Submitted by Cleide Dantas (cleidedantas@ufpa.br) on 2014-11-10T12:08:47Z No. of bitstreams: 2 license_rdf: 22974 bytes, checksum: 99c771d9f0b9c46790009b9874d49253 (MD5) Dissertacao_VariacaoEspacoTemporal.pdf: 992324 bytes, checksum: 3daa5caed6fa37d3623253f262d663c7 (MD5) / Approved for entry into archive by Ana Rosa Silva (arosa@ufpa.br) on 2014-11-10T13:34:02Z (GMT) No. of bitstreams: 2 license_rdf: 22974 bytes, checksum: 99c771d9f0b9c46790009b9874d49253 (MD5) Dissertacao_VariacaoEspacoTemporal.pdf: 992324 bytes, checksum: 3daa5caed6fa37d3623253f262d663c7 (MD5) / Made available in DSpace on 2014-11-10T13:34:02Z (GMT). No. of bitstreams: 2 license_rdf: 22974 bytes, checksum: 99c771d9f0b9c46790009b9874d49253 (MD5) Dissertacao_VariacaoEspacoTemporal.pdf: 992324 bytes, checksum: 3daa5caed6fa37d3623253f262d663c7 (MD5) Previous issue date: 2011 / Ao longo das últimas décadas, a carcinicultura vem apresentando um grande crescimento em diversas partes do mundo, com o Brasil seguindo esta tendência mundial (FAO, 2004). Nesta atividade três espécies de camarão têm se destacado como as mais cultivadas, sendo elas Penaeus monodon (Fabricius, 1798), Fenneropenaeus chinensis (Osbeck, 1765) e Litopenaeus vannamei (Boone, 1931), responsáveis por cerca de 80% da produção mundial (FAO, 2004). No Brasil L. vannamei é a espécie mais cultivada, com a produção brasileira correspondendo a 5% da produção mundial (FAO, 2004). L. vannamei é uma espécie marinha originária do Oceano Pacífico, distribuída do México ao Peru. Por ser eurihalino, este camarão pode se adaptar às mais diversas condições de cultivo, desde águas salgadas até de menores salinidades (BRAY et al., 1993; PONCE-PALAFOX et al., 1997), característica que tem aumentado o interesse dos produtores. Embora seja exótica no Brasil, L. vannamei, mostra maior resistência à variação de temperatura e salinidade do que outros camarões peneídeos nativos (BRITO et al., 2000). O alimento do camarão e as estratégias de seu fornecimento têm merecido uma atenção especial do setor, gerando novas técnicas ou seu aperfeiçoamento. A ração nos sistemas de cultivo intensivo e semi-intensivo, por exemplo, é responsável por 50-60% dos custos totais de produção, demonstrando a importância de novas estratégias para minimizar sue uso. O aumento da biomassa do plâncton (alimento natural), e conseqüentemente, da cadeia alimentar, reduz os custos com a alimentação suplementar, influenciando diretamente os custos finais de produção (AVAULT, 2003). Segundo Nunes (1995), o incremento da produtividade natural é tão importante quanto o uso de uma ração nutricionalmente completa e bem balanceada. Logo após a introdução nos viveiros de cultivo, a base da alimentação de L. vannamei é composta, em parte, pelo alimento natural disponível (NUNES et al. 1997; MARTINEZ-CORDOVA et al. 1997; ROTHLISBERG, 1998) complementada com ração comercial. Martinez-Cordova et al. (2002) mostraram que as concentrações de clorofila ‘a’ diminuem cerca de 50% do início ao fim do cultivo, provavelmente devido a pastagem pelo zooplâncton e por alguns invertebrados bentônicos. Além da importância do zooplâncton como alimento para as pós-larvas de camarão nos viveiros de engorda, o uso destes organismos (principalmente copépodes) como alimento vivo na aqüicultura marinha vem recebendo grande atenção nos últimos anos (DELBARE et al. 1996). Tal fato ocorre por serem ricos em fosfolipídios, ácidos graxos essenciais altamente insaturados e antioxidantes naturais, sendo nutricionalmente superiores aos rotíferos e aos náuplios de artemia, comumente usados na larvicultura marinha (SARGENT et al. 1997, STOTTRUP e NOSKER, 1997) promovendo o sucesso as larviculturas de camarão (PAYNE et al. 1998; SCHIPP et al. 1999; PAYNE e RIPPINGALE, 2000). Desta forma, estudos sobre o cultivo intensivo de camarões marinhos que enfoquem a composição da comunidade planctônica, as variáveis bióticas e abióticas no sistema, e a característica dos efluentes gerados, são de grande importância. Assim, os resultados obtidos podem incrementar a produtividade aquática no cultivo, alem de fornecer subsídios para pesquisas posteriores de avaliação e mitigação dos impactos ambientais causados por esta atividade.

The south coast of South Africa represents the extreme western end of the range of the Indo-Pacific humpback (Sousa chinensis, plumbea type) and Indo-Pacific bottlenose dolphins (Tursiops aduncus), which are both confirmed to range as far west as False Bay (Jefferson & Karczmarski, 2001; Hammond et al., 2008). Individual ranging behaviour for both species however is not well resolved. Recent genetic analyses suggest that animals currently considered as plumbea type Sousa chinensis (Reeves et al., 2008) may be a separate species, Sousa plumbea (Mendez et al., 2013). In South African waters less than 1000 adult humpback dolphins (Sousa chinensis, plumbea type hereafter “humpback dolphin”) may comprise the entire population (Karczmarski, 1996), while all estimates suggest the bottlenose dolphin (Tursiops aduncus, hereafter “bottlenose dolphins”) population is relatively large, numbering thousands of animals (Cockcroft et al., 1992; Reisinger & Karczmarski, 2010). Both dolphin species are exposed to variable levels of anthropogenic impacts throughout their range including vessel traffic, chemical pollution and habitat degradation associated with coastal development. This thesis describes the results of a study investigating: 1) the environmental and anthropogenic factors which influence the habitat use of humpback and bottlenose dolphins in two adjacent bays on the southern Cape coast, South Africa – Mossel Bay and Vlees Bay; 2) the abundance of humpback dolphins using Mossel Bay and 3) the interaction of these two dolphin species with white sharks, and the influence this has on dolphin group sizes and habitat use in Mossel Bay. Both land-based and boat-based survey platforms were used in this study with land-based data collected during dedicated watch periods at sites in Mossel Bay (n = 6) and Vlees Bay (n = 4) between February 2011 and March 2013, with a focus on humpback and bottlenose dolphins. A surveyor’s theodolite was used at these sites to collect positional data on animals, while behavioural data were collected through direct observation. Boat-based photographic identification surveys were used to collect data on the presence of individual humpback dolphins in Mossel Bay between April 2011 and November 2013. White shark data from Mossel Bay between February 2011 and March 2013 were provided from boat-based chumming surveys for the collection of photo-ID data from the Master’s thesis of Rabi’a Ryklief, based at Oceans Research. Data were analysed using ANOVA’s, Tukey honest significance tests and generalised additive modelling (Wood, 2006) in programme R, while capture histories of humpback dolphins were analysed with RMark (Laake, 2013) using POPAN open population models (Schwarz & Arnason, 1996) and Huggins heterogeneity closed capture models (Huggins, 1989; Chao et al., 1992). Humpback dolphins socialised over sandy beach habitats in both bays, while feeding/foraging occurred over reef systems in Mossel Bay and off fine grained sandy beach habitats in Vlees Bay. Humpback dolphin resting behaviour was observed at a very low frequency and occurred in all of the primary habitat types in Mossel Bay, while in Vlees Bay resting was only observed over reefs. Bottlenose dolphins in both bays preferentially used wave cut rocky platform habitats for feeding/foraging and resting while socialising occurred in the vicinity of estuaries in Mossel Bay and fine grained sandy beach habitats in Vlees Bay. Higher sighting rates were recorded in the control site, Vlees Bay, than in Mossel Bay for both dolphin species. The largest reverse osmosis desalination plant commenced operations in the sheltered corner of Mossel Bay in October 2011 and discharged approximately five million litres (Ml) of effluent per day (between October 2011 and February 2012) and 18 Ml per day in March and April 2012. In Mossel Bay higher sighting rates of humpback dolphins occurred in the period before desalination began while bottlenose dolphin sighting rates were highest after active desalination decreased to once per month (May, 2012). During the period of peak brine discharge in Mossel Bay, sighting rates were highest for both species in Vlees Bay. Even after desalination operations decreased the sighting rate of humpback dolphins remained low. The operation of the desalination plant at full capacity in Mossel Bay may have led to reduced use of this area by both humpback and bottlenose dolphins. Key habitats in Mossel Bay for both dolphin species are shared with great white sharks (Carcharodon carcharias hereafter “white sharks”) and focus around the three estuaries and their associated near-shore reef systems. The presence of predatory white sharks may limit the time dolphins spend in a specific habitat and influence the number of animals within groups, with larger humpback dolphin groups at sites with high shark utilisation. Both dolphin species had lower individual sighting rates during periods when white shark abundance peaked. Large group sizes of humpback dolphins at Seal Island, and of bottlenose dolphins at Hartenbos and Tergniet, combined with increased rates of travelling and decreased resting and socializing suggest that these areas may pose the largest threat to dolphins due to the variety of shark size classes’ present, especially larger sharks. Closed capture models generated within year population estimates ranging from 48 to 97 individual humpback dolphins (2011: 97, 95% CI: 46 – 205; 2012: 48, 28 – 81; 2013: 68, 35 – 131) while open population modelling produced a ‘super-population’ estimate of 116 animals (95% CI: 54 – 247) using Mossel Bay. During the study 67 humpback dolphins were individually identified with 94.3 % of the individuals in good quality photographs distinctively marked. Fewer humpback dolphins may be present on the south-east and southern Cape coast, including between Algoa Bay and Mossel Bay, than initially thought (Karczmarski, 1996), as definite links exist between Algoa Bay and Plettenberg Bay (Smith-Goodwin, 1997), and Plettenberg Bay and Mossel Bay (this study). The Gouritz River mouth (21º 53' E; Ross, 1984) and De Hoop (20º 30' E; Findlay et al., 1992) were previous suggested as the western limit of this species, but within the last 20 years knowledge on the extent of their range has been greatly improved, and range extension of this species may be occurring to the west with animals present as far west as False Bay (18º 48' E; Jefferson & Karczmarski, 2001). Due to the vulnerability of this species and their wide ranging behaviour, conservation plans need to be implemented on a wide scale to ensure protection of these animals from human impacts throughout their range. A concerted effort is required to further establish the population links between the various locations on the southern Cape coast that these animals frequent. / Dissertation (MSc)--University of Pretoria, 2014. / Zoology and Entomology / MSc / Unrestricted