Lam, Shu Kee. / Thesis (M.Phil.)--Chinese University of Hong Kong, 2007. / Includes bibliographical references (leaves 206-219). / Abstracts in English and Chinese. / Abstract --- p.i / Abstract (in Chinese) --- p.iv / Acknowledgements --- p.vi / Table of contents --- p.vii / List of tables --- p.xii / List of figures --- p.xvi / List of plates --- p.xvii / Chapter CHAPTER 1 --- INTRODUCTION / Chapter 1.1 --- Research background --- p.1 / Chapter 1.2 --- Conceptual framework --- p.4 / Chapter 1.3 --- Objectives of the study --- p.8 / Chapter 1.4 --- Significance of the study --- p.9 / Chapter 1.5 --- Organization of the thesis --- p.10 / Chapter CHAPTER 2 --- LITERATURE REVIEW / Chapter 2.1 --- Introduction --- p.12 / Chapter 2.2 --- Use of hydroseeding in slope bioengineering works --- p.12 / Chapter 2.3 --- Problems associated with hydroseeded slopes --- p.12 / Chapter 2.4 --- Common Bermudagrass used in hydroseeding --- p.13 / Chapter 2.5 --- "Sludge disposal, potentials and problems" --- p.14 / Chapter 2.5.1 --- Properties and disposal of sludge --- p.14 / Chapter 2.5.2 --- Use of sludge and potential problems --- p.16 / Chapter 2.5.3 --- Heavy metals in sludge --- p.19 / Chapter 2.5.3.1 --- Cadmium --- p.22 / Chapter 2.5.3.2 --- Chromium --- p.22 / Chapter 2.5.3.3 --- Copper --- p.23 / Chapter 2.5.3.4 --- Nickel --- p.24 / Chapter 2.5.3.5 --- Lead --- p.24 / Chapter 2.5.3.6 --- Zinc --- p.25 / Chapter 2.5.4 --- Speciation of heavy metals --- p.25 / Chapter 2.5.5 --- Factors affecting the bioavailability of heavy metals --- p.26 / Chapter 2.5.5.1 --- Reaction pH --- p.26 / Chapter 2.5.5.2 --- Organic matter --- p.28 / Chapter 2.5.5.3 --- Fertilizers --- p.29 / Chapter 2.5.6 --- Effect of heavy metals on plant growth --- p.29 / Chapter 2.5.7 --- Effect of heavy metals on animals and water bodies --- p.31 / Chapter 2.6 --- "Lime, heavy metals and plant growth" --- p.32 / Chapter 2.6.1 --- Effect of lime on heavy metal dynamics --- p.32 / Chapter 2.6.1.1 --- Competition with heavy metals for adsorption sites --- p.32 / Chapter 2.6.1.2 --- Immobilization of heavy metals --- p.32 / Chapter 2.6.2 --- Effect of lime on plant growth --- p.34 / Chapter 2.7 --- Effect of precipitation on slopes --- p.35 / Chapter 2.7.1 --- Infiltration --- p.35 / Chapter 2.7.2 --- Surface runoff --- p.38 / Chapter 2.7.3 --- Soil erosion --- p.39 / Chapter 2.8 --- Summary --- p.42 / Chapter CHAPTER 3 --- EFFECT OF SLUDGE AND LIME ON ABOVEGROUND BIOMASS OF COMMON BERMUDAGRASS / Chapter 3.1 --- Introduction --- p.43 / Chapter 3.2 --- Materials and methods --- p.44 / Chapter 3.2.1 --- Materials --- p.45 / Chapter 3.2.2 --- Experimental design --- p.46 / Chapter 3.2.3 --- Grass clipping and pre-treatment --- p.49 / Chapter 3.3 --- Chemical analysis --- p.50 / Chapter 3.3.1 --- Properties of decomposed granite --- p.50 / Chapter 3.3.2 --- "Properties of sludge," --- p.52 / Chapter 3.3.3 --- Nitrogen of grass clippings --- p.52 / Chapter 3.4 --- Statistical analysis --- p.53 / Chapter 3.5 --- Results and discussion --- p.54 / Chapter 3.5.1 --- Properties of DG and sludge --- p.54 / Chapter 3.5.2 --- Aboveground biomass of grass --- p.56 / Chapter 3.5.3 --- Effect of sludge on aboveground biomass --- p.63 / Chapter 3.5.4 --- Effect of lime on aboveground biomass --- p.66 / Chapter 3.5.5 --- Synergic effect of sludge and lime on aboveground biomass --- p.68 / Chapter 3.5.6 --- "Effect of sludge on nitrogen uptake by grass shoots," --- p.69 / Chapter 3.6 --- Summary --- p.72 / Chapter CHAPTER 4 --- EFFECT OF SLUDGE AND LIME ON HEAVY METAL UPTAKE BY COMMON BERMUDAGRASS / Chapter 4.1 --- Introduction --- p.74 / Chapter 4.2 --- Materials and methods --- p.77 / Chapter 4.2.1 --- Materials and experimental design --- p.77 / Chapter 4.2.2 --- Analysis of heavy metals in grass shoots --- p.77 / Chapter 4.2.3 --- Reaction pH at the end of Part 1 --- p.77 / Chapter 4.2.4 --- Statistical analysis --- p.78 / Chapter 4.3 --- Results and discussion --- p.78 / Chapter 4.3.1 --- Cumulative uptake of heavy metals by common Bermudagrass --- p.79 / Chapter 4.3.2 --- Effect of sludge on heavy metal uptake --- p.84 / Chapter 4.3.3 --- Effect of lime on heavy metal uptake --- p.86 / Chapter 4.3.4 --- Synergic effect of sludge and lime on cumulative heavy metal uptake --- p.88 / Chapter 4.3.5 --- Effect of fertilizer addition --- p.91 / Chapter 4.3.6 --- Concentration of heavy metals in grass --- p.93 / Chapter 4.3.7 --- Effect of pH on heavy metal uptake --- p.98 / Chapter 4.3.8 --- Effect of heavy metal uptake on aboveground biomass --- p.100 / Chapter 4.4 --- Summary --- p.103 / Chapter CHAPTER 5 --- EFFECT OF SLUDGE AND LIME ON HEAVY METALS IN LEACHATE / Chapter 5.1 --- Introduction --- p.106 / Chapter 5.2 --- Materials and methods --- p.107 / Chapter 5.2.1 --- Leachate collection --- p.108 / Chapter 5.2.2 --- Analysis of leachate --- p.109 / Chapter 5.2.3 --- Statistical analysis --- p.109 / Chapter 5.3 --- Results and discussion --- p.110 / Chapter 5.3.1 --- Effect of sludge and lime on leachate volume --- p.110 / Chapter 5.3.2 --- Leachate pH and the effect of sludge and lime --- p.115 / Chapter 5.3.3 --- Heavy metal contents in leachate --- p.119 / Chapter 5.3.4 --- Effect of sludge and lime on the leaching of heavy metals --- p.121 / Chapter 5.3.5 --- Effect of pH on the leaching of heavy metals --- p.125 / Chapter 5.4 --- Summary --- p.126 / Chapter CHAPTER 6 --- "LEACHATE, SURFACE RUNOFF, SEDIMENT YIELD AND THEIR HEAVY METALS" / Chapter 6.1 --- Introduction --- p.128 / Chapter 6.2 --- Materials and methods --- p.130 / Chapter 6.2.1 --- Materials --- p.130 / Chapter 6.2.2 --- Experimental design --- p.132 / Chapter 6.2.3 --- Rainfall intensities in simulation experiment --- p.134 / Chapter 6.2.4 --- Selection of slope gradient --- p.136 / Chapter 6.2.5 --- Rainfall simulation --- p.136 / Chapter 6.2.6 --- "Leachate, surface runoff and runoff sediment" --- p.137 / Chapter 6.2.7 --- Properties of decomposed granite and sludge --- p.138 / Chapter 6.2.8 --- "Heavy metals in leachate, surface runoff and runoff sediment" --- p.139 / Chapter 6.2.9 --- Statistical analysis --- p.140 / Chapter 6.3 --- Results and discussion --- p.140 / Chapter 6.3.1 --- Properties of DG and sludge --- p.140 / Chapter 6.3.2 --- "Leachate, surface runoff and runoff sediment production" --- p.142 / Chapter 6.3.3 --- "Heavy metal concentrations in leachate, surface runoff and runoff sediment" --- p.153 / Chapter 6.3.3.1 --- Heavy metal concentrations in leachate --- p.153 / Chapter 6.3.3.2 --- Heavy metal concentrations in runoff --- p.163 / Chapter 6.3.4 --- Cumulative loss of heavy metals --- p.170 / Chapter 6.3.4.1 --- Cumulative loss of heavy metals from leachate --- p.170 / Chapter 6.3.4.2 --- Cumulative loss of heavy metals from runoff --- p.178 / Chapter 6.3.4.3 --- "Heavy metal loss from leachate, surface runoff and runoff sediment" --- p.185 / Chapter 6.4 --- Summary --- p.189 / Chapter CHAPTER 7 --- CONCLUSIONS / Chapter 7.1 --- Summary of major findings --- p.192 / Chapter 7.2 --- Implications of the study --- p.196 / Chapter 7.2.1 --- Potential use of sludge in slope bioengineering works --- p.196 / Chapter 7.2.2 --- Measures to optimize the benefits of sludge in land application --- p.198 / Chapter 7.3 --- Limitations of the study --- p.200 / Chapter 7.4 --- Suggestions for further study --- p.202 / REFERENCES --- p.206 / APPENDICES --- p.220

Em muitas partes do mundo o aumento na demanda de água tem estimulado pesquisas relacionadas às práticas de reuso sustentáveis. Dentre as atividades humanas, a irrigação agrícola se revela como uma das práticas de maior consumo de recursos hídricos naturais. Uma alternativa para minimizar este problema é o reuso de efluentes gerados por sistemas biológicos de tratamento de esgotos. O objetivo desta pesquisa foi avaliar os efeitos da irrigação com esgoto tratado na dinâmica do carbono (C) e nitrogênio (N) e na atividade microbiana de um solo sob pastagem. O estudo foi conduzido em uma pastagem de capim-Bermuda Tifton 85 (Lins-SP), onde o delineamento experimental foi o de blocos completos com seis tratamentos: SI (sem irrigação e sem fertilização), A100 (água potável + 520 kg de N ha-1 ano-1); E0, E33, E66 e E100 (irrigação com esgoto tratado + 0, 33, 66 e 100% de 520 kg de N ha-1 ano-1). Os tratamentos receberam entre 420 a 1500 mm de esgoto tratado e água por ano, correspondendo a uma entrada pelo esgoto tratado de 640 a 2300 kg ha-1 ano-1 de C e de 135 a 480 kg ha-1 ano-1 de N. Utilizando como referência os estoques de C e N de SI, o menor decréscimo de C ocorreu em E33 (1,2 Mg ha-1) e o maior em A100 (7,9 Mg ha-1). Alterações no estoque de N do solo ocorreram após quatro anos de irrigação, onde A100 apresentou decréscimo de cerca de 450 kg de N ha-1. Os estoques de N dos tratamentos irrigados com esgoto tratado não foram afetados. A entrada de C e N orgânicos pelo esgoto tratado não afetaram a composição isotópica do C (\'delta\' 13C) e do N (\'delta\' 15N) da fração estável da matéria orgânica do solo (MOS) do solo. A alteração de \'delta\' 13C nos solos dos tratamentos irrigados (-0,7 a -1,2%o ), em relação a SI, foi resultante da mineralização do carbono orgânico remanescente do solo (plantas C3). Os valores de \'delta\' 15N do N da MOS (0 a 5 cm) foram significativamente maiores (+2,2%o) nos tratamentos irrigados com esgoto tratado do que em SI e A100, refletindo diferenciadas taxas e processos de ciclagem de N. A abundância natural de 15N nas folhas do capim-Bermuda refletiu a composição isotópica do N do solo, com enriquecimento de +2,5%o e +4,9%o em relação a A100 e SI, respectivamente. As taxas líquidas de mineralização e nitrificação negativas ou nulas nas épocas Seca-04, Chuvas-05 e Seca-05 indicaram predominância de processos de imobilização do N pela microbiota em virtude uma alta relação C:N da MOS. Nas épocas de Chuvas-06 e Seca-06 as taxas tornaramse positivas indicando a diminuição da relação C:N da MOS, término do efeito priming e, portanto, ciclagem interna de N. Os solos dos tratamentos apresentaram baixo consumo (-0,1kg de C ha-1 sem-1) ou pequena emissão média de CH4 (+0,8 kg de C ha-1 sem-1). A disponibilidade de N e a umidade do solo não representaram fatores limitantes nos tratamentos, assim as emissões de CO2 não diferiram entre si na maior parte das datas de coleta (médias de 14,7 e 12,2 Mg de C ha-1 para épocas de chuvas e seca, respectivamente). Os maiores fluxos de CO2 relacionaram-se com os períodos de maior precipitação e/ou irrigação do que com os tratamentos. Os maiores fluxos de N2O foram observados após a aplicação de N mineral nos tratamentos irrigados com esgoto tratado, sendo proporcionais as maiores quantidades de N adicionado. As relações médias entre o C da biomassa microbiana e o C orgânico total (Cmic:COT) dos tratamentos variaram de 2,3 a 3,8% ao longo das épocas, indicando boa resiliência do agroecossistema, onde os microrganismos apresentaram variações temporárias de biomassa. Interferências positivas do manejo (corte do capim e fertilização com N mineral) resultando em aumento de Cmic foram observadas no 1º ano hidrológico e Seca-06, como resultado da maior umidade do solo e com isso condições mais favoráveis para a disponibilização de C. Na Seca-04, com o aumento da atividade metabólica, e Chuvas-05, sem alteração deste parâmetro, ao longo do manejo, o quociente metabólico (qCO2) apresentou um cenário de eficiente conversão de C-CO2 em biomassa microbiana. No 2º ano hidrológico, com a diminuição das lâminas de irrigação os tratamentos irrigados e fertilizados apresentaram decréscimo de Cmic e respiração mantida (Seca-05) ou aumentada (Chuvas-06) após o manejo, os valores de qCO2 indicaram condições desfavoráveis a microbiota. Com a pouca interferência dos tratamentos, os indicadores eco-fisiológicos não foram suficientemente sensíveis para mostrar o manejo com menor impacto na qualidade do solo, revelando apenas cenários do metabolismo microbiano ao longo das práticas agrícolas. A quantidade de C exportada por E33, como biomassa (15,2 Mg de C ha-1 ano-1) não diferiu das maiores produções, a alteração em seu estoque de C foi inferior aos demais tratamentos irrigados, sugerindo ser o manejo mais sustentável, em termos de C, utilizando esgoto tratado como irrigação. Os tratamentos E100 (Seca-04) e E66 (Chuvas-05) representaram os manejos com as maiores exportações de N, respondendo linearmente até 940 ha-1 de N ano-1. De acordo com as variáveis avaliadas, o manejo com maior sustentabilidade produtiva e ambiental foi o tratamento E100, situação onde as saídas de N não superaram as entradas / In many parts of the world, the increasing demand and, especially in arid regions the natural scarcity of water has stimulated researches in terms of sustainable water reuse practices. Within human activities, common agricultural irrigation reveals one of the most consumptive practices of natural water resources. One alternative to minimize this problem represents the reuse of effluent generated by biological sewage treatment systems. The objective of this study was to investigate the impact of treated wastewater application in the dynamic of carbon (C) and nitrogen (N), and microbial metabolism of a soil under pasture. The study was carried out at Lins, São Paulo State, Brazil on a Tifton 85 bermudagrass pasture irrigated with secondary treated sewage effluent using a randomized complete block design with six treatments: SI (control, without irrigation and fertilization), W100 (potable water irrigation + 520 kg of N ha-1 year-1); E0, E33, E66 and E100 (treated wastewater irrigation + 0, 33, 66 and 100% of 520 kg of N ha-1 year-1). Samples of treated effluent/water, soil, plant (litter fall), and gases were taken from January 2004 through October 2007 and the treatments were kept under irrigation management receiving between 420 and 1,500 mm of water and treated sewage corresponding to an input of 640 to 2,300 kg ha-1 yr-1 of C and 135 to 480 kg ha-1 year-1 of N . Soil C stocks decreased slightly in the E33 treatment (-1.3 Mg ha-1) and a larger decrease was observed in W100 (-7.9 Mg ha-1). The inputs of organic C by the treated sewage did not affect the soil carbon isotopic composition (\'delta\' 13C), and in the irrigated treatments measured shifts in the isotopic signature (-0,7 a -1,2%o ) were caused by the mineralization of the remaining soil organic matter (SOC) (C3 plants). After 4 years of irrigation the only significant changes in soil N stocks were found in the W100 treatment (-450 kg de N ha-1). The \'deta\' 15N signature of the soil organic matter (0-5 cm depth) in the treatments irrigated with treated sewage was significantly higher (+2,2%o) than WI and W100, this suggests higher nitrogen cycling. The \'delta\' 15N signature of grass was enriched relative to the soil of W100 and WI +2,5%o and +4,9%o respectively). Negative or null rates of mineralization and nitrification occurred in the dry season of 2004, rainy and dry season of 2005 indicated an immobilization by the microorganisms, as a result of a high C:N ratio in the SOC. In the dry and wet seasons of 2006, mineralization and nitrification rates became positive suggesting a decrease of the C:N ratio, and the end of both priming effect and, thus the beginning of N cycling in the soil organic matter. Soils in the treatments showed low CH4 consumption rates (-0.1 kg de C ha-1 semester-1) and in some cases low emissions (+0.8 kg de C ha-1 emester-1). Nitrogen availability and soil moisture did not appear to be limiting factors for the treatments, thus CO2 emissions did not differ from each other over the collections (averages of 14.7 e 12.2 Mg of C ha-1 for wet and dry season, respectively). The highest CO2 fluxes were more related to periods of high precipitation and/or irrigation than to the applied treatments. The highest emissions of nitrous oxide were observed after the application of mineral N to the treatments irrigated with treated sewage, and the emissions were straightly related to the N addition. Values of Cmic:TOC (microbial C : Total Organic C) in the treatments averaged between 2.3 and 3.8 % through the seasons which means a significant resilience of the ecosystem, indicating that soil microbial community varied seasonally in their Cmic. Addition of mineral nitrogen and grass cutting practices influenced positively resulting in increase of Cmic in the first hydrological year and in the dry season in 2006, as well as an increase of soil moisture resulting in good conditions for C availability. With the increase metabolic activity in the dry season of 2004 and a continuous metabolic activity in the rainy season in 2005, the metabolic quotient (qCO2) resulted in an efficient scenario of conversion of C-CO2 into microbial biomass. In the second year, with a decrease of the irrigation depths and an increase in salts concentration after fertilization, the treatments irrigated with treated sewage and fertilizers presented decrease of Cmic with stable respiration (dry season 2005) or increase respiration (wet season 2006) after the management, and as a result qCO2 indicated inappropriate conditions for the microorganisms. In the dry season (2006) the physiological profile of the soil remained instable with no stress and Cmic increased and soil respiration remained inaltered. According to these results, the microbial indicators were not efficiently sensitive for revealing the more impacting management to the soil. The co-physiological indicators showed only the regular microbial metabolism along the agricultural practices. Carbon biomass exported by the grass in the E33 (15.2 Mg C ha-1 yr-1) did not differ from the biomass produced in the other treatments and the alterations in its C stocks were low compared to the other treatments. As a result, E33 seems to be the more sustainable and efficient practice for treated sewage use. Both the E66 and E100 treatments had high measured rates of N export, responding linearly up to 940 kg of N ha-1 yr-1. Thus, according to the variables studied, the management with highest sustainability was E100 where N outputs did not surpass the inputs

by Ngar, Yuen-ngor. / Thesis (M.Phil.)--Chinese University of Hong Kong, 1993. / Includes bibliographical references (leaves 186-196). / Chapter Chapter 1 --- Introduction Page / Chapter 1.1 --- Sludge as a waste problem --- p.1 / Chapter 1.2 --- The degraded geological environment of Hong Kong --- p.2 / Chapter 1.3 --- Use of weathered granitic material and sand as planting media --- p.3 / Chapter 1.4 --- Need of soil improvement material --- p.4 / Chapter 1.5 --- Potential for land application of sewage sludge --- p.5 / Chapter 1.6 --- Objectives of study --- p.6 / Chapter 1.7 --- Significance of study --- p.6 / Chapter Chapter 2 --- Literature Review / Chapter 2.1 --- Soil organic amendment for vegetation establishment --- p.9 / Chapter 2.2 --- Types and properties of sewage sludge --- p.10 / Chapter 2.3 --- Guidelines for land application of sludge --- p.12 / Chapter 2.3.1 --- Cation exchange capacity --- p.13 / Chapter 2.3.2 --- Zinc equivalent concept --- p.14 / Chapter 2.4 --- Effects of sludge on soil chemical and physical properties --- p.15 / Chapter 2.4.1 --- Chemical properties --- p.15 / Chapter 2.4.2 --- Physical properties --- p.18 / Chapter 2.5 --- Effects of sludge application on vegetation --- p.19 / Chapter 2.5.1 --- Germination --- p.19 / Chapter 2.5.2 --- Grass growth --- p.20 / Chapter 2.6.1 --- Choice of heavy metals for study --- p.21 / Chapter 2.6.2 --- Factors governing heavy metal availability --- p.25 / Chapter 2.6.3 --- Effects of lime on sludge-amended soil and the heavy metal availability --- p.26 / Chapter 2.6.4 --- Assessing available sludge-borne heavy metals --- p.27 / Chapter Chapter 3 --- Germination and seedling growth of bermudagrass in sludge-amended sand and CDG / Chapter 3 .1 --- Introduction --- p.30 / Chapter 3.2 --- Experimental design --- p.31 / Chapter 3.3 --- Experimental results --- p.34 / Chapter 3.3.1 --- Seed germination --- p.34 / Chapter 3.3.2 --- Seedlings and biomass growth --- p.35 / Chapter 3.3.3 --- DTPA-Extractable heavy metals --- p.39 / Chapter 3.3.4 --- Total heavy metals in plant tissue --- p.44 / Chapter 3.3.5 --- Chemical properties of the soil substrates --- p.49 / Chapter 3.4 --- Discussion --- p.54 / Chapter 3.4.1 --- Germination --- p.54 / Chapter 3.4.2 --- Nutrient effect --- p.56 / Chapter 3.4.3 --- Heavy metal availability from substrates --- p.59 / Chapter 3.4.4 --- Heavy metal uptake by the seedlings --- p.61 / Chapter 3.4.4.1 --- Metal uptake efficiency --- p.61 / Chapter 3.4.4.2 --- Amount of heavy metal uptake --- p.63 / Chapter 3.4.5 --- Textural characteristics --- p.66 / Chapter 3.5 --- Conclusions --- p.67 / Chapter Chapter 4 --- Growth and heavy metal uptake by bermudagrass grown in sludge-amended substrates / Chapter 4.1 --- Introduction --- p.70 / Chapter 4.2 --- Experimental design --- p.71 / Chapter 4.3 --- Results --- p.74 / Chapter 4.3.1 --- Biomass growth --- p.74 / Chapter 4.3.2 --- Heavy metal content of plant tissues --- p.82 / Chapter 4.3.2.1 --- Heavy metal content of the shoot --- p.83 / Chapter 4.3.2.2 --- Heavy metal content of the root --- p.89 / Chapter 4.3.3 --- Comparing the heavy metal levels in the shoot and root portions --- p.93 / Chapter 4.3.4 --- DTPA-extractable heavy metal content in soil substrates --- p.94 / Chapter 4.3.5 --- Chemical properties of the substrates --- p.100 / Chapter 4.4 --- Discussion --- p.103 / Chapter 4.4.1 --- Shoot biomass (First clipping) --- p.104 / Chapter 4.4.2 --- Shoot biomass (Second clipping) --- p.105 / Chapter 4.4.3 --- Shoot biomass ratio between the two clippings --- p.107 / Chapter 4.4.4 --- Total shoot biomass --- p.108 / Chapter 4.4.5 --- Root biomass and root: shoot ratios --- p.112 / Chapter 4.4.5.1 --- Nutrient effect --- p.113 / Chapter 4.4.5.2 --- Heavy metal phytotoxicity --- p.115 / Chapter 4.4.6 --- Total biomass production --- p.117 / Chapter 4.5 --- Conclusions --- p.118 / Chapter Chapter 5 --- Effect of lime on the growth and heavy metal uptake of bermudagrass in sludge-amended substrates / Chapter 5.1 --- Introduction --- p.121 / Chapter 5.2 --- Experimental design --- p.123 / Chapter 5.3 --- Results --- p.125 / Chapter 5.3.1 --- Biomass growth --- p.126 / Chapter 5.3.2 --- DTPA-extractable heavy metals --- p.133 / Chapter 5.3.3 --- Heavy metal uptake by the shoot portion --- p.138 / Chapter 5.3.4 --- Heavy metal uptake by the root portion --- p.147 / Chapter 5.3.5 --- Comparing metal uptake between shoot and root portions --- p.151 / Chapter 5.3.6 --- Chemical properties of substrates --- p.155 / Chapter 5.4 --- Discussion --- p.157 / Chapter 5.4.1 --- Effect of sludge and lime treatments on pH --- p.158 / Chapter 5.4.2 --- Patterns of DTPA-extractable metals and plant uptake --- p.159 / Chapter 5.4.2.1 --- Variation of heavy metal levels with liming rates --- p.160 / Chapter 5.4.2.2 --- Variation of heavy metal levels with sludge loading rates --- p.161 / Chapter 5.4.2.3 --- Bermudagrass as metal accumulator --- p.162 / Chapter 5.4.3 --- Metal uptake by the root and shoot --- p.162 / Chapter 5.4.3.1 --- Antagonistic interactions --- p.163 / Chapter 5.4.3.2 --- Parititioning of heavy metals in shoot and root --- p.163 / Chapter 5.4.4 --- Poor biomass growth --- p.166 / Chapter 5.4.4.1 --- Heavy metal toxicity --- p.166 / Chapter 5.4.4.2 --- Effect of poor soil conditions --- p.167 / Chapter 5.5 --- Conclusions --- p.177 / Chapter Chapter 6 --- Conclusions / Chapter 6.1 --- Summary of findings --- p.179 / Chapter 6.2 --- Implications of the study --- p.180 / Chapter 6.3 --- Limitations --- p.182 / Chapter 6.4 --- Suggestions for further studies --- p.184 / References --- p.186 / Appendix

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Made available in DSpace on 2016-04-28T20:15:31Z (GMT). No. of bitstreams: 1 2008 - Melissa Carvalho Machado do Couto Chambarelli.pdf: 767679 bytes, checksum: 28c75b5091c80e9da0651ba953952d51 (MD5) Previous issue date: 2008-02-29 / Coordena??o de Aperfei?oamento de Pessoal de N?vel Superior / The knowledge of cyathostomin infective larvae population level presents onto pasture is important to epidemiological purposes, estimating parasitic risk infection to horses and helping on setting up integrated control programs. The present study was elaborated in three parts: first is about the migratory dynamic and survival of cyathostomin infective larvae on Bermuda grass pasture for 12 months. Feces and grass samples were collected weekly at 8 a.m., 1 p.m. and 5 p.m. The samples were weighted and processed by Baermann technique. Higher survival of L3 was found at dry season, 15 and 12 weeks on feces and sward respectively, at rainy season the survival was smaller. The infective larvae were recovered during three times and the Kruskal-Wallis test did not present significance among them. At the second part, the ecology of cyathostomin infective larvae was studied for 24 months. During this period, samples of feces and grass (apex and base) were collected weekly. Samples were processed the same way as in the first part of the study. In the feces, cyathostomin L3 survived for up to 15 weeks, with higher recovery during the rainy period (46,228 kg-1.dh) and on the grass for up to 12 weeks. The recovery of L3 was greater during the dry period in the grass base (1,868 kg-1.dh) rather than in the apex (809 kg-1.dh). The L3 migration from feces to grass varied during the period. The last part of the study is about the effect of irrigation on cyathostomin infective larvae migration in Bermuda grass pasture during the four seasons of the year. Fecal masses of naturally infected horses were placed on Bermuda grass pasture at the beginning of each season. Samples of feces and grass were collected every two weeks at 8 a.m. and 5 p.m. until the end of each season from September/2007 to September/2008. Samples were processed the same way as in the first part of the study. The Kruskal-Wallis non parametric test showed a significant difference for L3 recovery in each season. The test did not present significance between the two times sampling. These results suggest that in conditions of Baixada Fluminense tropical climate horses are in permanent risk of infection. / O conhecimento do grau de contamina??o das pastagens pelas larvas infectantes de ciatostom?neos ? importante para os prop?sitos epidemiol?gicos, determinando o risco de infec??o para os eq?inos e podendo tamb?m auxiliar no estabelecimento de estrat?gias de controle integrado. O estudo foi elaborado em tr?s partes: a primeira relata o estudo da din?mica migrat?ria e a sobreviv?ncia de larvas infectantes de ciatostom?neos em pastagem coast cross durante 12 meses. Para este estudo foram coletados amostras de fezes e gram?nea com intervalos regulares de sete dias em tr?s hor?rios diferentes (8, 13 e 17 horas). As amostras foram pesadas e processadas segundo a t?cnica de Baermann. A sobreviv?ncia das L3 foi de at? 15 semanas nas fezes e 12 semanas na gram?nea no per?odo seco e de nove e oito semanas respectivamente para o per?odo chuvoso. No per?odo chuvoso, maior n?mero de L3 foi recuperado nas fezes e no per?odo seco na gram?nea. N?o foi observada diferen?a significativa entre os hor?rios de coleta pela an?lise n?o param?trica de Kruskal-Wallis. Na segunda parte experimental foi estudada a ecologia das larvas infectantes de ciatostom?neos por 24 meses. Durante este per?odo, foram realizados coletas semanais de fezes e gram?nea (?pice e base). O processamento das amostras seguiu o mesmo protocolo realizado na primeira parte do experimento. Nas fezes as L3 sobreviveram por at? 15 semanas, ocorrendo uma maior recupera??o das larvas durante o per?odo chuvoso (46.228 kg-1.ms). Na gram?nea, a sobreviv?ncia foi de at? 12 semanas. A recupera??o das L3 foi mais intensa durante o per?odo seco na base (1.868 kg-1.ms) e no ?pice (809 kg-1.ms) da gram?nea. A migra??o das L3 das fezes para a gram?nea variou durante todo o per?odo. A ?ltima parte do estudo observou a migra??o de larvas infectantes de ciatostom?neos em pastagem coast cross irrigada e n?o irrigada durante as quatro esta??es do ano. Massas fecais, de eq?inos naturalmente infectados foram depositadas nos canteiros de coast cross no in?cio de cada esta??o.A amostragem de fezes e gram?nea foi realizada quinzenalmente em dois hor?rios distintos (8 e 17 horas) at? o final de cada esta??o, no per?odo de setembro/2007 a setembro/2008. O processamento das amostras foi o mesmo descrito na primeira parte experimental. O teste n?o param?trico de Kruskal Wallis evidenciou uma diferen?a significativa na recupera??o de larvas infectantes entre as esta??es do ano. N?o foi observada uma varia??o significativa na recupera??o de L3 nos diferentes hor?rios de coleta. Os resultados sugerem que em condi??es tropicais de Baixada Fluminense, RJ os animais est?o em permanente risco de infec??o.

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This thesis explores the possibilities of adaptively reusing an existing site to provide new services and work spaces for the local artistic community within a once heavily used Brit- ish naval ship building and repair station, but now a major centre of tourist activity on the island of Bermuda. This thesis examines how a courtyard and two large stone storehous- es can be refurbished and made useful again rather than torn down. There exists a strong national bias to maintain and preserve the heritage of the place. By understanding both the site’s inherent value, varying levels of design can be proposed that not only transform the site but also bring forward a new sense of place. The adaptive reuse design and the program chosen is a synthetic response to the inherent cultural and historic values of the place, providing spaces that meet needs of the present artist and artisan communities of the Dockyard.

O objetivo do estudo foi avaliar produção de forragem, valor nutritivo, frações nitrogenadas e as características morfogénicas da pastagem irrigada de Cynodon spp. e adubado com nitrogênio com dose parcelada ou singular. O experimento foi conduzido na Unidade de Ensino e Pesquisa de Bovinocultura de corte da Universidade Tecnológica Federal do Paraná – Câmpus Dois Vizinhos, Sudoeste do Paraná, entre 09 de novembro de 2015 a 31 de março de 2016. A área experimental foi de 1,5 ha com pastagem de Estrela Africana (Cynodon spp.) irrigada, subdividida em 18 piquetes de áreas semelhantes, com média de 400 m2. O delineamento experimental foi inteiramente casualizado para as avaliações de produção, valor nutritivo, fracionamento protéico e as características morfogênicas da pastagem, com três tratamentos e seis repetições. Os tratamentos avaliados foram: 1A: Uma aplicação, 2A: Duas aplicações e 4A: quatro aplicações de N, com intervalos de dois pós-pastejos, totalizando a fração estabelecida de 200 kg de N ha-1. As avaliações da forragem foram determinadas diretamente através de três cortes nas condições de pré e pós-pastejo a cinco centímetros do solo, ajustadas para cada mês do ano. Para a análise da composição química, as amostras foram obtidas pela técnica de simulação de pastejo. As características morfogênicas foram obtidas pela técnica de perfilhos marcados durante o período de descanso. A taxa de acúmulo, massa de forragem pré pastejo, massa foliar, massa de colmo e material morto, apresentaram interação tratamento x mês (P<0,05). No entanto, não foram observadas diferenças significativas (P>0,05) no valor nutritivo e no fracionamento de nitrogênio total entre os tratamentos. As características morfogênicas apresentaram diferença significativa (P<0,05) para a aplicação singular e parcelada em até duas vezes. Pastagens de Cynodon spp. podem ser adubadas com 200 kg de nitrogênio por hectare em uma única dose sem interferência no valor nutritivo e sem alterações nas frações proteicas e resultados superiores nas características morfogênicas. / The objective of the study was to evaluate forage yield, nutritive value, nitrogen fractions and morphogenic characteristics of irrigated nitrogen fertilized on pasture of Cynodon spp. with split or single dose. The experiment was conducted at the Teaching and Research Unit of beef cattle breading of the Federal Technological University of Paraná, Campus Dois Vizinhos, South-West of Paraná. The experimental area was 1.5 ha with pasture of Cynodon ssp. irrigated, subdivided in 18 paddocks of similar areas, with an average of 400 m2. Experimental design was of completely randomized for the evaluation of production, nutritional value, protein fractionation and for the morphogenic characteristics, with three treatments and six repetitions. Treatments evaluated were: 1A: One application, 2A: Two applications and 4A: four applications of N, with intervals of two post-grazing, totalizing the established fraction. Forage evaluations were determined directly by three cuts in pre-and post-grazing to five cm of the soil, adjusted for each month of the year. For the analysis of chemical composition, samples were obtained by the grazing hand-plucked method. The morphogenic characteristics were obtained by the marked tills technique during the rest period. Data of accumulation rate, pregrazing forage mass, leaf mass, stem mass and dead material presented treatment x month interaction (P<0.05). However, no significant differences were observed (P> 0.05) in the nutritional value and total nitrogen fractionation between treatments. The morphogenic characteristics showed a significant difference (P <0.05) for the single and split application in two times. the pasture of Cynodon can be fertilized with 200 kg of nitrogen per hectare in single dose without interference on nutritional value and without alterations in the protein fractions and superior results in the morphogenic characteristics.

Submitted by TATIANE BORTOLETTO GOMES DA SILVA null (tatibortoletto@live.com) on 2016-04-20T11:15:44Z No. of bitstreams: 1 Dissertação_Tatiane_final.pdf: 2327927 bytes, checksum: 4763720bd11ec4d660134d198140b887 (MD5) / Approved for entry into archive by Felipe Augusto Arakaki (arakaki@reitoria.unesp.br) on 2016-04-26T13:36:02Z (GMT) No. of bitstreams: 1 silva_tbg_me_bot.pdf: 2327927 bytes, checksum: 4763720bd11ec4d660134d198140b887 (MD5) / Made available in DSpace on 2016-04-26T13:36:02Z (GMT). No. of bitstreams: 1 silva_tbg_me_bot.pdf: 2327927 bytes, checksum: 4763720bd11ec4d660134d198140b887 (MD5) Previous issue date: 2016-02-18 / Coordenação de Aperfeiçoamento de Pessoal de Nível Superior (CAPES) / Um gramado esportivo deve apresentar boa condição de jogo além de bom aspecto visual. O nutriente requerido em maior quantidade em gramados é o nitrogênio, portanto deve-se ter o conhecimento do manejo criterioso de sua aplicação, com a quantidade adequada e os melhores momentos para a adubação. Outro nutriente importante no manejo de gramados é o potássio que confere resistência ao estresse hídrico. O manejo adequado da irrigação mantém a umidade do solo, evitando que o gramado sofra com a deficiência hídrica e perca qualidade. Objetivou-se com esse trabalho obter recomendações técnicas para os manejos nutricional e hídrico da grama bermuda Tifton 419 (C. dactylon x C. transvaalensis) utilizada nos gramados esportivos brasileiros, de forma a melhorar sua qualidade. O trabalho foi realizado no Departamento de Solos e Recursos Ambientais da Faculdade de Ciências Agronômicas de Botucatu – Unesp (Universidade Estadual Paulista “Júlio de Mesquita Filho”). O gramado foi estudado nos períodos do outono e do inverno, com início em abril de 2015 e finalização em setembro de 2015. Estudou-se as seguintes características: concentração dos nutrientes no solo, massa de matéria seca das aparas, concentração de nutrientes na lâmina foliar das aparas, quantidade de nutrientes nas aparas, intensidade de cor verde, altura do gramado, tração do gramado e taxa de cobertura verde do gramado. O delineamento experimental adotado foi em blocos casualizados composto por quatro repetições em esquema fatorial triplo, com quatro doses de nitrogênio, duas doses de potássio e duas frequências de irrigação. As doses de nitrogênio e potássio variaram de acordo com a estação do ano, no outono aplicou-se 28,1 kg N ha-1; 84,4 kg N ha-1; 140,6 kg N ha-1; 196,8 kg N ha-1; 28,1 kg K2O ha-1; 84,4 kg K2O ha-1 e no inverno aplicou-se 16,9 kg N ha-1; 50,6 kg N ha-1; 84,4 kg N ha-1; 118,1 kg N ha-1; 16,9 kg K2O ha-1; 50,6 kg K2O ha-1 (parceladas em três vezes). As frequências de irrigação foram: diária e a cada dois dias. A dose de nitrogênio de 562,5 kg ha-1ano-1 estimulou suficientemente o crescimento da parte aérea, porém, em detrimento do desenvolvimento das raízes e estolões. A dose de potássio de 112,5 kg ha-1ano-1 foi suficiente para o gramado e para não exaurir a quantidade de potássio no solo. As duas frequências de irrigação foram satisfatórias para manter o gramado verde. / A sport turfgrass must provide good visual appearance as well as good playing conditions. Nitrogen is the nutrient required in largest amounts on turfgrass and the adequate nitrogen fertilization may provide a good quality of sports field. Other important nutrient is the potassium that confer resistance to stress. The irrigation management keeps soil moisture avoiding that the turfgrass suffer with water stress and quality lost. The objective of this work was to determine technical recommendations for nutritional and irrigation managements of bermudagrass Tifton 419 (C. dactylon x C. transvaalensis), used in Brazilian sports field in order to improve their quality. The research was conducted in Department of Soil and Environmental Resources of the Faculdade de Ciências Agronômicas de Botucatu – Unesp (Universidade Estadual Paulista “Júlio de Mesquita Filho”). The turfgrass was studied during autumn and winter, beginning in April 2015 and finishing in September 2015. The following characteristics were studied: concentration of nutrients in the clipping, dry mass of clipping, the amount of nutrients in the clipping, dry mass of root and stolon, the turfgrass green color intensity, height of the turfgrass, rotational resistance and green cover rate. The experiment was set in randomized blocks design, with four replications, involving four nitrogen rates, two potassium rates and two irrigation frequency. The rates of nitrogen and potassium varied according to the season, in the autumn were applied 28,1 kg N ha-1; 84,4 kg N ha-1; 140,6 kg N ha-1; 196,8 kg N ha-1; 28,1 kg K2O ha-1; 84,4 kg K2O ha-1 and in the winter were applied 16,9 kg N ha-1; 50,6 kg N ha-1; 84,4 kg N ha-1; 118,1 kg N ha-1; 16,9 kg K2O ha-1; 50,6 kg K2O ha-1 (parcel three times). The frequency of irrigation was daily or each two days. Nitrogen rate of 562,5 kg ha-1year-1 stimulated growth of shoots over the stolon and root. Potassium rates didn’t show significantly different for any treatment evaluated, therefore the rate of 112,5 kg ha-1year-1 was sufficient. Both irrigation frequencies were satisfactory to maintain the turfgrass green.