O número de projetos de restauração de ecossistemas florestais no Brasil aumentou nas últimas décadas e, consequentemente, aumentaram as exigências na avaliação e na busca por indicadores de sucesso. Apesar dos avanços na ecologia da restauração, existem lacunas no conhecimento em relação ao funcionamento e à autossustentabilidade dos ecossistemas restaurados. Esta pesquisa teve o objetivo de responder às seguintes questões: (1) É possível detectar padrões nos atributos de riqueza, estrutura e grupos funcionais nas matas ciliares nativas da Floresta Estacional Semidecidual (FES), que podem ser utilizados como metas da restauração florestal nesta região? (2) Quais as variáveis de biodiversidade, estrutura florestal e grupos funcionais, nas áreas restauradas, que seguem trajetórias previsíveis com o tempo? (3) Quanto tempo é necessário para que estas variáveis atinjam os valores de referência das matas ciliares nativas? (4) Quais são os fatores bióticos, abióticos, de técnica de plantio e de manutenção pós-plantio que influenciam nas trajetórias das matas ciliares restauradas? O estudo foi desenvolvido em região de FES, onde amostramos quatro matas nativas (referências) e 26 plantios de restauração, com idade entre quatro e 53 anos, que utilizamos para modelar as trajetórias em cronoseqüência. Em cada área, dez parcelas de 100 \'M POT.2\' foram aleatoriamente distribuídas, dentro de uma faixa de até 50 m de largura a partir da margem. Identificamos e contabilizamos os indivíduos de espécies arbóreas e arbustivas, plantadas ou regenerantes, a partir de 50 cm de altura e os agrupamos em três classes de tamanho segundo o diâmetro à altura do peito (DAP): DAP < 1 cm, 1 cm \'< ou =\' DAP < 5 cm e DAP \'> ou =\' 5 cm. Na classe de maior tamanho registramos o DAP e estimamos a altura de cada indivíduo. Classificamos as espécies de acordo com a sua síndrome de dispersão, ritmo de crescimento, tolerância à sombra, capacidade de fixar N, grau de ameaça e raridade. Para cada parcela, medimos a abertura do dossel, contabilizamos o número de lianas, pteridófitas e árvores com epífitas e coletamos uma amostra de solo, para formar uma amostra composta para cada local de estudo. Calculamos a biomassa acima do solo para árvores com DAP \'> ou =\' 5 cm, a riqueza total estimada por Jackknife e a riqueza rarefeita para 100 indivíduos. Por meio de entrevistas, observações em campo e análises da paisagem, obtivemos dados representativos de fatores abióticos, bióticos e de manejo que poderiam influenciar as trajetórias das comunidades arbóreas restauradas. Modelamos a trajetória de cada variável relativa à comunidade arbustivo-arbórea em função do tempo e estimamos o tempo que será necessário para igualar os ecossistemas de referência para cada variável. Entre as variáveis analisadas, selecionamos, como indicadores para monitoramento da evolução e sustentabilidade do ecossistema restaurado, as que fossem mais previsíveis (melhor qualidade dos modelos) e que representassem processos ecológicos mais relevantes. Os atributos que não variaram entre florestas nativas e que puderam ser utilizados como referência foram: riqueza observada, riqueza estimada para 100 indivíduos com DAP \'> ou =\' 5 cm, riqueza estimada por Jackknife para indivíduos com DAP \'> ou =\' 1 cm, densidade de indivíduos com DAP \'> ou =\' 1 cm, área basal, biomassa, cobertura de copas, proporção de indivíduos tolerantes à sombra e proporções de espécies zoocóricas, de crescimento lento, tolerantes à sombra, fixadoras de nitrogênio e de distribuição rara. No geral, as trajetórias foram mais bem ajustadas aos modelos logarítmicos, mas a riqueza de regenerantes de maior tamanho (DAP \'> ou =\' 5) ajustou-se melhor ao modelo linear. A riqueza nesta classe de tamanho não atingiu o nível de regenerantes dos ecossistemas de referência no período estudado. As trajetórias seguiram padrões semelhantes, independentes das técnicas de plantio ou do número de espécies plantadas. Variáveis de estrutura florestal foram homogêneas entre as matas nativas. Nos plantios, são facilmente medidas e evoluem rapidamente. Assim, metas da restauração podem ser estabelecidas com base nos parâmetros estruturais das matas nativas e tais variáveis seriam bons indicadores inclusive em plantios de restauração mais jovens. As variáveis que tendem a alcançar mais rapidamente os valores de referência são: área basal (12 anos), biomassa (13 anos), altura média das maiores árvores (26 anos), cobertura de gramíneas (33 anos), cobertura de copas (35 anos), riqueza de regenerantes com DAP \'> ou =\' 1 cm (52 anos), densidade de regenerantes com DAP \'> ou =\' 1 cm (52 anos) e riqueza total (53 anos). A área basal e a biomassa ultrapassaram em muito os valores de referência, o que pode indicar um filtro restritivo para a regeneração natural, caso a densidade dos indivíduos na classe de maior tamanho (geralmente plantados) não diminua naturalmente com o tempo. Para alguns grupos de espécies (zoocóricas, fixadoras de N, espécies raras e ameaçadas), as proporções em termos de riqueza e de densidade não apresentaram trajetórias previsíveis, mas algumas matas ciliares restauradas atingiram e ultrapassam os valores de referência. Excluímos o fator idade para identificar os fatores que influenciaram as trajetórias das variáveis selecionadas como indicadores, calculando um índice de sucesso (proporção entre o dado observado em cada local e o estimado para a mesma variável com base no modelo). Entre as seis variáveis selecionadas como indicadores, uma foi influenciada somente pela distância de fragmento-fonte (riqueza de regenerantes com DAP \'> ou =\' 5) e outra apena pela proporção de partículas finas no solo (área basal). Apesar da proporção do terreno ocupada por gramíneas não influenciar nas trajetórias, o controle da mato-competição com herbicida resultou em maiores valores de riqueza de plantas em regeneração. Independentemente das técnicas de plantio e dos tipos de manejo dos projetos de restauração, a estrutura florestal e os processos funcionais dos ecossistemas restaurados tendem a se tornar mais semelhantes aos ecossistemas de referência com o tempo, desde que haja fontes de propágulos e disponibilidade de água e nutrientes no solo. Os resultados obtidos apontam para uma influência muito pequena ou nula das técnicas de plantio e manejo, se comparados com a influência dos fatores ambientais e da paisagem sobre as trajetórias das matas ciliares em restauração. / A remarkable increase in the number of forest restoration projects has been recorded in Brazil in the last decade. As a consequence of this increase, the demand for monitoring and indicators of restoration success has also increased. Despite the advances in restoration ecology, there are still gaps in knowledge about the functioning and self-sustainability of restored ecosystems. In order to fill some of these gaps, in this study we aimed at to answer the following questions: (1) Are there patterns in the attributes of richness, structure, and functional groups on the native riparian Seasonally Semideciduous Forest (SSF), which may be used as goals to forest restoration in this region? (2) What are the variables representing biodiversity, forest structure and functional groups in the restored areas, which follow predictable paths over time? (3) How long it takes for these variables to achieve the reference values of native riparian forests? (4) Among the biotic, abiotic and technical factors analyzed, which can be considered as drivers of the successional trajectories of the restored forests? We assessed four native forests (as references) and 26 restored forests in the SSF region (a sub-type of the Atlantic Forest) in a chronosequence from four to 53 years since planting. At each site, the sample area comprised ten plots of 100 \'M POT.2\' randomly distributed within a range of 50 m away from the margin. We identified and counted all individuals of tree and shrub species from 50 cm in height, planted or regenerating, categorized in three size classes according to diameter at breast height (DBH): DBH < 1 cm, 1 cm \'< ou =\' DBH < 5 cm DBH \'> ou =\' 5 cm. We measured DBH and estimated the height of each individual from the upper class. We categorized the species according to their dispersion syndrome, growth rate, shade tolerance, Nitrogen-fixing ability, degree of threaten, and rarity. For each plot, we measured the canopy openness, and recorded the number of lianas, pteridophytes and number of trees with epiphytes. We also collected composite soil samples for chemical and physical analyses, from each study site. We estimated the aboveground biomass for trees with DBH \'> ou =\' 5 cm, total richness and richness rarefied to 100 individuals. By interviews, field observations, and landscape studies, we obtained information on other ecological factors and management practices that could affect the paths of the restored plant communities. We modeled the trajectory of each variable of the plant community over time, and estimated the period of time required for the restored forests to reach the reference ecosystems. Amongst the analyzed variables, we selected as indicators for monitoring the evolution and sustainability of the restored ecosystem those that were more predictable (best quality models) and that represent the most relevant ecological processes. The attributes that did not change among the native forests and could be used as references were: observed richness, estimated richness for 100 individuals with DBH \'> ou =\' 5 cm, total richness estimated by Jackknife DBH \'> ou =\' 1 cm, density DBH \'> ou =\' 1 cm, basal area, biomass, canopy cover, proportion of shade-tolerant individuals, and proportion of zoochoric species, slow growing, shade tolerant, nitrogen fixers, and rare distribution. Overall, the trajectories were best fitted to the logarithmic models, but richness (DBH \'> ou =\' 5 cm) was better adjusted to the linear model. In the upper size class, richness did not reach the \"species pool\" of the reference ecosystems in the 53 years period analyzed. The trajectories followed similar patterns, regardless of the planting techniques or the number of planted species. Variables representing forest structure were similar among the native forests and quickly recovered in comparison to those related to biodiversity. Thus, the restoration goals can be established based on native forests parameters and such variables would be good indicators even in young restoration plantings. The variables reaching more quickly the reference values were: basal area (12 years), biomass (13 years), average height of the largest trees (26 years), grass cover (33 years), canopy cover (35 years), richness of regenerants with DBH \'> ou =\' 1 cm (52 years), density of regenerants with DBH 1 cm (52 years), and total richness (53 years). The basal area and biomass greatly exceeded the reference values, which may indicate a restrictive filter for the forest dynamics if the density of individuals in the upper class (most planted) does not decrease naturally over time. For some functional groups (zoochoric, N-fixing, rare, and endangered species), the proportions of species and relative densities did not follow predictable trajectories, but some of the restored riparian areas reached and exceeded the reference values. In order to identify the factors driving the paths of the variables selected as indicators, we excluded the age factor, calculating an index of success (the ratio between observed and estimated values for the variable, the first directly measured for each site and the last obtained by the linear models). Among the six variables selected as indicators, some were influenced only by the distance of the source fragment (seedling richness of DBH \'> ou =\' 5 cm) and others only by the proportion of fine particles in the soil (basal area). While the ground cover by grasses does not influence the trajectories, weed control with herbicides resulted in higher plant richness in regeneration. Regardless of planting techniques and management practices, the forest structure and functional processes of restored ecosystems tend to become more similar to reference ecosystems over time, as long as there are propagule sources in the vicinity and availability of soil water and nutrients. Our findings pointed to a weak, if any, effect from the planting techniques or management and a high influence of environmental and landscape factors on the trajectories of a riparian forest restoration.

Chan Kit-ying. / Thesis (M.Phil.)--Chinese University of Hong Kong, 2001. / Includes bibliographical references (leaves 125-133). / Abstracts in English and Chinese. / Abstract --- p.i / Acknowledgements --- p.v / Table of Contents --- p.vi / List of Tables --- p.x / List of Figures --- p.xii / List of Plates --- p.xiii / List of Appendixes --- p.xiv / Abbreviations --- p.xv / Chapter CHAPTER 1 --- INTRODUCTION / Chapter 1.1 --- Introduction --- p.1 / Chapter 1.2 --- Organization of Study --- p.5 / Chapter 1.2.1 --- Stage One -Literature Review --- p.5 / Chapter 1.2.2 --- Stage Two - Review of EI A Reports and Case Studies of Ecological Mitigation/Compensation Measures --- p.5 / Chapter 1.2.3 --- Stage Three - Evaluation and Recommendations --- p.6 / Chapter 1.3 --- Chapter Outlines --- p.6 / Chapter CHAPTER 2 --- BACKGROUND OF STUDY / Chapter 2.1 --- Introduction --- p.9 / Chapter 2.2 --- Definitions --- p.9 / Chapter 2.3 --- The Ecological Impact Assessment Process --- p.10 / Chapter 2.3.1 --- Baseline Study and Scoping --- p.10 / Chapter 2.3.2 --- Impact Prediction and Evaluation --- p.11 / Chapter 2.3.3 --- Mitigation --- p.11 / Chapter 2.3.4 --- Environmental Monitoring and Auditing --- p.12 / Chapter 2.4 --- Ecological Impact Assessment in Hong Kong --- p.12 / Chapter 2.5 --- Problems of Ecological Impact Assessment --- p.16 / Chapter 2.6 --- Compensatory Mitigation --- p.19 / Chapter CHAPTER 3 --- METHDOLOGY AND STUDY AREA / Chapter 3.1 --- Introduction --- p.21 / Chapter 3.2 --- Critical Review of EIA Reports --- p.23 / Chapter 3.2.1 --- Methodology --- p.23 / Chapter 3.3 --- Case Studies of Compensatory Wetlands --- p.29 / Chapter 3.3.1 --- Selection of Ecological Compensation Projects --- p.29 / Chapter 3.3.2 --- Study Sites --- p.30 / Chapter 3.3.2.1 --- Climate --- p.30 / Chapter 3.3.2.2 --- Compensatory Fishponds at Au Tau Interchange --- p.32 / Chapter 3.3.2.3 --- Compensatory Mangrove at Main Drainage Channel --- p.34 / Chapter 3.3.2.4 --- Compensatory Mangrove at Kau Sai Chau --- p.36 / Chapter 3.3.3 --- Methods to Assess Ecological Functionality --- p.37 / Chapter 3.3.3.1 --- Bird Use of the Au Tau Compensatory Ponds --- p.39 / Chapter 3.3.3.2 --- Habitat and Vegetation Mapping --- p.41 / Chapter 3.3.3.3 --- Statistical Analysis --- p.43 / Chapter 3.3.4 --- Vegetation Performance and Soil Properties of Compensatory Mangroves --- p.45 / Chapter 3.3.4.1 --- Vegetation Sampling --- p.45 / Chapter 3.3.4.2 --- Statistical Analysis --- p.47 / Chapter 3.3.4.3 --- Soil Properties --- p.47 / Chapter 3.3.4.4 --- Statistical Analysis --- p.52 / Chapter CHAPTER 4 --- CRITICAL REVIEW OF ECOLOGICAL STATEMENTS / Chapter 4.1 --- Introduction --- p.53 / Chapter 4.2 --- Nature of the Projects Reviewed --- p.54 / Chapter 4.3 --- Quality of the Ecological Assessment --- p.56 / Chapter 4.3.1 --- Ecological Baseline Study --- p.56 / Chapter 4.3.2 --- Impact Predictions --- p.59 / Chapter 4.3.3 --- Mitigation --- p.63 / Chapter 4.3.4 --- Environmental Monitoring and Auditing --- p.67 / Chapter 4.3.5 --- Differences in Ecological Statements before and after EIAO --- p.67 / Chapter 4.4 --- Discussion --- p.69 / Chapter 4.4.1 --- Ecological Baseline Study and Scoping --- p.69 / Chapter 4.4.2 --- Impact Predictions --- p.71 / Chapter 4.4.3 --- Environmental Mitigation and Monitoring --- p.72 / Chapter CHAPTER 5 --- PROMISES AND REALITIES OF ECOLOGIAL COMPENSATORY SCHEMES / Chapter 5.1 --- Introduction --- p.76 / Chapter 5.2 --- Mangrove Communities at KSC and MDC --- p.77 / Chapter 5.2.1 --- Vegetation Performance --- p.77 / Chapter 5.2.2 --- Soil Properties --- p.81 / Chapter 5.2.3 --- Discussion of the Overall Performance --- p.85 / Chapter 5.3 --- Compensatory Fishponds --- p.91 / Chapter 5.3.1 --- Bird Use at Au Tau Compensatory Fishponds --- p.91 / Chapter 5.3.2 --- Total Bird Counts --- p.93 / Chapter 5.3.3 --- Species Composition --- p.94 / Chapter 5.3.4 --- Avian Density --- p.96 / Chapter 5.3.5 --- Species Diversity --- p.101 / Chapter 5.3.6 --- Discussion of Au Tau Compensatory Ponds --- p.102 / Chapter 5.4 --- Discussion --- p.107 / Chapter CHAPTER 6 --- CONCLUSION / Chapter 6.1 --- Major Findings --- p.111 / Chapter 6.2 --- Discussion of Findings --- p.114 / Chapter 6.3 --- Recommendations --- p.119 / REFERENCES --- p.125 / APPENDIXES --- p.134

Tentant d’accommoder protection de l’environnement et artificialisation de la nature, les mesures de compensation consistent techniquement à rééquilibrer un dommage écologique par un gain écologique. Imposées juridiquement dans les années 1970, la place de ces dispositifs interroge toujours. Mesures de police administrative par nature, elles s’assimilent à un mode de réparation en dehors de tout régime de responsabilité par leur finalité : remédier en nature aux atteintes causées aux milieux naturels. Échappant à toute définition en dépit de la variété des régimes juridiques actuels, les compensations à visée écologique demeurent inabouties sur le plan juridique. De cette hétérogénéité des régimes juridiques, peut-il émerger un concept unique propre à garantir sa nature curative ? Leur vocation commune est desservie par les indéterminations juridiques dont souffrent ces compensations et qui résident tant dans la pluralité juridique des compensations que dans les défaillances pratiques lors de leur mise en œuvre. Se créé alors un hiatus entre les décisions prises fondées sur une compensation idéalisée, à savoir un instrument de lutte contre la perte de biodiversité, et la réalité des mesures le plus souvent sans équivalence écologique, précaires voire inexistantes. C’est pourquoi il convient de mettre fin à cet amalgame grâce à une caractérisation juridique de ce que devrait être la compensation écologique. Cette tentative de définition s’accompagne d’une exploration des perspectives d’avenir de la compensation écologique notamment sous l’angle d’une mutualisation des sites de compensation. / The aim of ecological offsets is to combine environmental protection with the social and economic opportunities of implementing new projects on natural spaces. Technically, these measures involve restoring balance between ecological damages and ecological benefits to be provided for by the ecological offset. Ecological offsets measures became mandatory in the seventies, yet their adequacy is still questioned today. They are administrative policy measures, distinct from liability. Although several different ecological offsets exist, no law explicitly defines them. It appears then very important to know whether it’s possible to draw one global legal definition of ecological offset, in order to assure the achievement of the ecological goals of all this measures: providing effective reparation of the damages caused to the ecosystems. All the more as the lack of legal offset criteria is adding to already existing practical difficulties which may in term bring about the downfall of ecological offset.Actually, though it is widely presented as a legal instrument to reverse the loss of biodiversity; reality shows that this purpose may not be attained, especially because of a lack of unanimous ecological measurement model. That’s why ecological offset deeply needs a legal characterization of what it should be. After this attempt at a definition, the thesis proposes to explore the future of the ecological offset, including the opportunities offered by shared sites of natural remediation.

Yu Chi Cheung. / Thesis submitted in: August 2005. / Thesis (M.Phil.)--Chinese University of Hong Kong, 2006. / Includes bibliographical references (leaves 156-169). / Abstracts in English and Chinese. / Abstract / Declaration --- p.i / Acknowledgement --- p.ii / Contents --- p.iv / List of Figures --- p.vi / List of Tables --- p.vii / List of Plates --- p.x / Chapter Chapter 1 --- Introduction --- p.1 / Chapter 1.1 --- About Hong Kong --- p.2 / Chapter 1.1.1 --- Geography --- p.2 / Chapter 1.1.2 --- Climate --- p.4 / Chapter 1.1.3 --- Vegetation --- p.7 / Chapter 1.1.4 --- Wildlife conservation in Hong Kong --- p.10 / Chapter 1.2 --- Land Restoration --- p.12 / Chapter 1.2.1 --- General processes of restoration --- p.13 / Chapter 1.2.2 --- Plantation in Hong Kong quarries --- p.15 / Chapter 1.2.3 --- Ecological succession in Hong Kong --- p.16 / Chapter 1.2.4 --- Problems in quarry restoration --- p.17 / Chapter 1.3 --- Objectives --- p.18 / Chapter 1.3.1 --- Study sites --- p.18 / Chapter 1.3.2 --- Soil-plant ecosystem --- p.27 / Chapter 1.3.3 --- Insect study --- p.28 / Chapter 1.3.4 --- Lepidopteran as a study group --- p.29 / Chapter 1.3.5 --- Odonata as a study group --- p.31 / Chapter 1.4 --- Project Significant --- p.32 / Chapter Chapter 2 --- Soil Status in Restored Quarries in Hong Kong --- p.35 / Chapter 2.1 --- Introduction --- p.35 / Chapter 2.2 --- Materials and Methods --- p.37 / Chapter 2.2.1 --- Soil sampling --- p.37 / Chapter 2.2.2 --- Soil analysis --- p.37 / Chapter 2.3 --- Statistical Analysis --- p.39 / Chapter 2.4 --- Results and Discussion --- p.39 / Chapter 2.4.1 --- General properties of soil in the restored quarries --- p.39 / Chapter 2.4.2 --- Soil description on different phases among the sites --- p.43 / Chapter 2.4.3 --- Soil comparison on different phases with the same age --- p.45 / Chapter 2.5 --- Conclusion --- p.47 / Chapter Chapter 3 --- Vegetation Study of Restored Quarries --- p.49 / Chapter 3.1 --- Introduction --- p.49 / Chapter 3.2 --- Materials and Methods --- p.52 / Chapter 3.2.1 --- Vegetation survey --- p.52 / Chapter 3.2.2 --- Quadrat analysis --- p.53 / Chapter 3.2.3 --- Vegetation description --- p.53 / Chapter 3.2.3.1 --- Similarity index --- p.53 / Chapter 3.2.3.2 --- Species richness index --- p.53 / Chapter 3.2.3.3 --- Diversity index --- p.54 / Chapter 3.2.3.4 --- Evenness index --- p.54 / Chapter 3.2.3.5 --- Effective number of species --- p.54 / Chapter 3.3 --- Results and Discussion --- p.55 / Chapter 3.3.1 --- Vegetation coverage on restored quarries --- p.55 / Chapter 3.3.2 --- Vegetation structure and diversity on restored quarries --- p.58 / Chapter 3.3.3 --- Ecological indices on various sites --- p.78 / Chapter 3.3.4 --- Successful plants at various phases among the sites --- p.80 / Chapter 3.3.5 --- "Tree vs shrubs, native vs exotic" --- p.85 / Chapter 3.4 --- Conclusion --- p.87 / Chapter Chapter 4 --- Butterfly Communities on Restored Quarries --- p.89 / Chapter 4.1 --- Introduction --- p.89 / Chapter 4.2 --- Materials and Methods --- p.90 / Chapter 4.2.1 --- Pollard-walk method --- p.90 / Chapter 4.2.2 --- Statistical analysis --- p.95 / Chapter 4.3 --- Results and Discussion --- p.95 / Chapter 4.3.1 --- General description of the butterfly communities --- p.95 / Chapter 4.3.2 --- Uncommon species found on the quarries --- p.99 / Chapter 4.3.3 --- Butterfly species found on various phases of the sites --- p.102 / Chapter 4.3.4 --- Ecological indices on various sites --- p.114 / Chapter 4.4 --- Conclusions --- p.117 / Chapter Chapter 5 --- Moth Communities on Restored Quarries --- p.118 / Chapter 5.1 --- Introduction --- p.118 / Chapter 5 2 --- Materials and Methods --- p.119 / Chapter 5.2.1 --- Light trapping method --- p.119 / Chapter 5.3 --- Results and Discussion --- p.120 / Chapter 5.3.1 --- General description of moth community --- p.120 / Chapter 5.3.2 --- Ecological indices of moth on various sites --- p.123 / Chapter 5.3.3 --- Moth species found on various phases of the sites --- p.129 / Chapter 5.3.4 --- Ecological importance of Lepidopterans --- p.142 / Chapter 4.4 --- Conclusion --- p.143 / Chapter Chapter 6 --- General Conclusion --- p.145 / Chapter 6.1 --- Soil Development and Species Diversity --- p.145 / Chapter 6.2 --- Current Status of Restored Quarries in Hong Kong --- p.148 / Chapter 6.3 --- Conservation Value of Restored Quarries --- p.150 / Chapter 6.4 --- Limitation of the study --- p.151 / Chapter 6.4.1 --- Light trap --- p.151 / Chapter 6.4.2 --- Correlation vs causation --- p.153 / Chapter 6.5 --- Area for Further Investigation --- p.154 / Chapter 6.4.1 --- Seed bank analysis --- p.154 / Chapter 6.4.2 --- Other inventories --- p.154 / References --- p.156 / Appendix Odonate Communities on Restored Quarries --- p.170 / Introduction --- p.170 / Materials and Methods --- p.172 / Visual encounter survey --- p.172 / Statistical analysis --- p.172 / Results and Discussion --- p.173 / General description of odonate community --- p.173 / Ecological indices of odonate on various sites --- p.175 / Odonates species on various phases of the sites --- p.179 / Conclusion --- p.183 / References --- p.184

香港的山火主要是由於氣候及人類活動所引發，嚴重威脅著一些陸地上生物多樣性豐富的生境（如灌木林和林地）。在華南地區，有關火燒地的動物群落恢復生態學硏究的資料非常少，所以本硏究旨在調查山火後動物群落的復原，以及比較天然復原的林區及人工植林的生境恢復之差異。此外，枯枝落葉、物理因素及山火後的微生物對動物群落的影響亦會在此硏究中詳细分析。 / 在亞熱帶地區，地棲無脊椎動物群落的復原速度相對為慢，例如螞蟻群落需要12年的時間才能復原，但人工種植於火燒地能成功地加快其復原速度。 / 無脊椎動物群落與植被結構、山火之後的時間及生境發展都有一定的關係。山火發生兩年後火燒地的鳥類和無脊椎動物的數量、種或科的豐富度、單一性、多樣性及所有無脊椎動物的生物量都比參考樣地低，這意味著山火對動物群落有著長遠的影響。Pheidole spp. 及Tapinoma sp. 1 屬的螞蟻、隠翅甲科及小蠹科的甲蟲、管巢蛛科及狼蛛科的蜘蛛，牠們的數量，以及數量與生物量之比 (ABC plot) 都能用作反映火燒地的生態復原及演替進度的指標。 / 人工種植能夠使生態系統得到長遠的持續建立，對於動物群落的恢復非常重要。是次研究結果顯示人工種植能促進本地無脊椎動物的建群，其數量和群落亦會隨時間增加而增加。這很可能是由於山火後人工種植能為無脊椎動物創造較好的生存條件。其中，相對於原生樹種，外來樹種更有利於無脊椎動物的建群。在外來品種的人工種植區，微生物的數量較低，枯枝落葉的被分解速度較慢，加上生長速度快的外來品種能製造大量的枯枝落葉，這些都顯著增加了枯葉層的深度。較深的枯葉層為無脊椎動物提供了適宜的微生境，有利於其建群。 / 總的來說，在火燒地進行人工植樹能加快動物在火燒地的復原速度，這種方法是有效且成功的。人工種植時採用適當的品種能夠促進及預測早期的植被演替。根據此次硏究結果，我們建議在火燒地上種植生長快速的外來樹種，以加快無脊椎動物的建群。植被蓋度對動物的建群很重要，但植物和結構的多樣性及枯枝落葉層對無脊椎動物的建群更為重要。 / Hill fire in Hong Kong is mainly caused by a combination of weather and human activities. Fire is a major threat to terrestrial animal communities especially in shrublands and woodlands which have a rich faunal diversity. Since research done on hill fire ecology in southern China, especially on faunal colonization after fire, is very scarce, this research attempted to investigate the recovery of fauna after fire disturbance, and the difference in recovery between natural regeneration and artificial planting. Besides, the effects of litter and physical parameters on fauna community as well as the effect of fire on soil microbial community structure were studied. / The recolonization of ground-dwelling invertebrates was relatively slow in the study area, while proactive planting has been successful because they have considerably accelerated the return of fauna at the fire-affected sites. Ground-dwelling invertebrate communities appeared to be less resilient to fire in subtropical environment; the ant composition in the experimental plots needed 12 years to recover. / The composition of the ground-dwelling communities differed among study sites and was correlated with vegetation structure and time since last fire. They showed the trends in the development of invertebrate community composition in association with habitat development. Abundance, species/family richness, evenness, diversity of birds and ground-dwelling invertebrates, and biomass of total invertebrates were lower on the burned site than the reference site even 2 years after fire, implying that fire had longer-term impacts on the faunal communities. Ants such as Pheidole spp., Tapinoma sp. 1, beetles such as Staphylinidae, Scolytidae, and spiders such as Clubionidae, Lycosidae, as well as the abundance biomass comparison (ABC plot) can be chosen to reflect the situation or the recovery process and succession of the fire-affected sites. / The establishment of fauna in proactive planting is vital if ecosystem functions are to be reestablished and restorations to be sustained in the long term. In general the invertebrate data suggest that restoration plantings facilitated the reestablishment of indigenous invertebrate species and invertebrate community changed with time. Proactive plantings created better conditions for ground-dwelling invertebrates after fire, and exotic species with faster growth rate seem to be better than the natives. In exotic plantations, lower decomposition rate of litter provided by the lower microbial population together with higher productivity of exotic species of plants caused a higher litter depth, which provided more microhabitats for ground-dwelling and litter-dwelling invertebrates than the native plantations. / Correct species selection in proactive planting is essential to facilitate and determine the early stages of plant succession. The present study suggests that initial floristic composition is significant in proactive plantings and exotic species with fast growth rate is an effective planting species for invertebrate recolonization. Although plant cover is of importance to developing fauna, the provision of adequate floristic and structural diversity and the presence of logs and litter are important for the full range of native invertebrate recolonization. / Detailed summary in vernacular field only. / Detailed summary in vernacular field only. / Detailed summary in vernacular field only. / Detailed summary in vernacular field only. / Detailed summary in vernacular field only. / Cheung, Kwok Leung. / Thesis (Ph.D.)--Chinese University of Hong Kong, 2012. / Includes bibliographical references (leaves 192-219). / Electronic reproduction. Hong Kong : Chinese University of Hong Kong, [2012] System requirements: Adobe Acrobat Reader. Available via World Wide Web. / Abstract also in Chinese; some appendixes also in Chinese. / Abstract --- p.i / Acknowledgements --- p.vi / Table of contents --- p.vii / List of figures --- p.x / List of plates --- p.xvi / List of appendices --- p.xvii / Chapter Chapter 1 --- General Introduction --- p.1 / Chapter 1.1 --- Ecology of Fire --- p.1 / Chapter 1.2 --- Effects of Hill Fire on Soil --- p.3 / Chapter 1.3 --- Effects of Hill Fire on Microbial Communities --- p.7 / Chapter 1.4 --- Effects of Hill Fire on Vegetation --- p.10 / Chapter 1.5 --- Effects of Hill Fire on Fauna Communities --- p.14 / Chapter 1.6 --- The Use of Bioindicators on Restoration Ecology --- p.19 / Chapter 1.7 --- Hill Fire Situation and Research in Hong Kong --- p.23 / Chapter 1.8 --- Study Objectives --- p.28 / Chapter Chapter 2 --- Faunal Colonization after Fire Disturbance --- p.30 / Chapter 2.1 --- Introduction --- p.30 / Chapter 2.2 --- Materials and Methods --- p.32 / Chapter 2.2.1 --- Study sites --- p.32 / Chapter 2.2.2 --- Measurements of soil physicochemical parameters --- p.35 / Chapter 2.2.3 --- Determination of vegetation parameters --- p.36 / Chapter 2.2.4 --- Monitoring of vertebrate communities --- p.36 / Chapter 2.2.5 --- Sampling, sorting and identification of invertebrates --- p.37 / Chapter 2.2.6 --- Data analysis --- p.38 / Chapter 2.3 --- Results --- p.41 / Chapter 2.3.1 --- Soil physicochemical characteristics --- p.41 / Chapter 2.3.2 --- Vegetation parameters --- p.42 / Chapter 2.3.3 --- Vertebrate communities --- p.44 / Chapter 2.3.4 --- Invertebrate communities --- p.47 / Chapter 2.4 --- Discussion --- p.58 / Chapter 2.5 --- Conclusions --- p.66 / Chapter Chapter 3 --- Effect of Different Planting Approaches on Invertebrates --- p.68 / Chapter 3.1 --- Introduction --- p.68 / Chapter 3.2 --- Materials and Methods --- p.70 / Chapter 3.2.1 --- Study sites --- p.70 / Chapter 3.2.2 --- Proactive planting --- p.71 / Chapter 3.2.3 --- Measurement of soil, vegetation, and faunal parameters, and data analysis --- p.73 / Chapter 3.3 --- Results --- p.75 / Chapter 3.3.1 --- Soil physicochemical parameters --- p.75 / Chapter 3.3.2 --- Vegetation parameters --- p.77 / Chapter 3.3.3 --- Invertebrate communities --- p.78 / Chapter 3.4 --- Discussion --- p.92 / Chapter 3.5 --- Conclusions --- p.98 / Chapter Chapter 4 --- Long-term Changes of Invertebrate Community after Hill Fire by a Retrospective Approach --- p.100 / Chapter 4.1 --- Introduction --- p.100 / Chapter 4.2 --- Materials and Methods --- p.102 / Chapter 4.2.1 --- Study sites --- p.102 / Chapter 4.2.2 --- Measurement of soil physicochemical parameters --- p.102 / Chapter 4.2.3 --- Determination of vegetation parameters --- p.103 / Chapter 4.2.4 --- Collection, sorting and identification of invertebrates --- p.104 / Chapter 4.2.5 --- Data analysis --- p.104 / Chapter 4.3 --- Results --- p.105 / Chapter 4.3.1 --- Soil physicochemical characteristics --- p.105 / Chapter 4.3.2 --- Vegetation parameters --- p.106 / Chapter 4.3.3 --- Invertebrate communities --- p.110 / Chapter 4.4 --- Discussion --- p.123 / Chapter 4.5 --- Conclusions --- p.133 / Chapter Chapter 5 --- Relationship of Microbial Community with Recolonization of Invertebrates --- p.135 / Chapter 5.1 --- Introduction --- p.135 / Chapter 5.2 --- Materials and Methods --- p.139 / Chapter 5.2.1 --- Study sites --- p.139 / Chapter 5.2.2 --- Microbial biomass carbon (C[subscript mic]) and nitrogen (N[subscript mic]) --- p.139 / Chapter 5.2.3 --- Fatty acid methyl esters (FAME) extraction --- p.140 / Chapter 5.2.4 --- Data analysis --- p.141 / Chapter 5.3 --- Results --- p.142 / Chapter 5.3.1 --- Fumigation-extraction --- p.142 / Chapter 5.3.2 --- Fatty acid methyl esters --- p.144 / Chapter 5.3.3 --- Relationship of microbial communities with physicochemical, vegetation and invertebrate parameters --- p.145 / Chapter 5.4 --- Discussion --- p.152 / Chapter 5.5 --- Conclusions --- p.159 / Chapter Chapter 6 --- Effects of Critical Factors on Invertebrate Communities --- p.160 / Chapter 6.1 --- Introduction --- p.160 / Chapter 6.2 --- Materials and Methods --- p.162 / Chapter 6.2.1 --- Experimental sites --- p.162 / Chapter 6.2.2 --- Critical factors selection and simulation --- p.163 / Chapter 6.2.3 --- Measurement of microclimatic characteristics --- p.165 / Chapter 6.2.4 --- Collection, sorting and identification of invertebrates --- p.166 / Chapter 6.2.5 --- Data analysis --- p.166 / Chapter 6.3 --- Results --- p.167 / Chapter 6.3.1 --- Microclimatic characteristics --- p.167 / Chapter 6.3.2 --- Invertebrate communities --- p.168 / Chapter 6.4 --- Discussion --- p.173 / Chapter 6.5 --- Conclusions --- p.178 / Chapter Chapter 7 --- General Conclusions --- p.180 / Chapter 7.1 --- Overall Discussion --- p.180 / Chapter 7.2 --- Limitation of the Present Study and Future Research --- p.184 / Chapter 7.3 --- Contributions to Our Knowledge --- p.188 / Reference --- p.192 / Appendices --- p.220

O Urbanismo Ecológico surge como uma forma de reconciliar a paisagem com a ocupação urbana, pautado pelas potencialidades e limitações dos recursos naturais. As áreas verdes não exercem a função somente do embelezamento e da melhoria da qualidade visual e ambiental, elas se transformam em verdadeiros artefatos de engenharia e elementos de uma infraestrutura verde de alto desempenho. A arborização viária ganha força e escala ao conectar fragmentos de florestas urbanas e áreas verdes dispersas no tecido urbano. Os resultados da pesquisa mudam o olhar sobre a várzea dos rios. Renegadas na cidade contemporânea, no Urbanismo Ecológico, as planícies fluviais se tornam elementos estruturais e conectores da malha urbana e de grande valor. A tese parte da hipótese de que é possível implantar o Urbanismo Ecológico em São Paulo através da execução de um processo amplo e ferramentas que vão de políticas públicas, ações da iniciativa privada e envolvimento comunitário, tendo como consequência a melhoria da qualidade ambiental e de vida urbana. A pesquisa foca em Itaquera, bairro impactado pela implantação de grandes equipamentos urbanos pertencentes ao polo institucional e que abriga o novo estádio de futebol do clube Corinthians, para realização de jogos da Copa do Mundo de 2014. Através de levantamentos de campo, mapeamentos e análise de estudos de caso nos Estados Unidos e na África do Sul, identifica-se a clara oportunidade de transformação no entorno da arena a partir da aplicação de princípios ecológicos. Por fim, a pesquisa apresenta uma proposta de Urbanismo Ecológico para o entorno da Arena Corinthians, a partir de suas potencialidades locais, suas áreas verdes, sua hidrografia e a sua nova dinâmica decorrente de novos investimentos públicos e privados. / Ecological Urbanism has emerged as a way to reconcile the landscape with urban occupation, ruled by the potentialities and limitations of natural resources. Green áreas do not function only beautifying and improving the visual and environmental quality, they become true engineering artifacts and elements of a high performance green infrastructure. The street tree system gains strength and scale while connecting fragments of urban forests and green areas scattered in the urban fabric. The research results change the look on the river floodplains. Segregated in the contemporary city, under Ecological Urbanism principles, floodplains become structural elements and links of the urban fabric adding great value. The thesis presents the hypothesis that it is possible to implement the Ecological Urbanism in São Paulo through the implementation of a comprehensive process and tools ranging from public policies, private sector actions and community engagement resulting on the improvement of environmental quality and urban life. The research focuses on Itaquera neighborhood impacted by the implementation of large urban facilities part of an institutional hub and home to the new soccer stadium of Corinthians club that will host World Cup 2014 games. Through field surveys, mapping and analysis of case studies in the United States and in South Africa is possible to identify a clear opportunity for transformation in the vicinity of the arena based on ecological principles. At last, the research presents an Ecological Urbanism proposal for the surroundings of the Arena Corinthians taking advantage of its local potentiality, green areas, hydrograph and new dynamic as a result of new public and private investments.

Esta tese visa a construção de uma biografia histórica do engenheiro agrônomo e ambientalista José Lutzenberger (1926-2002). O objetivo é compreender de que maneira a trajetória de Lutzenberger se articula com a construção de uma ética ecológica, em meio às lutas que ele protagonizou ao longo de trinta e um anos de militância ambiental. O fio condutor da narrativa é a ética ecológica, pois foi o elemento central em seu trabalho, que orientava sua própria visão de como o mundo deveria ser se a humanidade adotasse uma postura que priorizasse a ecologia. Utilizou-se, entre outros acervos, principalmente documentação do Arquivo Privado de José Lutzenberger (APJL): correspondência, recortes de jornais e revistas, iconografia, obras de Lutzenberger e de terceiros, documentos pessoais e oficiais, textos de depoimentos, conferências e de entrevistas, charges, textos técnicos. Também fizemos uso de fontes orais. A tese está estruturada em oito capítulos, de acordo com as lutas e posições ocupadas por Lutzenberger, ao longo de sua trajetória, enfocando as principais campanhas ambientalistas em que se envolveu, o cargo de Secretário de Meio Ambiente no governo Collor, sua atuação como empresário de “tecnologias suaves”, seu trabalho com educação ambiental e agricultura ecológica. O trabalho também analisa as redes de relações tecidas pelo personagem e a abordagem teórica em que se embasou para criar sua ética ecológica, de caráter ecocêntrico. Foi possível avançar no entendimento do arcabouço intelectual de Lutzenberger, bem como na dinâmica de sua militância, oferecendo uma sistematização dos princípios do que chamamos a Ética Lutzenbergeriana, ou Ética do convívio ecossustentável. / This dissertation aims at constructing a historical biography of José Lutzenberger, agronomist and environmental engineer (1926-2002). This biography aids in observing how his trajectory is articulated with the construction of an ecological ethics amidst his protagonism in 31 years of environmental militancy. Ecological ethics conduces this narrative as this was the central element in his work, guiding his own view of how the world should be if Humanity adopted a posture that prioritized Ecology. The main documental source was his private archive (Arquivo Privado de José Lutzenberger - APJL). Other sources used were correspondence, news clippings, iconography, works by Lutzenberger and others, personal and official documents, textual testimonials, conferences and interviews, editorial cartoons, and technical texts. Oral sources have also been used. The 8-chapter structure of this dissertation delineates the positions occupied by Lutzenberger and his trajectory of fight, with focus on the main environmentalist campaigns with which he was involved, as well as his position as Secretary of the Environment during the Collor administration, his business in "soft technology", his work with ecological agriculture and environmental education. This study also presents analysis of the networks created around him, as well as the theoretical bases he used to create the ecological ethics with its eco-centric character. Advances in the understanding of Lutzenberger's intellectual outlines and of the dynamics of his militancy in this work offer a systematization of principles named the Lutzenbergerian Ethics, or the Ethics of Eco-sustainable Life.

Hipóteses e sistemas ecológicos podem ser descritos pelos mais variados tipos de modelos teóricos. Modelos teóricos por sua vez descrevem sistemas idealizados e podem ser construídos sob diferentes abordagens. A ecologia foi profundamente influenciada por modelos ou hipóteses verbais construídos em uma abordagem predominantemente indutiva. Apesar de inspiradoras, tais hipóteses podem apresentar previsões que são logicamente falhas, uma vez que sistemas ecológicos são altamente complexos cujas trajetórias são difíceis de se prever intuitivamente. Neste sentido modelos teóricos quantitativos podem ser usados como ferramentas para traduzir hipóteses e deduzir previsões que podem ser confrontadas com dados reais. Modelos matemáticos são a forma mais tradicional e aceita de abordagem quantitativa. Apesar das vantagens analíticas da aplicação de modelos matemáticos, eles apresentam limitações para tratar de sistemas mais complexos e em escalas mais basais. Além disso, eles podem se tornar rapidamente complicados não só em termos de tratamento matemático mas também de entendimento por parte de um público mais biológico e empírico. Essa dificuldade de entendimento pode estar impedindo que estudos empíricos sejam fortemente embasados em teoria. Neste sentido, modelos computacionais pode ser uma solução promissora. Modelos computacionais podem ser criados para descrever sistemas virtuais que além de ser mais fáceis de serem desenvolvidos e entendidos por biólogos, permitem a inclusão de vários processos, variáveis e interações. Neste trabalho desenvolvemos um modelo baseado em indivíduos (IBM) para descrever comunidades com estocasticidade demográfica, interações intra e inter-específicas e dispersão. Com essa composição de modelo é possível combinar de diferentes maneiras três dos quatro processos presentes em hipóteses e teorias em ecologia, a saber: deriva, seleção e dispersão. No primeiro capítulo descrevemos os detalhes do modelo e como foi sua concepção e implementação. Ainda no neste capítulo simulamos o modelo explorando um espaço de parâmetros arbitrário, i.e. sem especificar um grupo ou sistema de estudo e analisamos o comportamento do modelo em relação à proporção de espécies persistentes ao fim da simulação e comparamos com a previsão do modelo determinístico de competição sem dispersão. No segundo capítulo aplicamos o modelo em uma versão não espacializada para avaliar dentro das premissas do modelo a consistência lógica das previsões da Hipótese da perturbação intermediária (IDH). No terceiro capítulo simulamos o modelo explorando um espaço de parâmetros baseados em dados empíricos de aves e avaliamos quais características das espécies as tornavam mais ou menos suscetíveis à extinção em paisagens com destruição de habitat. Por fim, discutimos brevemente sobre como o modelo apresentado o modelo apresentado e explorado aqui pode ser usado para diferentes propósitos e responder diferentes perguntas dentro dos contextos teóricos de cada capítulo da tese. E concluímos com algumas considerações finais sobre quais foram as contribuições de se desenvolver um modelo computacional e aplicá-lo a diferentes contextos nesta tese para a formação da doutoranda. / Ecological systems and hypothesis can be described by many different kinds of theoretical models. Theoretical models, on the other hand, are idealized descriptions of real systems that can be constructed under different approaches. Ecology was deeply influenced by verbal models or hypothesis under a inductive approach. Although inspiring, such hypothesis can be logically flawed, since ecological systems are highly complex which trajectories are difficult to predict by intuition. Accordingly quantitative theoretical models can be used as tools to translate hypotheses and deduce predictions that can be confronted with empirical data. Mathematical models are most traditional and well-accepted quantitative approach. Despite of the analytical advantages of using mathematical models , they have limitations to address the complexity of biological systems in lower scales. Furthermore, they become rapidly complicated not only in terms of mathematical treatment but also in terms of comprehension by a biological and empirical audience. This difficulties might prevent that theoretical studies predictions play its role of ground empirical studies. In this sense, computer simulation models can be a promising solution. Computer simulation models are more flexible to include various processes, variables and interaction than mathematical models. Furthermore, they create virtual systems that are easier to be developed and understood by biologists. Here, we developed an individual based model (IBM) to describe communities with stochastic demography, intra and inter-specific interactions and dispersion. With this configuration we can build models combining of different manners three of the four processes present in hypotheses and theories in ecology: drift, selection and dispersal. In the first chapter we describe the model details of implementation and conceptions. We also simulated the model to explore a broad parameter space of competing systems, without specifying a group or system of study; we then analyze the model behavior regarding the proportion of persistent species in the end of the simulation and compared the results with the predictions of deterministic model with competition, without dispersion. In the second chapter we apply the model in a non spatialized version of it to assess the logical consistency of the predictions of the Intermediate disturbance hypothesis (IDH). In the third chapter we used the model to describe fragmented landscapes. We explored a parameter parameters based on empirical data of birds and we evaluate which characteristics of the species made them more or less susceptible to extinction in landscapes with habitat destruction. Finally, we discussed briefly how the model can be used for different purposes and some of the future directions within the theoretical contexts of each chapter of the thesis. We conclude the thesis with a reflexion on how the development and exploration of computer model in this thesis contributed to the student ecological background.

Le premier objectif de ce travail de thèse était de déterminer quel est le degré de ségrégation écologique entre cinq espèces sympatriques de cétacés odontocètes (i.e. le dauphin commun Delphinus delphis, le marsouin commun Phocoena phocoena, le grand dauphin tursiops truncatus, le dauphin bleu et blanc Stenella coeruleoalba et le globicéphale noir Globicephala melas) fréquentant l’aire marine restreinte et très productive du Nord-Ouest de la Péninsule Ibérique (NOPI). Pour cela, des paramètres chimiques ont été analysés dans les tissus biologiques, en tant que “ méthode alternative ” pouvant refléter de façon précise le régime alimentaire et l’habitat de ces animaux à différents échelles de temps d’intégration, et ainsi compléter les informations apportées par des méthodes plus traditionnelles tels que l’analyse des contenus stomacaux ou des fèces, ou encore les données d’observations en mer. Le second objectif de ce travail était d’évaluer l’état de contamination de ces espèces, pour acquérir une base de données de référence complète les concernant et estimer le risque toxicologique auquel elles peuvent faire face. Dans ce contexte, les éléments traces, les isotopes stables du carbone et de l’azote, et les polluants organiques persistants (POPs) sont les paramètres chimiques qui ont été sélectionnés pour répondre aux objectifs fixés.Dans un premier temps, les paramètres chimiques ont été utilisés comme traceurs écologiques des populations (ou de segments de population), procurant une image du régime alimentaire et de l’habitat des espèces à différentes échelles de temps. Nous avons calculé que le réseau trophique du NOPI avait cinq niveaux trophiques, au sein duquel les espèces étudiées occupaient les plus hautes positions, comprises entre 4,3 à 5,3, et sans qu’il y ait de différence significative de position trophiques entre les espèces. Alors que l’analyse d’un seul paramètre chimique ne permettait pas ségréger les cinq espèces, les informations apportées par l’analyse de plusieurs traceurs de long terme (i.e. rapport des isotopes stables du carbone et de l’azote dans les dents et concentrations de cadmium dans les reins) ont révélé une ségrégation de leur niche écologique dans deux des dimensions possibles (les dimensions trophique et spatiale). Cependant, les variations pouvant survenir d’une année sur l’autre ou saisonnières n’ont pas pu être étudiées, excepté pour le dauphin commun, et un chevauchement temporaire des niches ne peut donc pas être totalement exclu. De plus, nous avons montré que les profils de polychlorobiphényles (PCBs) pouvaient être un traceur pertinent de l’écologie trophique d’espèces taxinomiquement proches, en permettant une séparation fine des espèces telles que le marsouin commun et le dauphin bleu et blanc, d’après les différents profiles d’accumulation de ces deux espèces.Dans un second temps, l’état de contamination des espèces dans la zone d’étude a été évalué. Les concentrations ont été interprétées à la lumière des facteurs biologiques et écologiques pouvant influencer ces concentrations, et la bioaccumulation des éléments traces s’est révélée moins prévisible que celle des POPs. Le grand dauphin et le marsouin commun présentaient les concentrations de PCBs les plus élevées par rapport aux autres cétacés odontocètes du NOPI et par rapport à d’autres individus des eaux adjacentes de l’Atlantique Nord-Est.Les résultats principaux de ce travail de thèse ont mis en évidence la pertinence d’utiliser ces paramètres chimiques comme traceurs écologiques, et leur utilité dans la compréhension de la structure et le fonctionnement des écosystèmes à travers le rôle des prédateurs supérieurs. En combinant ces résultats à des informations concernant les activités anthropiques, ce travail peut contribuer au développement et à l’implémentation de mesures de gestion pour ces cinq espèces de cétacés odontocètes du NOPI. / The first objective of this PhD was to determine the degree of ecological segregation between five sympatric species of toothed whales (i.e. common dolphin Delphinus delphis, harbour porpoise Phocoena phocoena, bottlenose dolphin Tursiops truncatus, striped dolphin Stenella coeruleoalba and long finned pilot whale Globicephala melas) inhabiting a restricted and highly productive area, the North West Iberian Peninsula (NWIP). To this end, chemical parameters analyses were used as an “alternative method” of assessing diet and habitat of these animals over different periods of integration, complementing the information given by traditional methods of investigation such as stomach contents, faeces analyses and field observations. The second objective was to evaluate the contamination status of these species in order to estimate the toxicological risk these populations face and to complete the existing database. In this context, trace elements, carbon and nitrogen stable isotopes, as well as persistent organic pollutants (POPs) were selected as chemical parameters for our investigations.Firstly, the chemical parameters were used as ecological tracers of populations (or parts of populations) by drawing an image of the diet and habitat of the species at different time scales. We estimated that the food web has five trophic levels, with toothed whales occupying the top positions, with no significant difference in trophic positions among them, ranging from 4.3 to 5.3. While the analysis of a single chemical parameter did not completely segregate between the five species, the information gained by combining the analyses of several long-term ecological tracers (i.e. nitrogen and carbon stable isotopes in teeth and renal cadmium concentrations) revealed ecological niche segregation in two dimensions of this niche (the trophic and the spatial dimensions). However, year-to-year or seasonal variations could not be investigated, except for in common dolphin, and thus temporary overlap cannot be excluded. Additionally, we showed that polychlorinated biphenyls (PCBs) profiles could be a relevant tracer of the foraging ecology of taxonomically close species, allowing a fine separation of the species as result of their different patterns. This was particularly clear for the harbour porpoise and striped dolphin.Secondly, the contamination status of the species in this area was evaluated, with concentrations interpreted in the light of biological and ecological factors. But the bioaccumulation of trace elements appeared to be less predictable than that of POPs. Bottlenose dolphins and harbour porpoises were found to have higher PCBs concentrations than the rest of the analysed NWIP toothed whales, as well as those of adjacent NE Atlantic waters.The main results of this PhD highlight the relevance of exploiting these chemical parameters as ecological tracers, as well as their usefulness in the comprehensive study of structure and function of ecosystems through the role of top predators. Combined with the information on anthropogenic activities, this work can also contribute to the development and implementation of management plans and mitigation measures for these five species of toothed whales in the NWIP.

O Brasil é hoje um dos maiores produtores de madeira nativa do mundo. A demanda por este produto é cada vez maior perante a diminuição da oferta e supervalorização das madeiras de crescimento lento, tornando a silvicultura de espécies nativas um desafio, pois não existem estudos suficientes relacionados à produção de mudas, estabelecimento, crescimento e manejo florestal dessas espécies madeireiras. Neste contexto, este trabalho teve como objetivo avaliar a influência do microssítio na sobrevivência e crescimento de espécies nativas madeireiras utilizadas no enriquecimento artificial de florestas remanescentes na Amazônia (Pará), definidas como Reserva Legal (RL) da propriedade, mas que sofreram exploração madeireira recente, visando recompor e potencializar a exploração econômica dessas áreas. As espécies objeto desse trabalho, que foram usadas no enriquecimento artificial da RL, são: Carapa guianensis, Cedrela fissilis, Cordia goeldiana, Handroanthus serratifolius e Hymenaea courbaril. Essas espécies foram plantadas em abril de 2012 e avaliadas aos 9 e 19 meses após o plantio. Com o objetivo de identificar o momento que essas espécies são mais susceptíveis e que condições do microssítio influenciaram a mortalidade, foram caracterizadas as árvores circundantes à cada muda plantada, a taxa de herbivoria da muda, a possível competição com trepadeiras e plântulas, as aberturas no dossel sobre a muda e a luz difusa incidente. Para testar o efeito da espécie e do tempo na mortalidade das mudas, foi ajustado um modelo linear generalizado misto de análise de variância. Para testar a independência entre a sobrevivência e as variáveis ordinais do microssítio, foram construídas tabelas de contingência bidimensionais e aplicados os correspondentes testes de qui-quadrado. As análises demonstraram que a Carapa guianensis foi a espécie com maior mortalidade nos primeiros meses pós-plantio. Além disso, a mortalidade das espécies foi independente dos fatores luz difusa, árvores circundantes às mudas, trepadeiras e plântulas. Entretanto, a mortalidade de Carapa guianensis, Cedrela fissilis, Cordia goeldiana e Hymenaea courbaril foi explicada pelo vigor das mudas na fase inicial; a mortalidade de Cordia goeldiana foi explicada pela herbivoria; Carapa guianensis e Handroanthus serratifolius tiveram a mortalidade influenciada pela abertura no dossel. Afim de identificar os fatores do microssítio limitantes no crescimento das espécies, foram caracterizadas a herbivoria das mudas, a competição com trepadeiras, a competição com plântulas e luz difusa incidente. Para análise estatística, foram considerados modelos lineares de efeitos mistos para a altura, considerando as variáveis do microssítio. A herbivoria não interferiu no crescimento das espécies avaliadas. A luz direta na muda e a luz difusa alta foram significativas para o crescimento das espécies. Cordia goeldiana, Handroanthus serratifolius e Hymenaea courbaril tiveram crescimento máximo com a variável luz direta. As espécies avaliadas tiveram maior crescimento em locais com mais trepadeiras, provavelmente a maior incidência de luz tenha possibilitado o crescimento das trepadeiras e das espécies plantadas. As interações muita trepadeira x luz difusa alta e muita trepadeira x luz direta tiveram efeito negativo no crescimento de Hymenaea courbaril. O crescimento de Cordia goeldiana foi afetado negativamente pelo número de plântulas circundantes. / Brazil is one of the largest producers of native timber in the world. The demand for this product is increasing towards the supply is decreasing and overvaluation of the slowgrowing wood, turning out native species forestry a challenge because there are not enough studies related to the production of seedlings, establishment, growth and forestry management of these species. In this context, this study aimed to evaluate the influence of micro-sites on survival and growth of native timber species used in artificial enrichment of forest remnants in Amazon (Pará), defined as Legal Reserve (LR) of the property, even though suffered recent logging, aiming to restore the economic potential of these areas. The species used in this study are Carapa guianensis, Cedrela fissilis, Cordia goeldiana, Handroanthus serratifolius and Hymenaea courbaril. These species were planted in April 2012 and evaluated at 9 and 19 months after planting. In order to identify the right moment that those species are more susceptible and which micro-site conditions influenced the mortality, the surrounding trees to each planted seedling were characterized, the rate of herbivory of the seedling, possible competition with vines and other seedlings, openings in the canopy over the seedling and diffuse incident light. To test the effect of species and time in the mortality of seedlings, a generalized linear mixed model analysis of variance was adjusted. To test the independence between survival and the ordinal variables from the micro-site, two-dimensional contingency tables were constructed and applied chi-square tests. Analysis showed that Carapa guianenses was the specie with the greatest mortality in the first months after planting. In addition, the mortality of the species was independent from the factors: diffused light, surrounding trees to seedlings, vines and seedlings of other species. However, the mortality of species Carapa guianensis, Cedrela fissilis, Cordia goeldiana and Hymenaea courbaril was explained by the vigor of the seedlings in the initial phase; the mortality of Cordia goeldiana was explained by herbivory; and Carapa guianensis, Handroanthus serratifolius have mortality influenced by canopy opening. In order to identify the micro-site limiting factors in the growth of the species, herbivory of seedlings, competition with vines, competition with seedlings and diffuse incident light were characterized. Statistical analysis included linear mixed models for height, considering the micro-site variables. Herbivory did not affect the growth of the species assessed. The direct light over the seedling and high diffuse light were significant for the growth of the species. Cordia goeldiana, Handroanthus serratifolius and Hymenaea courbaril had maximum growth with the variable direct light. The species evaluated had higher growth in places with more vines, probably the largest incidence of light enabled the growth of vine and the species planted. Interactions high level of vine x high diffuse light and high level of vine x direct light had a negative effect on the growth of Hymenaea courbaril. The growth of Cordia goeldiana was negatively affected by the number of surrounding plants.