chapter 3.8.2 --- Batch type multiple adsorption-desorption cycles of Cu2+ using ethylenediaminetetra-acetic acid (EDTA) --- p.74 / Chapter 3.9 --- Removal and recovery of Cu2+ from the electroplating effluent by a bioreactor --- p.74 / Chapter 3.9.1 --- Batch type multiple adsorption-desorption cycles using the copper solution and electroplating effluent --- p.74 / Chapter 3.9.2 --- Continuous type bioreactor to remove and recover Cu2+ from copper solution and electroplating effluent --- p.81 / Chapter 4. --- Discussion --- p.89 / Chapter 4.1 --- Selection of copper-resistant bacteria --- p.89 / Chapter 4.2 --- Effects of physical and chemical factors on the immobilization of the bacterial cells on magnetites --- p.89 / Chapter 4.2.1 --- Effects of cells to magnetites ratio --- p.89 / Chapter 4.2.2 --- Effects of pH --- p.90 / Chapter 4.2.3 --- Effects of temperature --- p.91 / Chapter 4.2.4 --- Effects of pH on the desorption of bacterial cells from magnetites --- p.92 / Chapter 4.3 --- Copper ion uptake experiments --- p.93 / Chapter 4.4 --- Effects of physico-chemical and operational factors on the Cu2+ removal capacity of the magnetite-immobilized bacterial cells --- p.94 / Chapter 4.4.1 --- Effects of pH --- p.95 / Chapter 4.4.2 --- Effects of temperature --- p.96 / Chapter 4.4.3 --- Effects of retention time --- p.97 / Chapter 4.4.4 --- Effects of cations --- p.98 / Chapter 4.4.5 --- Effects of anions --- p.101 / Chapter 4.5 --- Transmission electron micrograph of Pseudomonas putida 5-X loaded with Cu2+ --- p.101 / Chapter 4.6 --- Scanning electron micrograph of Pseudomonas putida 5-X loaded with Cu2+ --- p.102 / Chapter 4.7 --- Copper ion adsorption isotherm of the magnetite-immobilized cells of Pseudomonas putida 5-X --- p.103 / Chapter 4.8 --- Recovery of adsorbed Cu2+ from the magnetite-immobilized cells of Pseudomonas putida 5-X --- p.104 / Chapter 4.8.1 --- Effects of eluents on the Cu2+ removal and recovery capacity of the magnetite-immobilized cells --- p.104 / Chapter 4.8.2 --- Batch type multiple adsorption-desorption cycles of Cu2+ using ethylenediaminetetra-acetic acid (EDTA) --- p.105 / Chapter 4.9 --- Removal and recovery of Cu2+ from the electroplating effluent by a bioreactor --- p.107 / Chapter 4.9.1 --- Batch type multiple adsorption-desorption cycles using the copper solution and electroplating effluent --- p.107 / Chapter 4.9.2 --- Continuous type bioreactor to remove and recover Cu2+ from copper solution and electroplating effluent --- p.108 / Chapter 5. --- Conclusion --- p.110 / Chapter 6. --- Summary --- p.112 / Chapter 7. --- References --- p.115

Thesis (Master of Engineering in Chemical Engineering)--Cape Peninsula University of Technology, 2017. / Pre-treatment of wastewater such as that from poultry slaughterhouses, which contains fats, oil,and grease (FOG) is necessary prior to the primary biological treatment of the wastewater to meet legislated discharge standards and to prevent environmental pollution. Physico- chemical pre-treatment is often applied to remove FOG in poultry slaughterhouse wastewater (PSW) before biological treatment. These pre-treatment methods, in particular physical pre- treatment systems, use synthetic chemicals, known to cause environmental contamination challenges, with FOG being inefficiently removed in certain instances. Biological techniques such as bio-delipidation using enzymatic catalysis for the pre-treatment of FOG-laden PSW could enhance the efficiency of the downstream biological treatment processes. This research focused on further bio-delipidation of PSW pre-treated with a dissolved air flotation system (DAF) for FOG removal using microbial lipases from bacterial strains isolated from the PSW itself. Bacterial strains (n = 2) isolated from the PSW and screened for their potential to produce lipases were found to have a higher bio-delipidation potential when compared to other isolates (n = 18). Both isolates were identified using 16s rRNA as Bacillus sp., i.e. both Bacillus cereus AB1 (BF3) and CC-1 (B3O). These isolates were used to produce lipases, whereby are sponse surface methodology (RSM) was used to optimise pH (4-8) and temperature (30-60°C) as critical production conditions. achieving an optimum lipase production was achieved, with activity of 11.25 U/mL at 60°C, a pH of8 for BF3, and 15.50U/mL at 45°C and pH of 8.8 for B3O respectively, after 72 hours of bioreactor operation. The enzymes produced from both isolates were partially purified using a Bio-Rad size exclusion chromatography column (Bio-Gel® P-60) prior to use in subsequent experiments. The presence and activity of lipase were further determined using p-nitrophenyl acetate (p- NPA) as a substrate with the functionality of the semi-purified enzymes being characterized by optimizing the conditions in which the enzymes were required to function. Lipase activity was enhanced by Mg2+ while Fe2+, Na+, K+, Ca2+ were observed to have an inhibitory effect on the enzymes from both strains. Similarly, reduced stability of the lipases in organic solvents, namely toluene, methanol, and isopropanol, was also established. Additionally, detergents, Triclosan (TCS) (5-chloro-2-(2,4-dichlorophenoxy-phenol) and trichlorocarbonilide (3,4,4- trichlorocarbonilide)(TCC), usually found in PSW as antimicrobial and disinfectant agents to sanitise poultry product processing facilities, were used assess the activity of the enzyme in their presence at a concentration of 30% (v/v) (although these anti- microbial agents are used in minute quantities in cleaning products). The lipases from isolate BF3 maintained an activity of 91.43% and 81.36% in the presence of TCS and TCC, while that of B3O enzyme had 85.32% and 73.91% acitivity, when compared to the reference (control) experiments. The bio-delipidation efficacy was studied under varying pH and temperature conditions using DAF pre-treated PSW, observing a further removal efficiency of fatty acids from the protein- laden PSW at different pH and temperature. Bio-delipidation was found to be largely influenced by pH, as a pH below 7 and above 10 at 40°-45°C, calculated in the bio- delipidation efficiency reduction to below 50%. The temperature range mentioned, i.e 40°- 45°C, had a positive effect on further deffating of the protein-rich DAF pre-treated PSW, as high removal efficiency was observed at this temperature range. This could be due to the characteristic of the enzymes used,or the formation of stable FOG agglomerates and/oremulsion. Overall, a DAF effluent containing residual FOG and proteins was bio-delipidated effectively using enzymes from the PSW isolates, achieving further removal of FOG and proteins by 64.35% to 80.42%, culminating in tCOD reduction and reduced PSW turbidity, further resulting in improved wastewater quality characteristics meeting disposal standards. This study demonstrated that sequential DAF pre-treated PSW bio-delipidation has the potential to enhance the efficiency of downstream biological anaerobic treatment processes for PSW by further reducing residual FOG from a DAF system.