Thesis (MTech (Chemistry))--Cape Peninsula University of Technology, 2017. / Pharmaceuticals have found extensive application in human health management. They are released into the environment through urine, excreta and inappropriate disposal methods. Residues of pharmaceutical products have been reported to show toxic consequences in some freshwater and marine organisms. Antibiotics are one of the most important groups of common human pharmaceuticals widely in use as prescribed and non-prescribed drugs. Antibiotics and their metabolites have been quantitated in water and found in trace levels. But even at such low concentrations they can maintain high biological activities with potential adverse effects on humans and animals. Unfortunately, many pharmaceutical compounds are resistant to breakdown in the environment, hence they have tendency for environmental magnification, since they are designed to be biologically active. Therefore, there is need to evaluate their environmental levels and their possible abatement methods using simple, cheap and low cost techniques, in order to avert their potential toxic consequences. In this research, a cost effective, robust, selective and rugged method for the analysis of antibiotics in water samples using liquid chromatography was developed, and used for monitoring levels of the selected antibiotics in Diep River. Also, an effective remediation procedure for these contaminants in water was developed using activated carbon produced from grape slurry waste.

In soils spiked with gamma-HCH & DDT, and transplanted with wheat, the differences of gamma-HCH between the rhizosphere and non-rhizosphere soils increased with time, reached the peak on 30th sampling day, and then decreased with time. In the rhizosphere and non-rhizosphere soils, pp'-DDE/SigmaDDTs, op'-DDD/SigmaDDTs and pp'-DDD/SigmaDDTs increased with time; whilst op'-DDT/SigmaDDT and pp'-DDT/SigmaDDT decreased with time. The wheat, corn and soybean rhizosphere soils differed greatly in soil properties, but it was hard to conclude the effect of crop roots on the variation in concentration of gamma-HCH, p,p'-DDE, p,p'-DDD and p,p'-DDT in the rhizosphere soils except for root accumulation and translocation. / In the control, wheat and corn rhizosphere soils, the n-hexane extracted fraction of gamma-HCH, DDE, DDD and DDT decreased with time whereas the hexane/acetone extracted fraction increased with time after the 20th sampling day. The n-hexane extracted forms were higher in the rhizosphere soils than those in the non-rhizosphere soils, while the hexane/acetone extracted forms were lower in the rhizosphere soils than in the non-rhizosphere soils. / In the wheat, corn rhizosphere soils and the control, the concentration of NO3-N showed a significant negative correlation with n-hexane extracted DDE, DDD and DDT residues and a significant positive correlation with hexane/acetone extracted residues. The concentration of ammonium nitrogen (NH4-N) showed a significant negative correlation with hexane extracted gamma-HCH, DDE, DDD and DDT residues in the control, corn and wheat rhizosphere soils: but only had significant positive correlation with the n-hexane/acetone extracted fraction in the corn rhizosphere soil. The positive correlations between the n-hexane extracted residues of the target pesticides and soil OC were seldom significant in the control, sometimes significant in the wheat rhizosphere soils, and always strong and significant in the corn rhizosphere soils. The correlation of the n-hexane/acetone extracted residues with soil OC was positive and sometimes significant in the wheat rhizosphere soils, and significant and negative in the corn rhizosphere soils. The results indicated that the concentrations of different OCPs extracted from were strongly influenced by nutritional conditions and soil organic carbon. / Organic carbon (OC), dissolved organic carbon (DOC) and cultivation period were tested to explore their potential effects on target OCPs in the rhizosphere soils. The concentration of the target OCPs in the wheat rhizosphere soils increased proportionally to soil OC, whilst the uptake of OCPs by wheat roots and further translocation to the aboveground part were inversely proportional to soil OC. DOC only showed a negative correlation with concentration of p,p'-DDE and p,p'-DDT in the corn rhizosphere soils. After a longer root-soil interaction, roots had a more significant effect on the concentration of OCPs in the rhizosphere soils closer to the root surface. / The variation of different forms of OCPs in rhizosphere soils and their relationships with nitrogen nutrients and organic carbon were studied. / Variations in concentrations of organochlorine pesticide (OCP) residues in the rhizosphere soils were evaluated using rhizoboxes. A sequential extraction method was developed to study the fractionation and extractability of OCPs in rhizosphere soils. The key findings are as follows: / Zhu Xuemei. / "September 2006." / Adviser: Kin Che Lam. / Source: Dissertation Abstracts International, Volume: 68-03, Section: B, page: 1532. / Thesis (Ph.D.)--Chinese University of Hong Kong, 2006. / Includes bibliographical references (p. 265-288). / Electronic reproduction. Hong Kong : Chinese University of Hong Kong, [2012] System requirements: Adobe Acrobat Reader. Available via World Wide Web. / Electronic reproduction. [Ann Arbor, MI] : ProQuest Information and Learning, [200-] System requirements: Adobe Acrobat Reader. Available via World Wide Web. / Abstracts in English and Chinese. / School code: 1307.

by Wai Lok Man. / Thesis (M.Phil.)--Chinese University of Hong Kong, 2003. / Includes bibliographical references (leaves 142-155). / Abstracts in English and Chinese. / Acknowledgements --- p.i / Abstracts --- p.ii / Contents --- p.vii / List of figures --- p.xiii / List of tables --- p.xvi / Abbreviations --- p.xviii / Chapter 1. --- Introduction --- p.1 / Chapter 1.1 --- Pentachlorophenol / Chapter 1.1.1 --- Applications of pentachlorophenol --- p.1 / Chapter 1.1.2 --- Characteristics --- p.3 / Chapter 1.1.3 --- Pentachlorophenol in the environment --- p.3 / Chapter 1.1.4 --- Toxicity of Pentachlorophenol --- p.6 / Chapter 1.2 --- Treatments of Pentachlorophenol --- p.10 / Chapter 1.2.1 --- Physical treatment --- p.10 / Chapter 1.2.2 --- Chemical treatment --- p.11 / Chapter 1.2.3 --- Biological treatment --- p.13 / Chapter 1.3 --- Biodegradation --- p.14 / Chapter 1.3.1 --- Biodegradation of PCP by bacteria --- p.14 / Chapter 1.3.2 --- Biodegradation of PCP by white-rot fungi --- p.15 / Chapter 1.4 --- Biosorption --- p.24 / Chapter 1.5 --- Proposed Strategy --- p.28 / Chapter 1.6 --- Spent Mushroom Compost / Chapter 1.6.1 --- Background --- p.28 / Chapter 1.6.2 --- Physico-chemical properties of SMC --- p.29 / Chapter 1.6.3 --- As a biosorbent --- p.29 / Chapter 1.6.3.1 --- Factors affecting biosorption --- p.31 / Chapter 1.6.3.2 --- Contact time --- p.31 / Chapter 1.6.3.3 --- Initial pH --- p.32 / Chapter 1.6.3.4 --- Concentration of biosorbent --- p.33 / Chapter 1.6.3.5 --- Initial PCP concentration --- p.34 / Chapter 1.6.3.6 --- Incubation temperature --- p.34 / Chapter 1.6.3.7 --- Agitation speed --- p.35 / Chapter 1.6.4 --- Modeling of adsorption --- p.36 / Chapter 1.6.4.1 --- Langmuir isotherm --- p.36 / Chapter 1.6.4.2 --- Freundlich isotherm --- p.36 / Chapter 1.6.5 --- As a source of PCP-degrading bacteria --- p.38 / Chapter 1.6.5.1 --- Identification of PCP-degrading bacterium --- p.40 / Chapter 1.6.6 --- As a source of fungus --- p.42 / Chapter 1.7 --- Objectives of this Study --- p.43 / Chapter 2. --- Materials and Methods --- p.44 / Chapter 2.1 --- Spent Mushroom compost (SMC) Production --- p.44 / Chapter 2.2 --- Characterization of SMC --- p.46 / Chapter 2.2.1 --- pH --- p.46 / Chapter 2.2.2 --- Electrical conductivity --- p.46 / Chapter 2.2.3 --- "Carbon, hydrogen, nitrogen and sulphur contents" --- p.46 / Chapter 2.2.4 --- Infrared spectroscopic study --- p.47 / Chapter 2.2.5 --- Metal analysis --- p.47 / Chapter 2.2.6 --- Anion content --- p.47 / Chapter 2.2.7. --- Chitin assay --- p.48 / Chapter 2.3 --- Extraction of PCP --- p.49 / Chapter 2.3.1 --- Selection of extraction solvent --- p.49 / Chapter 2.3.2 --- Selection of desorbing agent --- p.49 / Chapter 2.3.3 --- Extraction efficiency --- p.50 / Chapter 2.4 --- Adsorption of Pentachlorophenol on SMC --- p.50 / Chapter 2.4.1 --- Preparation of pentachlorophenol (PCP) stock solution --- p.50 / Chapter 2.4.2 --- Batch adsorption experiment --- p.51 / Chapter 2.4.3 --- Quantification of PCP by HPLC --- p.51 / Chapter 2.4.4 --- Data analysis for biosorption --- p.51 / Chapter 2.4.5 --- Optimization of PCP adsorption --- p.52 / Chapter 2.4.5.1 --- Effect of contact time --- p.52 / Chapter 2.4.5.2 --- Effect of initial pH --- p.52 / Chapter 2.4.5.3 --- Effect of incubation temperature --- p.53 / Chapter 2.4.5.4 --- Effect of shaking speed --- p.53 / Chapter 2.4.5.5 --- Effect of initial PCP concentration and amount of biosorbent --- p.53 / Chapter 2.4.6 --- Adsorption isotherm --- p.53 / Chapter 2.4.7 --- Effect of removal efficiency on reuse of biosorbent --- p.54 / Chapter 2.5 --- Biodegradation by Isolated Bacterium --- p.54 / Chapter 2.5.1 --- Isolation of PCP-tolerant bacteria from mushroom compost --- p.54 / Chapter 2.5.2 --- Screening for the best PCP-tolerant bacterium --- p.54 / Chapter 2.5.3 --- Identification of the isolated bacterium --- p.55 / Chapter 2.5.3.1 --- 16S ribosomal DNA sequencing --- p.55 / Chapter 2.5.3.1.1 --- Extraction of DNA --- p.55 / Chapter 2.5.3.1.2 --- Specific PCR for 16S rDNA --- p.56 / Chapter 2.5.3.1.3 --- Gel electrophoresis --- p.57 / Chapter 2.5.3.1.4 --- Purification of PCR products --- p.57 / Chapter 2.5.3.1.5 --- Sequencing of 16S rDNA --- p.58 / Chapter 2.5.3.2 --- Gram staining --- p.60 / Chapter 2.5.3.3 --- Biolog Microstation System --- p.60 / Chapter 2.5.3.4 --- MIDI Sherlock Microbial Identification System --- p.61 / Chapter 2.5.4 --- Optimization of PCP degradation by PCP-degrading bacterium --- p.62 / Chapter 2.5.4.1 --- Effect of incubation time --- p.63 / Chapter 2.5.4.2 --- Effect of shaking speed --- p.63 / Chapter 2.5.4.3 --- Effect of initial PCP concentration and inoculum size --- p.63 / Chapter 2.5.4.4 --- Study of PCP degradation pathway by isolated bacterium using GC-MS --- p.64 / Chapter 2.6 --- Biodegradation by Fungus Pleurotus pulmonarius --- p.64 / Chapter 2.6.1 --- Optimization of PCP degradation by P. pulmonarius --- p.65 / Chapter 2.6.1.1 --- Effect of incubation time --- p.65 / Chapter 2.6.1.2 --- Effect of shaking speed --- p.65 / Chapter 2.6.1.3 --- Effect of initial PCP concentration and inoculum size --- p.65 / Chapter 2.6.2 --- Study of PCP degradation pathway by fungus using GC-MS --- p.65 / Chapter 2.6.3 --- Specific enzyme assays --- p.66 / Chapter 2.6.3.1 --- Extraction of protein and enzymes --- p.66 / Chapter 2.6.3.2 --- Protein --- p.66 / Chapter 2.6.3.3 --- Laccase --- p.67 / Chapter 2.6.3.4 --- Manganese peroxidase (MnP) --- p.67 / Chapter 2.6.4 --- Microtox® assay --- p.67 / Chapter 2.7 --- Statistical Analysis --- p.68 / Chapter 3. --- Results --- p.69 / Chapter 3.1 --- Physico-chemical Properties of SMC --- p.69 / Chapter 3.2 --- Extraction Efficiency and Desorption Efficiency of PCP --- p.69 / Chapter 3.3 --- Batch Adsorption Experiments --- p.76 / Chapter 3.3.1 --- Optimization of adsorption conditions --- p.76 / Chapter 3.3.1.1 --- Effect of contact time --- p.76 / Chapter 3.3.1.2 --- Effect of initial pH --- p.76 / Chapter 3.3.1.3 --- Effect of shaking speed --- p.79 / Chapter 3.3.1.4 --- Effect of incubation temperature --- p.79 / Chapter 3.3.1.5 --- Effect of initial PCP concentration and amount of biosorbent --- p.79 / Chapter 3.3.2 --- Reuse of SMC --- p.83 / Chapter 3.3.3 --- Isotherm plot --- p.83 / Chapter 3.4 --- Biodegradation by PCP-degrading Bacterium --- p.86 / Chapter 3.4.1 --- Isolation and purification of PCP-tolerant bacteria --- p.86 / Chapter 3.4.2 --- Identification of the isolated bacterium --- p.90 / Chapter 3.4.2.1 --- 16S rDNA sequencing --- p.90 / Chapter 3.4.2.2 --- Gram staining --- p.90 / Chapter 3.4.2.3 --- Biolog MicroPlates Identification System --- p.90 / Chapter 3.4.2.4 --- MIDI Sherlock Microbial Identification System --- p.90 / Chapter 3.4.3 --- Growth curve of PCP-degrading bacterium --- p.90 / Chapter 3.4.4 --- Optimization of PCP degradation by PCP-degrading bacterium --- p.97 / Chapter 3.4.4.1 --- Effect of incubation time --- p.97 / Chapter 3.4.4.2 --- Effect of shaking speed --- p.97 / Chapter 3.4.4.3 --- Effect of initial PCP concentration and inoculum size of bacterium --- p.101 / Chapter 3.4.5 --- Determination of breakdown products of PCP by PCP-degrading bacterium --- p.101 / Chapter 3.5 --- Biodegradation by Fungus Pleurotus pulmonarius --- p.103 / Chapter 3.5.1 --- Growth curve of P. pulmonarius --- p.103 / Chapter 3.5.2 --- Optimization of PCP degradation by P. pulmonarius --- p.103 / Chapter 3.5.2.1 --- Effect of incubation time --- p.103 / Chapter 3.5.2.2 --- Effect of shaking speed --- p.103 / Chapter 3.5.2.3 --- Effect of initial PCP concentration and inoculum size of fungus --- p.108 / Chapter 3.5.3 --- Determination of breakdown products of PCP by P. pulmonarius --- p.108 / Chapter 3.5.4 --- Enzyme assays --- p.108 / Chapter 3.6 --- Integration of Biosorption by SMC and Biodegradation by P. pulmonarius --- p.112 / Chapter 3.6.1 --- Evaluation of PCP removal by an integration system --- p.112 / Chapter 3.6.2 --- Evaluation of toxicity by Micortox® assays --- p.112 / Chapter 4. --- Discussion --- p.115 / Chapter 4.1 --- Physico-chemical Properties of SMC --- p.115 / Chapter 4.2 --- Extraction Efficiency and Desorption Efficiency of PCP --- p.116 / Chapter 4.3 --- Batch Biosorption Experiment --- p.117 / Chapter 4.3.1 --- Effect of contact time --- p.117 / Chapter 4.3.2 --- Effect of initial pH --- p.118 / Chapter 4.3.3 --- Effect of shaking speed --- p.120 / Chapter 4.3.4 --- Effect of incubation temperature --- p.120 / Chapter 4.3.5 --- Effect of initial PCP concentration and amount of biosorbent --- p.121 / Chapter 4.3.6 --- Reuse of SMC --- p.122 / Chapter 4.3.7 --- Modeling of biosorption --- p.122 / Chapter 4.4 --- Biodegradation of PCP by PCP-degrading Bacterium --- p.124 / Chapter 4.4.1 --- Isolation and purification of PCP-tolerant bacterium --- p.124 / Chapter 4.4.2 --- Identification of the isolated bacterium --- p.125 / Chapter 4.4.3 --- Optimization of PCP degradation by PCP-degrading bacterium --- p.126 / Chapter 4.4.3.1 --- Effect of incubation time --- p.126 / Chapter 4.4.3.2 --- Effect of shaking speed --- p.128 / Chapter 4.4.3.3 --- Effect of initial PCP concentration and inoculum size of bacterium --- p.128 / Chapter 4.4.4 --- PCP degradation pathway by S. marcescens --- p.129 / Chapter 4.5 --- Biodegradation of PCP by Pleurotus pulmonarius --- p.130 / Chapter 4.5.1 --- Optimization of PCP degradation by P. pulmonarius --- p.130 / Chapter 4.5.1.1 --- Effect of incubation time --- p.131 / Chapter 4.5.1.2 --- Effect of shaking speed --- p.131 / Chapter 4.5.1.3 --- Effect of initial PCP concentration and inoculum size of fungus --- p.131 / Chapter 4.5.2 --- Enzyme activities --- p.132 / Chapter 4.5.3 --- PCP degradation pathway by P. pulmonarius --- p.133 / Chapter 4.6 --- Comparison of PCP Degradation between S.marcescens and P. pulmonarius --- p.133 / Chapter 4.7 --- Integration of Biosorption by SMC and Biodegradation by P. pulmonarius --- p.135 / Chapter 4.8 --- Evaluation of toxicity by Microtox® assay --- p.135 / Chapter 4.9 --- Comparison of PCP Removal by Integration System of Sorption and Fungal Biodegradation and Conventional Treatments --- p.136 / Chapter 4.10 --- Further Investigations --- p.137 / Chapter 5. --- Conclusion --- p.139 / Chapter 6. --- References --- p.142

No description available.

Groundwater at Oak Ridge National Laboratory's Field Research Center (FRC) is contaminated with U(VI) and Tc(VII), has pH values as low as 3.3, and nitrate concentrations as high as 120 mM. The objective of this research was to determine if in-situ bio-immobilization is a viable treatment alternative for this water. A laboratory column packed with crushed limestone and bicarbonate was used to model in-situ pH adjustment. Denitrification and metal reduction were modeled in columns packed with FRC sediment with ethanol as the electron donor. Two intermediate-scale physical models deployed in the field were packed with limestone and sediment and were stimulated with ethanol to support denitrification, U(VI) reduction, and Tc(VII) reduction of FRC groundwater. The limestone/bicarbonate column maintained a pH of above 5 for nearly one hundred pore volumes without significant loss in hydraulic conductivity. The high-nitrate (~120 mM) column study provided rates of denitrification (~15.25 mM/day), ethanol utilization (~13 mM/day), and technetium reduction (~120 pM/day) by sediment microorganisms, but no uranium reduction was detected. Results of the low nitrate (3 mM) column study indicate that once the pH of FRC water is adjusted to pH ~7 and nitrate is removed, uranium (~3 μM) and technetium (~500 pM) reduction occurred with ethanol as the electron donor at rates of 0.5 μM/day and 57 pM/day. Similar results were obtained in two intermediate-scale (~3 m long) physical models. Data from the high-nitrate, low-pH model indicate that the pH was increased and nitrate and technetium reduction were occurring. Decreased U(VI) concentrations were measured in the presence of high nitrate concentrations. Thus, U(VI) precipitates may form or sorption of U(VI) may occur near the inlet in the pH adjustment region. The maximum pseudo-first order rates of reduction measured during the seventh week of model operation were: nitrate at 0.76 day⁻¹, Tc(VII) at 0.28 day⁻¹, and U(VI) at 0.12 day⁻¹. Ethanol concentrations were reduced from ~180 mM to zero in ~10 days during the seventh week of model operation. No Fe(II) production was measured. Concentration data collected from the low nitrate, neutral pH model indicate that nitrate, uranium, and technetium reduction were occurring, though the model had been operational for only ~6 weeks. No Fe(II) production was detected but sulfate reduction was occurring. The results of the laboratory experiments and the performance of the intermediate-scale physical models suggest that bio-immobilization is a viable treatment alternative for the contaminated groundwater at the FRC. / Graduation date: 2004

Graduation date: 1999

Groundwater contamination on irrigated land is of concern in this nation and around the world. In order to reduce the potential of groundwater contamination by agricultural practices such as irrigation, fertilizer and pesticide application, vadose-zone monitoring and sampling are needed. The main objective of this study was to evaluate impacts of current irrigation treatments and soil structures on the migration of pollutants to groundwater. Passive CAPillary wick pan Samplers (PCAPS) and suction cups were installed in two cracking clays and one sandy soil under the pear tree root zone. PCAPS and suction cups were used to collect nitrate-nitrogen and tracer samples. Tracers were applied to track the spatial and temporal patterns of compounds that mimic nitrate-nitrogen and pesticide movement. The observed magnitude of water leaching over 3 months differed between irrigation methods and soil structures and decreased in this order: flooding over 3 months in clay soil (22.8 cm) > micro-sprinkler in clay soil (16.1 cm) > over-head sprinkler in sandy soil (4.1 cm). Leaching patterns were varied spatially; soil structures, irrigation methods, preferential flow, and high water table may have been responsible for the spatial variation of leaching. Mass recovery of all three tracers, including bromide, blue dye, and rhodamine had the same decreasing order: flooding in clay soil > micro-sprinkler in clay soil > over-head sprinkler in sandy soil. Average blue dye and rhodamine concentrations had the following order: flooding in clay soil > micro-sprinkler in clay > over-head sprinkler in sandy soil. Since blue dye and rhodamine have similar properties to some moderately adsorbed pesticides, we may infer that the risk of pesticide movement in three sites should also decrease in this order. Presumably pesticide movement in clay soil would have been more pronounced for flooding than sprinkler irrigation. On the annual/seasonal basis, the total mass of nitrate-nitrogen leaching differed between irrigation methods and soil structures and decreased in the following order: over-head sprinkler in sandy soil > flooding in clay soil > micro-sprinkler in clay soil. The annual average nitrate-nitrogen concentration observed under over-head sprinkler in sandy soil was 15 mg/l over the maximum allowed concentration level (10 mg/l) by the EPA while seasonal nitrate-nitrogen concentration was low in clay soil under current irrigation practices. Strong evidence suggested the occurrence of preferential flow in this study. Preferential flow may contribute to high water leachate, nitrate and pesticide migration. High correlation coefficients between paired PCAPS indicated that PCAPS have similar responses to water and solute leaching. Several improvements in PCAPS are needed to obtain representative samples under severe flooding conditions. Limited data suggested that ultra-low rate irrigation devices could reduce the water leaching and the potential of pollutant migration to the groundwater because ultra-low rate application devices minimize the soil macropore flow. / Graduation date: 1995

Environmental issues are manifest throughout our lives. Sport is no exception. The concern for sustainable sport management has precipitated efforts to reduce the ecological footprint of sport, and to use sport to raise environmental awareness. This dissertation examines the challenges of reducing the ecological footprint of an urban recreational sport: disc golf. The project consists of four studies. The ecological degradation associated with the sport of disc golf is reported in the first study. It is shown that disc golf increases soil compaction, which yields greater soil erosion and a decrease in vegetation cover. The second study examines player behaviors, and identifies two behaviors that are clearly related to the environmental degradation, and that could be reduced without interfering with the game: (1) dragging bags with disc golf equipment along the ground, and (2) using tress as practice targets. The subculture of disc golfers is explored in the third study in order to identify characteristics of the subculture that could be leveraged to foster the desired behavioral changes. Disc golfers felt a strong sense of ownership and attachment to the park in which they played, and placed a high value on the sport and the park in which they played. However, disc golfers were unaware of the environmental effects of their behaviors. In the final study, a brochure was distributed to players that informed them about the environmental damage caused by dragging bags and using trees for target practice, and that appealed to their sense of ownership and attachment to the park in which they played. A multiple baseline study of disc golfer behaviors in three parks demonstrated that the brochure reduced the target behaviors so significantly that they were virtually extinguished. It is concluded that behavioral management strategies can be useful tools for environmental management of urban sport settings. It is suggested that appeals to supportive subcultural values enable self-policing of target behaviors. It is also noted that education can be an effective intervention when the values are supportive but player ignorance of their impact has allowed environmentally damaging behaviors to be tolerated. / text

The scarcity of fossil fuel and its environmental impact have shifted the world focus on green innovations At a time when the use of fossil fuel means increasing energy scarcity and an environmental crisis in the world in which we live, we need green innovations now more than ever. Growing attention has been drawn to the use of biofuels, such as bioethanol and biodiesel, which have gradually come to make up part of the total energy supply. Uncertainties about the environmental and ecological aspects of the production and consumption of biofuel still exist despite its rapid development. A life cycle analysis (LCA) evaluates the two principal functional parameters 1) energy efficiency and 2) Greenhouse Gas (GHG) balance of different feedstocks for biodiesel production from the cradle to the grave. By accounting a life cycle analysis stage by stage, we can ascertain the change in GHG emissions and energy demand that result from the various uses of feedstocks for the production of biodiesel. In this thesis, various life cycle analysis models are reviewed and evaluated with emphasis on specific biofuels. Different LCA models depend on different LCA calculation under different situations, including GREET, LEM, SimaPro, etc. The software SimaPro was used to compare the life cycle GHG emissions and energy demand from conventional petroleum fuels and several hydro-processed renewable green diesels. A consistent methodology was used for selected fuel pathways to facilitate relatively equitable comparisons. The building of life cycle flow tree in SimaPro combined the input and output with an emphasis on the following stages 1) raw material farming and acquisition, 2)liquid fuel production, 3)transport, 4)refueling, 5)liquid fuel conversion to biodiesel and 6) end uses. Consistent impact assessment methods were chosen for simulation, equitable comparisons and comprehensive analysis of selected fuel pathways for the calculation of Global Warming Potential (GWP) and Cumulative Energy Demand (CED). However, the results of the entire lifetime estimates vary dramatically in production chains, which make it difficult to take a holistic view about energy intake and yields, economic costs and values, environmental impacts and their benefits. Apart from the diversity in system boundaries and life cycle inventories, a variance in terminologies and the limitations of interdisciplinary communication are the main factors that affect the quality of the results. / published_or_final_version / Mechanical Engineering / Master / Master of Philosophy

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