Gotowa bibliografia na temat „Longneck Lagoon, N.S.W”

In the Imboassica Lagoon (22º24'S and 42º42'W) (Macaé, RJ, Brazil), two species of macroalgae of the genus Chara (C. angolensis and C. fibrosa) registered in large areas were identified. The lagoon is subject to several relevant anthropic impacts, of which untreated sewage is one of the most important. Results of the biomass distribution as analyzed in different areas of the lagoon showed values ranging from 172 to 510 gDW.m-2. As for the nutrient concentration, the results presented large fluctuations, with carbon values ranging from 325 to 392 mg.g-1DW, those of nitrogen, from 14 to 27 mg.g-1DW, and of phosphorus from 0.45 to 0.85 mg.g-1DW. This led to large fluctuations of the C:N:P ratio (from 387:24:1 to 872:47:1). The minimum and maximum energetic values of the biomass were 9.54 e 12.34 kJ.g-1DW. Smaller C:N:P ratios tended to occur in more eutrophic areas. The association between biomass and nutrient concentration showed that the highest quantities in the beds are found in oligotrophic areas. The Spearman correlation between nutrient concentration in the water column and biomass was r s = 0.45 (p < 0.05) for nitrogen and r s = 0.50 (p < 0.01) for phosphorus (n = 30). The large total biomass associated with nutrient concentration and energy content indicates that Charophytes are an important biological compartment in the structure and metabolism of the lagoon.

The structure of estuarine fish assemblages at temperate latitudes in Patos Lagoon (32º05'S, 52º04'W), Rio Grande do Sul, Brazil and York River (37º17'N, 76º33'W), Virginia, USA was compared using mid and late 1970's data from bottom trawl collection to investigate whether geographically isolated fish assemblages have similar ecological structure given similar latitudinal positions on the warmtemperate southwestern and northwestern Atlantic regions, respectively. Since estuarine species often exhibit an ontogenetic shift in habitat requirements or preferences we examined Capture per Unity of Effort by size class (CPUE-SC) and split species into "size ecological taxa" (SET) for analysis. The use of CPUE-SC also allowed the abundance of a SET to be computed by summing the mean CPUE of each size class within that SET and use this information to follows SET's temporal and or spatial abundance. A total of 65 and 63 species was collected during a year of bottom trawling in the Patos Lagoon and York River estuaries, respectively. In both localities the strongest modal size class was < 80 mm TL, and several abundant species were smaller than 100 mm TL. The size between 80 and 100 TL effectively separated several species into discrete SET's in both systems. Those SET's could have different ecological preferences, temporal and spatial distributions and so identified as different "ecological taxa". In warm months, when predation by large fish is most likely, the abundance of fish between 80 and 100 mm TL in "bottom trawl" demersal fish assemblages was low in both systems. Only the sea catfishes, in Patos Lagoon, protected by strong dorsal and pectoral spines, and the Hogchoker, in the York River, protected by burrowing in the bottom substrate, peak in abundance at this size class. The seasonal pattern of estuarine use was similar between localities and did not differ from other warm-temperate estuarine fish assemblages.

The Marano and Grado Lagoon, is a northern Adriatic wetland system of relevant naturalistic and economic value, that is constantly under quality control in accordance with the current environmental directives. Benthic foraminifers community with its morphological abnormalities were investigated in the recent sediments (about 10 years old) of 21 stations collected in the framework of the “MIRACLE” Project which aimed at testing the coexistence of clam farming with high Hg contamination. Euryhaline foraminifers, well known in Mediterranean brackish-waters, mainly characterizes the total assemblage. A. tepida dominates in areas characterized by low salinity, high clay and Corg content, but also to anthropogenic pressure. E. gunteri and H. germanica are recorded in the western sector of the lagoon, which is more affected by salinity variations and agricultural activities. Slightly higher values of assemblage diversity appear in less restricted areas of the lagoon or, at least, where physical parameters such as temperature and salinity are less variable. The test abnormalities, carried out on total assemblage, shows that the FAI (Foraminiferal Abnormality Index) values always exceed 1% of the total assemblage, with clear decreasing gradients from inland to the sea (from N to S) and from W to E in the studied area.

The present investigation examines the characteristics of a high energy storm event, that took place on November 9-11, 2007 in the NE Ionian Sea (eastern Mediterranean), and its impact upon the barrier beach that separates the Lefkada lagoon from the open Ionian Sea. The storm event was caused by NW winds with speeds exceeding 20 m/s (40 knots), which have an annual frequency of occurrence less than 0.015%. This high energy event produced waves with >5 m significant offshore height and 9.5 s period; these waves developed on 10th November during the rapid rise of barometric pressure (~1.4 hPa/hr), which followed the barometric pressure drop from 1020.5 hPa at 06:00 (UTC) of 9th November to 1001.7 hPa at 06:00 h (UTC) of 10th November. Secondary breaking at the shoreline produced wave heights >1.5 m, associated with a surge of >0.4 m and a run-up capability of >2.4 m. The waves managed to overtop the barrier beach (elevations ~2.5 m), lowering the seaward side of the barrier beach by 10-30 cm and causing a coastline retreat of 0.9 to 2.2 m; these morphological changes correspond volumetrically to a sediment loss of approximately 8 m3/m of coastline length from the sub-aerial part of the beach. During the last three decades a significant change in the frequency of occurrence and direction (from S-SW-W to N-NW-NE) of severe storms with wind speeds exceeding 40 knots has been recorded, affecting the sediment transport pattern and contributing to the erosion of the north beaches of Lefkada.

Depletion of phytoplankton biomass by the introduced reef-forming polychaete Ficopomatus enigmaticus has previously been observed in the Mar Chiquita lagoon (37°40′S 57°23′W; Argentina), but the effect of polychaetes on the higher trophic levels is still unknown. To evaluate the effect of this polychaete on the zooplankton assemblage, replicated mesocosm experiments (N = 10) were performed during spring, summer and winter. Mesocosms with reefs and without reefs were installed and grazing intensity and the effect on the zooplankton assemblage by the polychaetes were assessed. Our results show that the reefs of F. enigmaticus generate minor changes in overall composition of zooplankton assemblage. Although the structure of the zooplankton assemblage was different between seasons, the impact of the reefs was not significant in any of them. There was no relationship between the decline of food resource by grazing and changes in the structure of the zooplankton assemblage. Thus, contrary to our hypothesis, the grazing impact of the invasive polychaete on the biomass of primary producers did not generate cascading effects to higher trophic levels. However, changes in some components of the zooplankton assemblage (e.g. cladocerans) clearly show that the reefs of F. enigmaticus have the potential to affect the structure of the zooplankton community. The lack of data of community composition and abundance of zooplankton before the invasion limits the understanding of how this polychaete might have affected the structure and abundance of the zooplankton of this lagoon. Nevertheless this work suggests that these changes may not be so significant.

The diet and feeding pattern of scyphomedusa Stomolophus meleagris (Rhizostomeae) was studied, by comparing stomach samples from different developmental stages and environmental zooplankton with the aim to determine diet composition, trophic niche breadth, selectivity and feeding overlap of this edible jellyfish species. Samplings were performed during April and December 2010 and in January 2011, in the coastal lagoon Las Guásimas (27°49′–27°54′N 110°40′–110°35′W), central Gulf of California, which consisted of zooplankton tows and jellyfish collections for stomach content. More than 39 prey items were identified in the gut contents (N = 69), from which eight taxa formed over 90% of the total. Fish eggs were considered main prey (58.6%), copepods (10.8%), veliger larvae of gastropod (13.0%) and bivalve (12.7%) were secondary prey while cirriped and decapod larvae were incidental prey (<3%). However, these proportions varied significantly between small, medium and large size classes of medusa as well as number and type of prey increasing as a function of medusa size. Values of Levin's index confirmed S. meleagris is a specialist predator and Pearre's index showed positive selection of fish eggs, gastropods, bivalves and cirripeds while selectivity was negative for copepods and appendicularians. The relative timing of these changes suggests that ontogenetic processes are closely related with shift in the diet, which indicates increasing predation pressure during development of the medusoid stage of this species, thus emphasizing their ecological importance in coastal ecosystems.

Atol das Rocas, the unique atoll in the South-western Atlantic, is located 144 nautical miles (266 Km) northeast from the city of Natal, NE Brazil and 80 nautical miles from Arquipélago de Fernando de Noronha, with geographic co-ordinates 3º51'S and 33º49"W. It's of volcanic origin and coralline formation. The reef is ellipsoid, its largest axis (E-W) is approximately 3.7 km long, and the shortest (N-S) is 2.5 km. Inside the lagoon, there are two islands: the Ilha do Farol and Ilha do Cemitério, which comprehend 7.2 Km² of emerged area. The Atol das Rocas lodges 143,000 birds, mainly by Sula dactilatra, S. leucogaster, Anous stolidus, A. minuta and Sterna fuscata. Due to their remote location, the islands remain largely undisturbed by the human activities. Aiming to a first characterization of the entomological diversity and the general trophic niches of atoll's entomofauna, three collects were made (1994, 1995 and 1996) utilizing several methods for a wide sample. One thousand six hundred and six insect specimens were collected belonging to eight orders: 1. Coleoptera - 333 individuals of Dermestidae (Dermestes cadaverinus); Tenebrionidae (Phaleria testacea and morphospecies) and Curculionidae (one morphospecies); 2. Dermaptera - 50 individuals of Carcinophoridae (Anisolabis maritima); 3. Diptera - 281 individuals of Ephydridae (Scatella sp. and Hecamede sp.) and Hippoboscidae (one morphospecies); 4. Hymenoptera - 45 individuals of Formicidae (Brachymyrmex sp.); 5. Lepidoptera - 111 individuals of Microlepidoptera (one morphospecies); 6. Mallophaga - 18 individuals in birds (two morphospecies); 7. Orthoptera - 237 individuals of Acrididae (Schistocerca cancellata), Tridactylidae (one morphospecies) and Blattidae (three morphospecies); 8. Thysanoptera -531 individuals (one morphospecies). Also were collected 112 individuals of Arachnida. The taxa of the Order Araneae were represented by the families: 1. Miturgidae (Cheiracanthium inclusum); 2. Salticidae (two morphospecies) and 3. Segestriidae (Ariadna sp.); 4. Theridiidae (Achaearanea sp. and Latrodectus geometricus). For the Order Scorpionida, only samples of Buthidae (Isometrus maculatus) were collected. Through field observations, it was concluded the most insects are detritophagous and/or necrophagous. It is suggested that which the dimension of ecological niches of the insects are a function of the droppings, trash and corpses of birds. A low diversity in the entomofauna of atoll, with its 25 morphospecies, was ascertained.

The Madagascar fauna of the beetle family Hydraenidae is comprehensively revised, based on the study and databasing of 6,949 specimens. New collection records are provided for 11 previously described species, and 95 new species are described. Three new subgenera of Hydraena, viz. H. (Micromadraena), H. (Monomadraena), and H. (Dnahydnaedna) are described, and several new species groups of Hydraena are diagnosed. Two new genera in the tribe Madagastrini are described: Menomadraena and Trinomadraena. The Malagasy hydraenid fauna now comprises 106 species arrayed in the following nine genera: Aulacochthebius (2), Hydraena (65), Limnebius (10), Madagaster (8), Menomadraena (6), Ochthebius (1), Protozantaena (5), Sicilicula (8), and Trinomadraena (1). Lectotypes are designated for the following species: Aulacochthebius plicicollis (Fairmaire), 1898 (Ochthebius); Hydraena dilutipes Fairmaire, 1898; Hydraena impressicollis Fairmaire, 1898; Hydraena marginicollis Regimbart, 1903 (= Hydraena regimbarti Zaitzev 1908; nomen novum); and Ochthebius alluaudi Regimbart, 1903. Hydraena discicollis Fairmaire, 1898, is considered a nomen dubium: no type specimens were found, and the description appears to be that of a species of Aulacochthebius or Ochthebius, not Hydraena. High resolution digital images of lectotypes and holotypes of new species are presented (online versions in color). Male genitalia, representative antennae, maxillary palpi, and female terminal abdominal segments and spermathecae are illustrated. Geographic distributions of all species are mapped. Possible colonization and vicariance events are discussed at the tribal, generic and species group levels. The tribe Madagastrini, found only in Madagascar and southern India, is hygropetric, indicating that this microhabitat type has been continuously present in both Madagascar and India at least since the two separated, currently estimated to be 88 million years ago. Contrastingly, some lowland lentic species of other genera appear to be closely related to species in southern Africa, suggesting rather recent colonization events. New species of Aulacochthebius: A. perlaevis (Mahajanga, Boeny: Mahavavy Kinkony RS). New species of Hydraena (Micromadraena): H. breviceps (Fianarantsoa, 29 km SSW Ambositra, Ankazomivady); H. fortipes (Antsiranana, Forêt d' Antsahabe); H. genuvela (Antsiranana, Forêt de Binara); H. parvipalpis (Antananarivo, Réserve Spéciale d'Ambohitantely); H. rubridentata ((Mahajanga, Parc National de Namoroka); H. serripennis (Antsiranana, Forêt d' Antsahabe). New species of Hydraena (Monomadraena): H. acicula (Antsiranana, Antsaba, Galoko Mountains); H. ambohitantely (Antananarivo, Ambohitantely Spec. Res.); H. amplexa (Fianarantsoa, Andringitra NP); H. amplipunctata (Fianarantsoa, 7 km W Ranomafana); H. antsahabe (Antsiranana, Forêt d' Antsahabe); H. bergsteni (Antsiranana, Diana: Beraty); H. bisinuata (Toamasina, Tamatave 6.3 km S Ambanizona); H. bisinuloba (Toliara, Menabe: Kirindy RS.); H. bispica (Toamasina, Alaotra Mangoro: Analamazoatra SR); H. casacolumna (Fianarantsoa, Andringitra NP); H. compacta (Antananarivo, Ankaratra, Reserve Manjakatompo); H. contracolorata (Antsiranana, Montagne des Francais); H. epipleurata (Antsiranana, Forêt de Binara); H. furcula (Toliara, 40km N of Fort Dauphin, Managotry); H. gereckei (Antananarivo, Ankaratra, Reserve Manjakatompo); H. goldschmidti (Antananarivo, Anjozorobe, Ravoandrina); H. inseriata (Antananarivo, Anjozorobe, Ravoandrina); H. jubata (Antsiranana, Sava Marojejy NP); H. levifurcata (Fianarantsoa, Namarona River, 7 km SW Ranomafana); H. lubrica (Antananarivo, Ambohitantely Spec. Res.); H. mahavavona (Fianarantsoa, Ionilahy, Mahavavona); H. manjakatompo (Antananarivo, Ankaratra, Reserve Manjakatompo); H. marojejy (Antsiranana, Parc National de Marojejy); H. multiarcuata (Fianarantsoa, Ranomafana); H. oscillata (Toamasina, Alaotra Mangoro Andasibe-Mantadia NP); H. parvispinosa (Toamasina, Andasibe NP); H. pentarubra (Antsiranana, Montagne d'Ambre); H. quatriloba (Toliara, Andohahela NP, Tsimelahy); H. ranomafana (Fianarantsoa, Ranomafana); H. ravoandrina (Antananarivo, Anjozorobe, Ravoandrina); H. rubrifurcata (Antsiranana, Sava, Marojejy NP); H. sculponea (Antsiranana, Befingotra (9.2 km WSW), Res. Anjanaharibe-Sud); H. simplicata (Antsiranana, Montagne d'Ambre); H. tibiodentipes (Fianarantsoa, Andringitra NP); H. triaequalis (Fianarantsoa, Ranohira); H. tripartita (Fianarantsoa, Ranomena); H. upsilonica (Toamasina, Zahamena NP); New species of Hydraena (Hydraenopsis): H. andranomena (Toliara, Andranomena); H. arta (Antsiranana, Parc National de Marojejy); H. bucollis (Toamasina, Tamatave, Andranobe Field Station); H. clavulata (Fianarantsoa, Ranomafana); H. contorta (Antananarivo, Anjozorobe forest reserve); H. dilutipoides (Mahajanga, Parc National Tsingy de Bemaraha); H. divisa (Antsiranana, Antsaba,Galoko Mountains); H. elementaria (Antananarivo, Tamatave, Coastal lagoon); H. fulgidicollis (Antananarivo, Parc de Tsimbazaza); H. longiloba (Fianarantsoa, Madiorano); H. nanula (Antsiranana, Ankarana, Ampositelo); H. orchisa (Toamasina, Alaotra Mangoro Andasibe-Mantadia NP); H. pilobova (Antsiranana, Sava, Marojejy NP); H. pilotumida (Fianarantsoa, 7 km W Ranomafana); H. ranarilalatiani (Toamasina, Alaotra Mangoro: Analamazoatra SR); H. randriamihajai (Antsiranana, Diana: Montagne d'Ambre NP); H. renalisa (Antsiranana, Sambava: Marojejy NP); H. sinuatipes (Antsiranana, Ankarana); H. torquata (Fianarantsoa, Andringitra NP). New species of Limnebius: L. angulatus (Fianarantsoa, Namarona River, 7 km W Ranomafana); L. balkei (Antsiranana, Montagne d'Ambre); L. bergsteni (Fianarantsoa, Namarona River, 7 km W Ranomafana); L. clandestinus (Mahajanga, Boeny:Mahavavy Kinkony RSc); L. labratus (Toamasina, Maroantsetra); L. lacrimosus (Toamasina, 18.7911S 48.4259E Alaotra Mangoro Andasibe-Mantadia NP); L. lobatus (Toliara, Manakaravavy); L. maximadus (Toamasina, Alaotra Mangoro: Analamazoatra SR); L. nanostillus (Antsiranana, Ankarana); L. steineri (Fianarantsoa, 7 km W Ranomafana). New species of Madagaster: M. barbata (Fianarantsoa, Andringitra NP); M. bergsteni (Antananarivo, 18.8704S 47.6708E Analamanga); M. cataracta (Antsiranana, Sava, Marojejy NP); M. procarina (Fianarantsoa, 32 km S Ambositra); M. quadricurvipes (Fianarantsoa, Andringitra NP); M. simplissima (Fianarantsoa, 32 km S Ambositra). New species of Menomadraena: M. andringitra (Fianarantsoa, Res. Andringitra); M. concava (Fianarantsoa, R.S. Ivohibe); M. fisheri (Toliara, Enakara (11 km NW), Res. Andohahela); M. ivohibe (Fianarantsoa, R.S. Ivohibe); M. nitedula (Fianarantsoa, Res. Andringitra); M. sembella (Fianarantsoa, Amparihibe). New species of Protozantaena: P. duplicata (Antananarivo, Vakinankaratra: Manjakatompo Stn. Forestière); P. elongata (Antananarivo, Vakinankaratra: Manjakatompo Stn. Forestière). New species of Sicilicula: S. ampla (Antananarivo, Onive River near Ilempona); S. bergsteni (Fianarantsoa, 21.2263S 47.3694E, Matsiara Ambony, Ranomafana NP); S. conjugalis (Fianarantsoa, Namarona River, 7 km SW Ranomafana); S. cordicollis (Fianarantsoa, Namarona River, 7 km SW Ranomafana); S. hygropetrica (Fianarantsoa, Matsiara Ambony, Ranomafana NP); S. malagasica (Fianarantsoa, Abohimahasoa); S. sexplanata (Antsiranana, Mt. Tsaratanana). New species of Trinomadraena: T. clusa (Antsiranana, Mt. d’Ambre).

International visitor surveys (IVS) are traditionally designed to provide destinations with marketing data and intelligence. The New Zealand Tourism Research Institute has been developing new approaches to IVS implementation and data collection in the Pacific Islands that can provide a much richer source of information [1]. The research outlined here is the first to utilise an IVS to explore the positioning of cuisine in the culinary identity of a destination – specifically, the cuisine of the Cook Islands. The Cook Islands is known primarily for its sun, sea and sand features, rather than its culinary attributes. Drawing on data mining of the Cook Islands IVS (2012–2016) and a web audit of destination websites and menus, this paper considers the positioning of food and food-related activities within the Pacific nation’s tourism experience. National tourism organisations are increasingly seeking competitive advantage by utilising their local cuisines as tourist attractions. Research suggests that distinctive local cuisines can act as both a tourism attraction, and as a means of shaping the identity of a destination [2, 3]. In addition to providing an important source of marketable images, local cuisine can also provide a unique experience for tourists. This reinforces the competitiveness and sustainability of the destination [2]. The cuisine of the Cook Islands has come up repeatedly in recommendations for how the country can grow its tourism revenue. Recommendations have been made to improve the food product on offer, develop a distinctive Cook Islands cuisine based on fresh, local produce, and to promote a Cook Islands cuisine experience [4, 5], and to use these to market the Cook Islands as a destination for local food tourism experiences [4]. Despite these recommendations, Cook Island cuisine features less prominently than stereotypical sun, sea, and sand marketing images, and little is known about tourists’ perceptions of and satisfaction with food and food-related activities [6]. Our research addresses this gap by mining IVS data to gain a deeper understanding of tourists’ experiences and perceptions of food in the Cook Islands and assessing whether local food can be positioned as means of creating a unique destination identity. Two methods were used to develop a picture of where food sits in the Cook Islands tourist experience: one focussed on tourist feedback; and the other focused on how food is portrayed in relevant online media. Analysis of all food-related data collected as part of the national IVS between 1 April 2012 and 30 June 2016 was conducted (N = 10,950). A web audit also focused on how food is positioned as part of the Cook Islands tourism product. After identifying the quantitative food-related questions in the IVS, satisfaction with these activities was analysed. Qualitative comments related to food experiences were also examined. The results suggest that participation in food-related activities is generally a positive feature of the visitor experience. The web-audit revealed, however, that food is not a salient feature in the majority of Cook Islands-related websites, and when food did feature, it tended to be oriented towards international cuisine with a ‘touch of the Pacific’ rather than specifically Cook Islands cuisine. This reinforced findings from the IVS data mining that Cook Islands food is presented as a generic tropical ‘seafood and fruit’ cuisine that, largely, lacks the defining and differentiating features of authentic Cook Island cuisine. High participation rates in food-related activities and overall positive evaluations by visitors emerged from the IVS data, yet a dearth of images and information on the country’s food suggests that the Cook Islands is not exploiting its cuisine and food experiences to their full potential. As a direct result of this secondary analysis of IVS data, which highlighted the importance of and potential for food-related activities, the Cook Islands Government is now actively addressing this gap by developing a range of food-related resources and information that can better link tourism to local cuisine. In addition to developing a greater presence of local food in online resources, the Cook Islands Tourism Corporation has also taken on board the messages from the IVS to drive the development of Takurua [7] – an initiative to develop and document local, traditional cuisine and share it with the world. This approach is part of a broader ongoing effort to differentiate the Cook Islands from other South Pacific destinations through its unique cultural attributes. Data mining and secondary analysis of IVS data has not been restricted to the identification of food-related opportunities. Secondary analysis of IVS data in the Pacific has also been used to investigate the impact of other niche markets such as events [8] and to gauge the impact of environmental incidents, for example Cyclone Pam in Vanuatu [9] and algal bloom in the Cook Islands [10], thus reinforcing that IVS data are a rich source of information and are indeed more than just numbers. Corresponding author Tracy Berno can be contacted at tracy.berno@aut.ac.nz References (1) New Zealand Tourism Research Institute (NZTRI). Cook Islands Resources and Outputs; NZTRI: Auckland. http://www.nztri.org.nz/cook-islands-resources (accessed Jun 10, 2019). (2) Lin, Y.; Pearson, T.; Cai, L. Food as a Form of Destination Identity: A Tourism Destination Brand Perspective. Tourism and Hospitality Research 2011, 11, 30–48. https://doi.org/10.1057/thr.2010.22 (3) Okumus, F.; Kock, G.; Scantlebury, M. M.; Okumus, B. Using Local Cuisines when Promoting Small Caribbean Island Destinations. Journal of Travel & Tourism Marketing 2013, 30 (4), 410–429. (4) Food and Agricultural Organization (FAO). Linking Farmers to Markets: Realizing Opportunities for Locally Produced Food on Domestic and Tourist Markets in Cook Islands. FAO Sub-regional Office of the Pacific Islands: Apia, Samoa, 2014. (5) United Nations. “Navigating Stormy Seas through Changing winds”: Developing an Economy whilst Preserving a National Identity and the Modern Challenges of a Small Island Developing State. The Cook Islands National Report for the 2014 Small Islands Developing States (SIDS) Conference and post 2015 Sustainable Development Goals (SDGs). https://sustainabledevelopment.un.org/content/documents/1074217Cook%20Is%20_%20Final%20NATIONAL%20SIDS%20Report.pdf (accessed Jun 10, 2019). (6) Boyera, S. Tourism-led Agribusiness in the South Pacific Countries; Technical Centre for Agriculture and Rural Cooperation (CTA): Brussels, 2016. (7) Cook Islands Tourism Corporation (CITC). Takurua: Food and Feasts of the Cook Islands; CITC: Avarua, Cook Islands, 2018. (8) Thorburn, E.; Milne, S.; Histen, S.; Sun, M.; Jonkers, I. Do Events Attract Higher Yield, Culturally Immersive Visitors to the Cook Islands? In CAUTHE 2016: The Changing Landscape of Tourism and Hospitality: The Impact of Emerging Markets and Emerging Destinations; Scerri, M., Ker Hui, L., Eds.; Blue Mountains International Hotel Management School: Sydney, 2016; pp 1065–1073. (9) Sun, M.; Milne, S. The Impact of Cyclones on Tourist Demand: Pam and Vanuatu. In CAUTHE 2017: Time for Big Ideas? Re-thinking the Field for Tomorrow; Lee, C., Filep, S., Albrecht, J. N., Coetzee, W. JL, Eds.; Department of Tourism, University of Otago: Dunedin, 2017; pp 731–734. (10) Thorburn, E.; Krause, C.; Milne, S. The Impacts of Algal Blooms on Visitor Experience: Muri Lagoon, Cook Islands. In CAUTHE 2017: Time for Big Ideas? Re-thinking the Field For Tomorrow; Lee, C., Filep, S., Albrecht, J. N., Coetzee, W. JL, Eds., Department of Tourism, University of Otago: Dunedin, 2017; pp 582–587.

Biogas production considered the most encouraging sources of renewable energy in Sudan. Anaerobic process of digestion is considered as efficient techniques of producing biogas. The process also a trustworthy method for treatment of municipal wastes, and the digested discharge could be utilized as soil conditioner to improve the productivity. This research work states at the option of using domestic sludge of the wastewater treatment plant in Soba municipal station (south of Khartoum-Sudan) to produce biological gas (biogas). A laboratory investigation was carried out using five-liter bioreactor to generate biogas for 30 days. The total volume of gas made was 270.25 Nml with a yield of 20 Nml of biogas/mg of COD removed. Chemical oxygen demand, Biological oxygen demand, & total solids drop produced were 89, 91 & 88.23% respectively. Microbial activity was declined from 1.8x107 (before starting the process of digestion) to 1.1x105 germs/mL (after completion of 30 days of digestion). This study offered a significant energetic opportunity by estimated the power production to 35 KWh.Key word: Sludge, municipal plant, organic material, anaerobic process, breakdown, biological gas potentialNTRODUCTIONIncreasing of urban industries style in the world has given rise to the production of effluents in huge amounts with abundant organic materials, which if handled properly, be able to end in a substantial source of energy. Although of a fact that there is an undesirable environmental effect related with industrialization, the influence can be diminished and energy can be tapped by means of anaerobic digestion of the wastewater (Deshpande et al., 2012). Biological wastewater treatment plant (WWTP) is a station for removal of mainly organic pollution from wastewaters. Organic materials are partly transformed into sludge that, with the use of up-to-date technologies, represents an important energy source. Chemical biological, and physical technology applied throughout handling of wastewater produce sludge as a by-product. Recent day-to-day totals, dry solids range from 60–90 g per population equivalent, i.e. EU produces per year 10 million tons of dry sludge (Bodík et al., 2011). Sludge disposal (fertilizers use, incineration, and landfills) is often explored since of increasingly limiting environmental legislation (Fytili and Zabaniotou, 2008). The energy present in sludge is obviously consumed in anaerobic digestion. Anaerobic Process is considering the most appropriate choice for the handling of organic effluents of strong content. This process upgraded in the last few years significantly with the applications of differently configured high rate treatment processes, particularly for the dealing of industrial releases (Bolzonella et al., 2005). Anaerobic process leads to the creation of biological gas with high content of methane, which can be recovered, and used as an energy source, making it a great energy saver. The produced gas volume during the breakdown process can oscillate over a wide range varying from 0.5 – 0.9 m3 kg–1 VS degraded (for waste activated sludge) (Bolzonella et al., 2005). This range rest on the concentration of volatile solids in the sludge nourish and the biological action in the anaerobic breakdown process. The residue after digestion process is stable, odorless, and free from the main portion of the pathogenic microorganism and finally be able to use as an organic nourishment for different application in agriculture. Sludge significant coming out from breakdown which allows to yield a renewable energy, that was cheap, obtainable, & no polluting. Sustainable development considered the production of biogas as environmentally friendly and an economic key (Poh and Chong, 2009).OBJECTIVES Sudan have huge tones of sewage sludge from domestic sewage water is accumulated daily in lagoon of soba sewage treatment plant, so this work, we were carried for energy production and treatment of sludge, which constitutes a plentiful waste which ever know any sort of handling after few years from establishing the station.MATERIALS AND METHODSExperimental apparatus: Anaerobic breakdown was done in five liters fermenter. The fermenter was maintained at 35oC in a thermostatic bath and stirred regularly. U shaped glass tube was connected to the fermenter, allowing the measurement of produced biogas volume and pressure. Water displacement technique was used for determination of the volume of produced biological gas (biogas) at the beginning of each sampling. Testing of the biogas combustibility was determined by connecting one of ends of the tube to a gas collection and storage device (balloon), the other end to a Bunsen burner. In the process of reduction of carbon dioxide (CO2) to maximum dissolution in the tube the liquid must be a salty saturated acid solution (5% citric acid, 20% NaCl, pH ¼ 2) (Connaughton et al., 2006).Substrate: About 5L sludge containing culture medium were taken from the lowest part of the first settling tank in Soba station. The moisture content of initial substrate was 35%. The collected sample was preserved at 4oC prior to loading the biological reactor (Tomei et al., 2008). Table 1 showed the sludge features in the reactor with a loading rate of 16 g TS/L, (Connaughton et al., 2006; Tomei et al., 2008).Analytical Methods: The pH was controlled by using HANNA HI 8314 model as pH meter device. Assay was used for determination of Alkanility & Volatile fatty acids (Kalloum et al., 2011). The standard method of analysis was used for recognized the Chemical Oxygen Demand (COD) (Raposo et al., 2009). Titrimetric method was used for analyzing Volatile fatty acids (VFA). Alkalinity assay was used for determination of Total Alkalinity (TA). Oxitop assay was used for measuring the biological oxygen demand. Ignition method was used for measuring Volatile Solids (VS) by losing weight in dry sample at 550oC in the furnace, & Total solids were done to constant weight at 104oC (Monou et al., 2009). A method of water displacement was used for determination of the total volume of Biological gas produced (Moletta, 2005). Microbial species & analyses were determined by microbial standard assay. Sample analysis was done by explore of three replicates and the outcomes were the middling of these replicates. Startup of experiments continues until a bubble of gas was detected.RESULTS AND DISCUSSIONMeasurement of pH: Figure 2 exhibited pH trends during 30 days with a drop pattern from 7.0 to 6.0 during the first five days; this was mainly because of the breakdown of organic materials and the development of (VFA). Then later, an increasing pattern in pH was noticed to 6.98, for the next week, then Steadying around this pH level was continued till the completion of the breakdown period which taken 30 days. Those out comes were also reported by other researchers (Raposo et al., 2008)Measurement of VFA: Development of VFA throughout 30 days was depicted in figure 3, an increase in volatile fatty acids up to 1400 mill equivalents per liter (meq/L) in the first ten days. This criterion of making of volatile fatty acid is typical to the researcher’s report of identification of hydrolysis in acidogenesis stage (Parawira et al., 2006). The decline in volatile fatty acids after the tenth day was owing to intake by bacteria which would relate to the stage of acetogenesis.Total alkalinity (TA): During the ten days, we observed rise in volatile fatty acids content followed by a drop in a pH in the same time (figures 4 and 5). Encountered to these alterations, an increase in the total alkalinity in the medium for reestablishing situations of alkalinity to the outbreak of methanogens stage (figure 4). Through all the digestion period the ratio of VFA/TA which was equal and lower than 0.6±0.1 were described in figure 6. These ratios designated the achievability of the procedure despite the essential production of volatile fatty acid (Chen and Huang, 2006; Nordberg et al., 2007). The anaerobic digestion process may be hinder by the production of volatile fatty acid.Biogas production: Pressure measurement and biogas volume were used for controlling biogas production. Figure 7 explained the changing in biogas pressure throughout the digestion period. quality of Biogas was obtained with minimum methane of 40% (Bougrier et al., 2005; Lefebvre et al., 2006). Total volume of biological gas production was 270.25 Nml. The yield of biological gas was 20.25 Nml/mg COD removed, which is in range of the others researcher report (Tomei et al., 2008). Biogas production can be calculated from the following formula (Álvarez et al., 2006): Biogas production= (Total quantity of biogas produced)/(Total solid).The COD and BOD removal: Chemical oxygen Demand (COD) and Biological Oxygen Demand (BOD) showed a significant reduction of 89% and 91% respectively (figures 8 and 9). Consequently these reduction in contaminants proved that anaerobic process of digestion was an operational technique for removal of organic pollution. Some researchers reported the same results (Bolzonella et al., 2005; Álvarez et al., 2006; Wang et al., 2006). Another criterion for proving the removal of organic pollutants was reduction of total solids (TS), where the drop approached 88.23% (figure 10). Some researcher’s reports approached the same drop (Hutnan et al., 2006; Linke, 2006; Raposo et al., 2009). Therefore it was possible to conclude that anaerobic digestion necessary showed decrease or reduction of organic pollutants rates because of the transformation of organic substances into biogas and accordingly led to the drop of chemical oxygen demand (COD). This could be explained in figure 11 by the comparison of the two techniques during the anaerobic digestion process. That means the chemical oxygen demand (COD) drop should be tailed essentially by Total solids drop (TS).Microbial activity: Figure 11 showed the microbial variation during anaerobic digestion. The total micro flora (total germs) declined from 1.8x107 (before starting the process of digestion) to1.1x105 germs/mL (after completion of 30 days of digestion). Moreover figure 12 obviously explained what was running during the process of digestion in the reactor, microbial species vanishing after the 30 days such as streptococci and Escherichia coli. Some researchers reports explained that there was some sort of relationship between physicochemical and the biological parameters of micro flora with total solid (TS). figure 13 described obviously this relationship of the drop of micro flora which go along with total solids reduction. This intended that consumption and a declining in the mass residue of organic materials created at the termination of digestion was the outcome of the transformation of organic materials into biological gas and also the sum of microorganism reduction. This attained result proved that the process of anaerobic digestion was a good process for decontamination (Deng et al., 2006; Perez et al., 2006; Davidsson et al., 2007).CONCLUSIONSoba sludge’s municipal station carried in this research paper demonstrated operative for biological gas production (biogas). During the first five days, breakdown of organic materials and the formation of volatile acids were started. Volatile fatty acids increased up to 1400 mill equivalents per liter (meq/L) in the first ten days, then started to decline in after the tenth day this owing to intake by bacteria which would resemble to acetogenesis stage. The biogas production lasted until the 21th day then starting decreasing till the last day (30 day) this due to instability of the culture medium of fermentation which became completely poor. COD and BOD showed a significant reduction of 89% and 91% respectively. Another criteria for proving of removal rate of organic pollutants was reduction of total solids (TS), where the reduction rate approached 88.23%. Total volume of biological gas production was 270.25 Nml. The yield of biological gas was 20.25 Nml/mg COD removed, which is in range of the others researcher report. The total micro flora (total germs) declined from 1.8x107 (before starting the process of digestion) to 1.1x105 germs/mL (after completion of 30 days of digestion). Study proved that process of anaerobic digestion was a good process for decontamination. Industries and will be usefulness for bioremediation in marine environment and petroleum industry.ACKNOWLEDGMENTSThe authors wish to express their appreciation to Soba treatment plant, for their financial support of this research.CONFLICT OF INTERESTThe authors wish to express their appreciation to Soba treatment plant, for their financial support of this research.REFERENCES Álvarez, J., I. Ruiz, M. Gómez, J. Presas and M. Soto, 2006. Start-up alternatives and performance of an uasb pilot plant treating diluted municipal wastewater at low temperature. Bioresource technology, 97(14): 1640-1649.Bodík, I., S. Sedláček, M. Kubaská and M. Hutňan, 2011. Biogas production in municipal wastewater treatment plants–current status in eu with a focus on the Slovak Republic. Chemical biochemical engineering quarterly, 25(3): 335-340.Bolzonella, D., P. Pavan, P. Battistoni and F. Cecchi, 2005. Mesophilic anaerobic digestion of waste activated sludge: Influence of the solid retention time in the wastewater treatment process. Process biochemistry, 40(3-4): 1453-1460.Bougrier, C., H. Carrere and J. Delgenes, 2005. Solubilisation of waste-activated sludge by ultrasonic treatment. Chemical engineering journal, 106(2): 163-169.Chen, T.-H. and J.-L. Huang, 2006. Anaerobic treatment of poultry mortality in a temperature-phased leachbed–uasb system. Bioresource technology, 97(12): 1398-1410.Connaughton, S., G. Collins and V. O’Flaherty, 2006. Psychrophilic and mesophilic anaerobic digestion of brewery effluent: A comparative study. Water research, 40(13): 2503-2510.Davidsson, Å., C. Gruvberger, T. H. Christensen, T. L. Hansen and J. la Cour Jansen, 2007. Methane yield in source-sorted organic fraction of municipal solid waste. Waste management, 27(3): 406-414.Deng, L.-W., P. Zheng and Z.-A. Chen, 2006. Anaerobic digestion and post-treatment of swine wastewater using ic–sbr process with bypass of raw wastewater. Process biochemistry, 41(4): 965-969.Deshpande, D., P. Patil and S. Anekar, 2012. Biomethanation of dairy waste. Research journal of chemical sciences, 2(4): 35-39.Fytili, D. and A. Zabaniotou, 2008. Utilization of sewage sludge in eu application of old and new methods—a review. Renewable sustainable energy reviews, 12(1): 116-140.Hutnan, M., M. Drtil and A. Kalina, 2006. Anaerobic stabilisation of sludge produced during municipal wastewater treatment by electrocoagulation. Journal of hazardous materials, 131(1-3): 163-169.Kalloum, S., H. Bouabdessalem, A. Touzi, A. Iddou and M. Ouali, 2011. Biogas production from the sludge of the municipal wastewater treatment plant of Adrar city (Southwest of Algeria). Biomass bioenergy, 35(7): 2554-2560.Lefebvre, O., N. Vasudevan, M. Torrijos, K. Thanasekaran and R. Moletta, 2006. Anaerobic digestion of tannery soak liquor with an aerobic post-treatment. Water research, 40(7): 1492-1500.Linke, B., 2006. Kinetic study of thermophilic anaerobic digestion of solid wastes from potato processing. Biomass bioenergy, 30(10): 892-896.Moletta, M., 2005. Characterization of the airborne microbial diversity of biogas. In: PhD diss. Montpellier 2.Monou, M., N. Kythreotou, D. Fatta and S. Smith, 2009. Rapid screening procedure to optimise the anaerobic codigestion of industrial biowastes and agricultural livestock wastes in cyprus. Waste management, 29(2): 712-720.Nordberg, Å., Å. Jarvis, B. Stenberg, B. Mathisen and B. H. Svensson, 2007. Anaerobic digestion of alfalfa silage with recirculation of process liquid. Bioresource technology, 98(1): 104-111.Parawira, W., M. Murto, R. Zvauya and B. Mattiasson, 2006. Comparative performance of a uasb reactor and an anaerobic packed-bed reactor when treating potato waste leachate. Renewable energy, 31(6): 893-903.Perez, M., R. Rodriguez-Cano, L. Romero and D. Sales, 2006. Anaerobic thermophilic digestion of cutting oil wastewater: Effect of co-substrate. Biochemical engineering journal, 29(3): 250-257.Poh, P. and M. Chong, 2009. Development of anaerobic digestion methods for palm oil mill effluent (pome) treatment. Bioresource technology, 100(1): 1-9.Raposo, F., R. Borja, M. Martín, A. Martín, M. De la Rubia and B. Rincón, 2009. Influence of inoculum–substrate ratio on the anaerobic digestion of sunflower oil cake in batch mode: Process stability and kinetic evaluation. Chemical engineering journal, 149(1-3): 70-77.Raposo, F., R. Borja, B. Rincon and A. Jimenez, 2008. Assessment of process control parameters in the biochemical methane potential of sunflower oil cake. Biomass bioenergy, 32(12): 1235-1244.Tomei, M., C. Braguglia and G. Mininni, 2008. Anaerobic degradation kinetics of particulate organic matter in untreated and sonicated sewage sludge: Role of the inoculum. Bioresource technology, 99(14): 6119-6126.Wang, J., D. Shen and Y. Xu, 2006. Effect of acidification percentage and volatile organic acids on the anaerobic biological process in simulated landfill bioreactors. Process biochemistry, 41(7): 1677-1681.