Keyword

marine

174 record(s)
 
Type of resources
Topics
Keywords
Contact for the resource
Provided by
Years
Formats
Representation types
Update frequencies
status
Scale
From 1 - 10 / 174
  • Categories    

    This dataset is a compilation of available ocean temperature data, aerial and in-water bleaching observations during the 2016 and 2017 bleaching events on the Great Barrier Reef in order to estimate the total reef area impacted by coral bleaching and thermal heat stress. A total of 982 reefs (56.8% reef area of the GBR) were surveyed in 2016 and 781 reefs (50.9% reef area of the GBR) surveyed in 2017. This analysis provides an improved understanding of the variability and the increase in spatial impacts from coral bleaching throughout the GBR in a warming ocean. This data compilation of available bleaching survey data was used to provide: i) a quantitative assessment of the spatial variability of accumulated heat stress, severe coral bleaching and mortality throughout the GBR on regional and within individual reef scales, in comparison with previous widespread bleaching events in 1998 and 2002; ii) a quantitative comparison of bleaching observations from a range of observers which used a variety of methods and spatial assessments. The recent heat waves in 2016 and 2017 were unprecedented for the GBR. Temperatures remained above historical summer maximums for more than three months, and maximum anomalies in some locations were as high as 2.9°C (2016) and 3.2°C (2017) above the recent historical average summer maximum (1985-2012). During the 2016 - 2017 bleaching events, both coral bleaching and coral mortality occurred at a lower level of accumulated heat stress than previously proposed by the National Oceanic and Atmospheric Administration (NOAA) Coral Reef Watch (CRW) Degree Heating Week (DHW) product. The combined data recorded widespread coral bleaching occurring at a NOAA DHW value of 2-4 degree-weeks, severe bleaching, and some coral mortality at 5-8 DHW’s, and extensive mortality at reefs exposed to more than 8 DHW’s. Prior to this event, the general guideline based upon previous observations was that coral bleaching would occur at a DHW >4 and that coral mortality would begin at a DHW >8. In 2016 and 2017 on the GBR at heat stress exposures of 2.5°C-weeks we observed coral bleaching, after 5°C-weeks severe bleaching and some mortality and severe mortality following 8°C-weeks. Methods: All available aerial and in-water bleaching observations were assessed to quantify the relationship between coral bleaching and accumulated heat stress from ocean SST products and bleaching severity and coral mortality. Sea Surface Temperature Data was sourced from SSTAARS Climatology, NOAA-CRW Degree Heating Week (DHW). Broad spatial coverage of satellite Sea Surface Temperature (SST) monitoring products (NOAA Coral Reef Watch) were combined with the established relationship of observed bleaching severity with the accumulated heat stress product NOAA Degree Heating Weeks (DHWs), to scale up estimates of bleaching to the whole GBR. The NOAA Degree Heating Week product is a thermal stress index which combines the intensity of the temperature anomaly (Hotspot) at least 1°C above the historical summer Maximum Monthly Mean (MMM, Version 3.1) temperature (upper thermal threshold) with the duration of time exceeding this threshold over a 12 week period. Coral Bleaching Surveys Aerial Data was sourced from: Aerial – Berkelmans 1998 - Aerial survey of the GBR during the 1998 bleaching event [Region: Whole of GBR, Dates: 1998-03-09, Number of sites: 495 reefs]. AIMS Aerial – Berkelmans 2002- Aerial survey of the GBR during the 2002 bleaching event [Region: Whole of GBR, Dates: 2002-03-20, Number of sites: 1295 reefs]. AIMS Aerial - Hughes 2016 – Aerial survey of the GBR during the 2016 bleaching event [Region: Whole of GBR, Dates: 2016-03-22/2016-04-28, Number of sites: 924 reefs]. JCU and TSRA Aerial - Hughes 2017 – Aerial survey of the GBR during the 2017 bleaching event [Region: Whole of GBR, Dates: 2017-03-15 / 2017-04-05, Number of sites: 725 reefs]. JCU Aerial – AIMS 2017 - Aerial survey of the GBR during the 2017 bleaching event [Region: Townsville and Cairns, Dates: 2017-03-09, Number of sites: 70 reefs]. AIMS and GBRMPA Data handling: The data from Berkelmans 1998 and Berkelmans 2002 was presented with five-point rating (1-5) but converted to align with the Hughes dataset format (Category 0-4). Berkelmans Hughes 5 (<1% bleached) = 0 4 (1–10% bleached) = 1 3 (10–30% bleached ) = 2 2 (30–60% bleached) = 3 1 (>60% bleached) = 4 Methods: Aerial Bleaching Surveys: conducted from a combination of light fixed wing aircraft and helicopter, flying at an elevation of approximately 150m. This method accurately captures the proportion of healthy and bleached coral colonies in the shallow reef flat (0-3m) and in the upper reef slope (0-6m). Reefs were scored independently (isolated communications) by 2-4 observers looking out the left and right windows of the aircraft. Bleaching scores were recorded on spatial GBRMPA zoning reef maps, with mapping handheld GPS devices recording the flight path and confirming the reef location during the flight (Berkelmans & Oliver 1999; Berkelmans et al. 2004; Hughes et al. 2017). Surveys in 1998 and 2002, did not have GPS recorders. Reefs were categorised by visual assessment based upon the proportion of living coral visible to the observer that appeared bleached, severely bleached white, or fluorescent, into five community bleaching severity categories: 0 (no bleaching) <1%, 1 (moderate) 1-10%, 2 (high) 10-30%, 3 (very high) 30-60%, 4 (extreme bleaching) > 60%; These categories were used to align with the protocols developed in 1998 by Ray Berkelmans and GBRMPA (Berkelmans & Oliver 1999; Berkelmans et al. 2004). Photographs of each categorised reef in 2016 were recorded, stored, geo-located with GPS locations and made available to the public through the JCU Centre of Excellence for Reef Studies website (https://www.coralcoe.org.au/coral-bleaching-map). Images from the GBRMPA flight in 2017 between Townsville and Cairns will be available through the eAtlas. Coral Bleaching Surveys In-water: Sectors: • Far North (9-14°S; including the Torres Strait) • Northern (14-18°S; Innisfail to Cooktown) • Central (18-21°S; Mackay to Innisfail) • Southern sector (21-24°S; Mackay to Gladstone). AIMS 2016 - In water survey of reefs in the Townsville-Cairns area in 2016 [Region: Central and Northern sectors, Method: in water – 1m belt Transect, Dates: 2016-03-02 / 2016-04-06, Number of sites: 27 reefs] Reported metrics: Bleaching categories 1-4, % Mortality, % Bleaching AIMS 2017 - In water survey of reefs in the Townsville-Cairns area in 2017 [Region: Central and Northern sectors, Method: in water – 1m belt Transect, Dates: 2017-03-14 / 2017-04-01, Number of sites: 19 reefs] Reported metrics: Bleaching categories 1-4, % Mortality, % Bleaching GBRMPA 2016 - In water survey of reefs in the GBR area in 2016 [Region: all sectors, Method: in water – RHIS, Dates: 2016-03-02 / 2016-06-11, Number of sites: 102 reefs] Reported metrics: Bleaching categories 1-4, % Mortality, % Bleaching GBRMPA EotR 2015-2017- Eye on the Reef CoTS Control team observers in water survey of reefs in the GBR area in 2016/2017 [Region: all sectors, Method: in water – RHIS (5m radius), Dates: 2016-02-01 / 2017-04-30, Number of sites: 1200 reefs] Reported metrics: Bleaching percent by coral type, Mortality percent by coral type, % Bleaching, % Mortality Frade 2016 - Local survey up to 40m depth to test depth as refuge for bleaching. [Region: Far North and Northern sectors, Method: in water – 1m belt Transect, Dates: 2016-05-14/23, Number of sites: 6 reefs / 9 sites] Reported metrics: Bleaching categories 1-4. University of Queensland Global Change Institute. Baird 2016 - Local survey up to 27m depth to test depth as refuge for bleaching.[Region Far North, Method: in water – 1m belt Transect, Dates: 2016-04-11/14, Number of sites: 7 reefs / 11 sites] Reported metrics: Bleaching categories 1-6 to genus level coral ID Methods: In-water quantitative transect based surveys conducted by AIMS: In-water surveys were conducted between Townsville and Port Douglas by the AIMS at 54 sites within 19 reefs in 2016 and 40 sites within 12 reefs in 2017, from 13 March – 6 April 2016 and from 14 March – 1 April 2017. Surveys were conducted following the onset of maximum temperature exposure to capture the bleaching response at its peak, with an additional 0 – 2.9 DHW accumulating following the time of the survey. Follow up surveys were conducted in June 2016, September 2016 and September 2017 to assess survivorship. For each reef, surveys were conducted at three habitats: (1) shallow, sheltered reef flat at 2m; (2) exposed shallow reef slope at 3m; and (3) deeper exposed reef slope at 7-9m along permanent AIMS Long-term monitoring sites or equivalent on the northern exposed flank of each reef. Scleractinian hard corals >5cm in diameter were identified to genus level and bleaching severity categorised as: (1) healthy; (3) minor-moderate bleaching (paling/ 1-50%; (4) major bleaching (51-90% bleached); severe bleaching (100% white) and (6) recently dead (full colony or partial sections of the colony). In water surveys conducted by the University of Queensland Global Change Institute (Frade et al. 2018) were conducted between 14 - 23 May 2016 at nine sites within six outer shelf reefs in the Northern Sector of the GBR, at a depth of 5, 10, 25 and 40m, in order to determine the effect of bleaching over a large depth range. Surveys were conducted along 1m belt transects covering 75m length at each depth. Scleractinian hard corals >10cm in diameter were identified to genus level and bleaching severity categorised as: (1) healthy; (2) minor bleaching (paling/ 1-50%; (3) severely bleached (51-100% bleached) and (4) recently dead. In-water qualitative Reef Health Index Surveys (RHIS): In water surveys conducted by the GBRMPA field management team in 2016 were conducted at a total of 62 reefs across seven inshore-offshore transects following guidelines outlined in the Coral Bleaching Risk and Impact Assessment Plan (GBRMPA 2011). The survey plan aimed to conduct 15 or more Reef Health Index Surveys (RHIS) (that is, replicate samples) across three different locations on each reef, corresponding to three different aspects (north-east, north-west and south-west). At each of the western locations (i.e. north-west and south-west), three RHIS surveys were conducted at the same depth (approximately one to four metres), making a total of six RHIS. At the north-eastern location, three surveys were conducted at three different depths (approximately one to three metres, six metres and nine metres), making a total of nine RHIS. Surveys followed the standard protocol for Reef Health Impact Surveys (RHIS) (Beeden et al. 2014). Key information recorded includes: i) qualitative estimates of the percentage of the benthos (sea floor) made up by macroalgae, live coral, recently dead coral, live coral rock, coral rubble and sand; and ii) observations of coral impacts, and this is done over a series of five-metre radius point surveys (with one RHIS form completed for each circular plot of 78.5 square metres). The percentage of coral cover (if any) that had recently died from each impact-type (that is, bleaching, disease, predation, damage) was estimated as described in Beeden et al. (2014) for each RHIS survey by examining all coral colonies within the point surveys for any impacts. These data were used to categorise the percentage of bleached corals within the total living coral within each RHIS area. For comparison to all aerial survey data and the in-water transect based quantitative estimates, the average RHIS per cent bleached scores for each reef were converted to align with the aerial bleaching categories described above (Berkelmans et al. 2004). In-water surveys conducted by the COTS Targeted Control Program were also collected for this analysis from the Eye on the Reef Program from 2016 and 2017 (RRRC and AMPTO 2016). Three RHIS surveys were conducted at each reef and followed the standard protocol for RHIS (Beeden et al. 2014), recording the percentage of bleached corals among the living coral cover in addition to records of coral cover, coral type and potential COTS presence, absence and damage. Bleached corals were categorised according to the GBRMPA Coral Bleaching Response Plan (GBRMPA 2011) among four RHIS Colony bleaching levels: (1) upper surfaces (2) Pale/Fluoro (3) Totally white (4) Recently dead. Data handling: All in-water bleaching observations were converted to align with the National Bleaching Taskforce aerial bleaching categories 0-4. For community level bleaching response transect and RHIS based observations were converted into a percentage (%) bleached of all corals counted from the survey method, which was then converted into the 5 category scale used by the aerial survey scores. The in-water and aerial bleaching observations to establish the relationship between total heat stress accumulation (DHW) and the overall coral community level bleaching response (% of living corals bleached) were combined. The in-water transect and RHIS were combined to provide estimates of the proportion of individual coral colonies that were severely bleached or recently dead. Further information can be found in the report: Cantin, N. E., Klein-Salas, E., Frade, P. (2021) Spatial variability in coral bleaching severity and mortality during the 2016 and 2017 Great Barrier Reef coral bleaching events. Report to the National Environmental Science Program. Reef and Rainforest Research Centre Limited, Cairns (64pp.). Format: GIS Spatial layers, Tif and KML files. Data Dictionary: GBR Community Bleaching Surveys - over the 2016-2017 time frame 0 (<1% bleached) 1 (1–10% bleached 2 (10–30% bleached ) 3 (30–60% bleached) 4 (>60% bleached) GBR: NOAA Coral Reef Watch – GBR Maximum Monthly Mean (MMM; raster) - Historical average maximum of the monthly mean temperatures for 1985-2012 climatology (v3.1) from annual sea surface Temperature anomalies. Represents the upper thermal limit for each location. 25 °C 26 °C 27 °C 28 °C 29 °C 30 °C GBR: NOAA CRW – DHW max [2002, 1998, 2016, 2017] Maximum accumulation of Degree Heating Weeks for each bleaching year. The NOAA DHW product is a summation of temperature anomalies at least 1°C above the MMM value over a 12 week period, which generates a measure of thermal stress as a function of both the strength of the anomaly above the MMM and the duration of the heating event. The DHW max value used here is the maximum DHW value accumulated for each summer heat wave. 0 °C – weeks 2 °C – weeks 5 °C – weeks 8 °C – weeks 15 °C - weeks References: Beeden R, Turner M, Dryden J, Merida F, Goudkamp K, Malone C, Marshall Paul A, Birtles A, Maynard J (2014) Rapid survey protocol that provides dynamic information on reef condition to managers of the Great Barrier Reef. Environmental Monitoring and Assessment 186:8527-8540 Berkelmans R, Oliver JK (1999) Large-scale bleaching of corals on the Great Barrier Reef. Coral Reefs 18:55-60 Berkelmans R, De'ath G, Kininmonth S, Skirving W (2004) A comparison of the 1998 and 2002 coral bleaching events on the Great Barrier Reef: spatial correlation, patterns and predictions. Coral Reefs 23:74-83 Cantin, N. E., Klein-Salas, E., Frade, P. (2021) Spatial variability in coral bleaching severity and mortality during the 2016 and 2017 Great Barrier Reef coral bleaching events. Report to the National Environmental Science Program. Reef and Rainforest Research Centre Limited, Cairns (64pp.). Frade PR, Bongaerts P, Englebert N, Rogers A, Gonzalez-Rivero M, Hoegh-Guldberg O (2018) Deep reefs of the Great Barrier Reef offer limited thermal refuge during mass coral bleaching. Nature Communications 9:3447 GBRMPA (2011) Coral Bleaching Response Plan. Great Barrier Reef Marine Park Authority, Townsville Hughes TP, Kerry JT, Álvarez-Noriega M, Álvarez-Romero JG, Anderson KD, Baird AH, Babcock RC, Beger M, Bellwood DR, Berkelmans R, Bridge TC, Butler IR, Byrne M, Cantin NE, Comeau S, Connolly SR, Cumming GS, Dalton SJ, Diaz-Pulido G, Eakin CM, Figueira WF, Gilmour JP, Harrison HB, Heron SF, Hoey AS, Hobbs J-PA, Hoogenboom MO, Kennedy EV, Kuo C-y, Lough JM, Lowe RJ, Liu G, McCulloch MT, Malcolm HA, McWilliam MJ, Pandolfi JM, Pears RJ, Pratchett MS, Schoepf V, Simpson T, Skirving WJ, Sommer B, Torda G, Wachenfeld DR, Willis BL, Wilson SK (2017) Global warming and recurrent mass bleaching of corals. Nature 543:373-377 Data Location: This dataset is filed in the eAtlas enduring data repository at: data\nesp5\5.7_Bleaching-Assessment

  • Categories    

    The purpose of this study is to detect and quantify spatial and temporal changes in reef fish assemblages of the Great Barrier Reef (GBR). Between 1993 and 2005, reef fish assemblages of 46 reefs were monitored annually along permanent transects within a standard habitat using visual census. The selected intensive survey reefs are distributed across three positions of the continental shelf and among six sectors each representing one band of latitude. These reefs continue to be surveyed in odd years as part of the Long Term Monitoring Program (LTMP). The survey pattern changed in 2006 in response to the implementation of a new zoning plan for the GBR Marine Park in 2004. In order to assess the effects of re-zoning on the biodiversity of reefs, a different selection of reefs are surveyed in even years as part of the Representative Areas Program (RAP). Surveys are carried out for 28 pairs of reefs, with each pair comprising one reef which was re-zoned as a no-take area in 2004 and another nearby reef which remained open to fishing. The RAP survey reef pairs are distributed among four of the same sectors in the original LTMP survey design and two different sectors. The cross-shelf distribution of reefs differs, though, as inshore reefs were not included in the RAP sampling design. Fishes of 214 species are counted along the permanently marked transects. Larger mobile fishes (141 spp.) are counted in a 5m wide belt and damselfishes (73 spp.) are counted in a 1m wide belt. Total lengths of any coral trout species (Serranidae, Plectropomus spp.) recorded within transect belts have been estimated from 1996 onwards. Length estimates of other species within the Serranidae, Lethrinidae and Lutjanidae families have been recorded in RAP surveys since 2006. To demonstrate spatial variation in fish community assemblages of the GBR, spatial distributions of a number of relevant variables were mapped in Google Earth using the long term average. Monitoring data collected up until and including the 2008 field season are included. Spatial variation in species richness and in total fish abundance are displayed. Fish species have also been divided into trophic groups and the spatial variation in abundance of each group is mapped accordingly. As part of the Reef Atlas project (now the eAtlas) the fish observations were interpolated over the whole GBR by Glenn De'ath using Generalized Additive Models with a Quasipoisson fit. This produced a gridded version of the dataset and is available as a KML. Data units: Richness: number of species per transect Density: Number of fishes per transect Resource Constraints: Copyright remains with the data owner(s) References: - Cheal A, Wilson S, Emslie M, Dolman A, Sweatman H (2008) Responses of reef fish communities to coral declines on the Great Barrier Reef Marine Ecology - Progress Series 372:211-223 - Emslie M, Cheal A, Sweatman H, Delean S (2008) Recovery from disturbance of coral and reef fish communities on the Great Barrier Reef, Australia. Marine Ecology - Progress Series 371:177-190 - Sweatman H, Cheal A, Coleman N, Emslie M, Johns K, Jonker M, Miller I, Osborne K (2008) Long-term monitoring of the Great Barrier Reef. Australian Institute of Marine Science, Townsville 379

  • Categories    

    The purpose of this study was to quantify patterns in skeletal density, linear extension and calcification throughout the GBR based on the AIMS Coral Core Archive of 328 colonies of massive Porites from 69 reefs. Annual data for the three growth parameters, skeletal density, annual extension, and calcification rate (the product of skeletal density and annual extension) were obtained from each colony using standard x-ray and gamma densitometry techniques. The data set contains 16,472 annual records, with corals ranging 10 – 436 years in age, most of which were collected in two periods covering 1983 – 1992 and 2002 – 2005. The oldest colony dates back to 1672. As part of the Reef Atlas project (now the eAtlas) the calcification observations were interpolated over the whole GBR by Glenn De'ath using Generalized Additive Models. This produced a gridded version of the dataset and is available as a KML. For the original data contact Janice Lough. Data Units: Skeletal density: g / cm^3; Annual extension: cm / yr; Calcification: g / cm^2 / yr. References: - De'ath G, Lough JM, Fabricius KE (2009) Declining coral calcification on the Great Barrier Reef. Science 323: 116-119 - Cooper TF, De'ath G, Fabricius KE, Lough JM (2008). Declining coral calcification on the Great Barrier Reef. Global Change Biology 14: 529–538 - Lough JM, Barnes DJ (2000) Environmental controls on growth of the massive coral Porites. Journal of Experimental Marine Biology and Ecology 245: 225-243

  • Categories    

    Trajectories of decline have been observed in coral reefs throughout the Caribbean and Indo-Pacific region attributable to the synergistic effects of human-induced disturbances. Whilst direct and indirect evidence suggests that inshore reefs from the Great Barrier Reef (GBR) are showing signs of regional decline following European settlement in the mid 18th century, it has proven difficult to ascertain the link between anthropogenic disturbance and coral degradation on a regional scale. This is primarily due to the absence of detailed ecological baselines on the past condition of many of these reefs prior to the advent of long-term monitoring in the mid 1980’s. An understanding of the timing, frequency, duration and cause of mortality events in hard coral communities is necessary to help direct management efforts towards ameliorating potential impacts. Furthermore, assessing the spatial and temporal variability of changes in community structure before and after European settlement, will provide an invaluable management tool to overcome the ‘shifting baseline’ syndrome. By dating and mapping historical changes in coral communities of inshore reefs of the GBR, the purpose of this study is to provide a detailed baseline assessment on coral community structure and an accurate chronology on the history and nature of mortality events. Dead coral skeletons have been dated using the highly-precise (2? ± up to 1 year) thermal ionisation mass spectrometry (TIMS) uranium-series (U-series) dating method in order to determine 1) the timing of historical mortality in coral communities and massive Porites corals in the Palm Islands region (central Inshore GBR) and reefs adjacent to catchments in the southern GBR (Mackay region) and far northern GBR, 2) historical patterns of storm occurrence on the offshore GBR (One Tree and Heron Reefs), and 3) Holocene sea level changes from the inshore GBR (Magnetic Island). So far, more than 320 samples have been dated at the Radiogenic Isotope Facility, University of Queensland. Our results have revealed shifts in coral community structure and a loss of previously dominant Acropora corals in the early 20th century in the Palm Islands region. It is theorized that this loss may be attributable to the synergistic impacts of declining water quality and climatic related factors. Analysis of uplifted reef blocks from the offshore GBR reveals a period of high storm activity throughout the 19th & 20th centuries. Furthermore, U-series dating of fossil massive corals from Magnetic Island suggests that sea level was higher than present around 2200 to 7000 years ago during the Holocene. Overall, our results show that U-series dating and palaeoecological approaches can provide unique insight into the GBR’s past. Data Units: U-series age (AD) ± 2-sigma error References: - Yu K. F. and Zhao J. X. (2010) U-series dates of Great Barrier Reef corals suggest at least +0.7 m sea level ~7000 years ago. The Holocene 20, 1-8. - Zhao J. X., Neil D. T., Feng Y. X., Yu K. F., and Pandolfi J. M. (2009) High-precision U-series dating of very young cyclone-transported coral reef blocks from Heron and Wistari reefs, southern Great Barrier Reef, Australia. Quaternary International 195, 122-127. - Zhao J. X., Yu K. F., and Feng Y. X. (2009) High-precision 238U-234U-230Th disequilibrium dating of the recent past - a review. Quaternary Geochronology 4, 423–433.

  • Categories    

    The Biophysical Oceanography Group produces monthly oceanographic reports for the eastern Australian coast, including the Torres Strait, which summarise key environmental variables such as sea surface temperature (SST) and chlorophyll concentration. These variables are important indicators for coral reef ecosystems and other biological processes. This series of the reports covers from August 2011 - November 2014 The NERP Torres Strait/GBR environmental condition reports have been assembled from an array of satellite and in situ data, as well as selected bleaching and temperature forecast models. These reports identify the differences between the models and observed conditions, and include a brief analysis of the ocean-atmospheric current conditions, from Pacific basin to GBR scale. The NERP reports cover Northern and Southern GBR and includes: - A monthly composite of SST, SST anomaly, chlorophyll-a and chlorophyll-a anomaly derived from MODIS imagery and processed by the Biophysical Oceanography Group; - Great Barrier Reef SST Anomaly Forecast (POAMA-2); - NOAA Coral Reef Watch outlook; - In-situ temperature measurements by the Australian Institute of Marine Science (AIMS) for Lizard Island, Davies Reef, Heron Island, Hardy Reed, Myrmidon Reef and Orpheus Island; - NOAA Optimum Interpolation Sea Surface Temperature Analysis - OceanMaps 15m Depth-Average Currents - ENSO index Historic reports go back to 2009. Note: The eAtlas does not contain the source data used to generate these reports. Repository Location: These reports have been filed in the eAtlas enduring data repository at: data\NERP-TE\2.3_TS-coral-monitoring\TS_NERP-TE-2-3_UQ_Condition-reports

  • Categories    

    This project will determine the movement and habitat use of large predatory fishes such as sharks and coral trout in reef and coastal environments of the Great Barrier Reef. This project will employ acoustic monitoring technology in a series of inshore and offshore environments including coastal bays, inshore reefs and offshore reefs to monitor the presence and movements of predator species (elasmobranchs and teleosts). Mobile predators will be fitted with acoustic transmitters to define their presence and distribution, extent of movement and amount of connectivity between study locations (i.e., movement from bay to inshore reef, movement among reef platforms, etc.). Predator presence and movement will be integrated with habitat mapping and environmental monitoring data to identify factors that lead to changes in movement patterns and to define any preferred locations or conditions that can be targeted for conservation or management. Examination of use of habitats will provide information about the amount of time spent in various GBRMP zones and amount of movement among zones to assess the amount of protection provided under current management arrangements.

  • Categories    

    This dataset is the U-series data for Pelorus Island as described in Roff et al (2013) Palaeoecological evidence of a historical collapse of corals at Pelorus Island, inshore Great Barrier Reef, following European settlement. Proceedings of the Royal Society Series B 10.1098/rspb.2012.2100 Methods: We surveyed three leeward reef sites at Pelorus Island (figure 1). At each site, four belt transects (1 m width, 20 m length) were surveyed on SCUBA at 4–6 m depth. Surficial death assemblages were collected by hand on SCUBA at eight points (n = ?40 fragments per point) at random across a single 20 m transect at each site. From these collections, fragments of the dominant genus/growth form present in death assemblages were identified, and samples were selected for U-series dating haphazardly (i.e. with no bias for taphonomic state of fragments). Sample fragments were sectioned laterally, and a sub-sample (2–3 g) of skeleton was taken from the cleanest section (i.e. unaffected by internal bioerosion) in closest proximity to the growth margin. Approximately 1 g of carefully cleaned material from each sub-sample was used for thermal ionization mass spectrometry (TIMS) and multi-collector inductively coupled plasma mass spectrometer (MC-ICPMS) U-series dating (Roff et al 2013 for more information) Format of the data: The dataset comprises of U-Th data obtained using thermal ionisation mass spectrometry (TIMS) and multi-collector inductively coupled plasma mass spectrometry (MC ICP-MS). Data is presented in a table in a word file (<Roff et al. 2013. U-series dates>) with values for uranium concentration (U ppm), 232Th concentration (ppb), measured 230Th/232Th (activity ratio), 230Th/238U (activity ratio), ?234U (activity ratio), uncorrected and corrected 230Th age (in years), time of chemistry (years AD) and corrected 230Th age (years AD). References: Roff et al (2013) Palaeoecological evidence of a historical collapse of corals at Pelorus Island, inshore Great Barrier Reef, following European settlement. Proceedings of the Royal Society Series B 10.1098/rspb.2012.2100 Data Location: This dataset is filed in the eAtlas enduring data repository at: data\NERP-TE\1.3_Coral-cores

  • Categories    

    This is data associated with MTSRF Task 4.8.4s, a MTSRF supported PhD project titled /Biology and ecology of the blacktip reef shark/. As part of this project, basic water quality data were collected during shark tagging trips at the study site - Cockle Bay Reef at Magnetic Island. The meta data regarding these shark catch and tagging trips are recorded in a separate data file. Basic water quality of Cockle Bay was measured at weekly to monthly intervals with handheld instruments - a YSI water quality meter (temp, salinity, condutivity, dissolved oxygen), and secchi disk depth. Data units: * Temperature - Degrees celcuis * Salinity - ppt * Conductivity - ms * Dissolved oxygen - mg/l and % saturation * Secchi depth - cm

  • Categories    

    The aim of this component of the Reef Rescue Monitoring Program is to assess trends in the concentrations of specific herbicides and pesticides, primarily through routine monitoring at sites (Green Island, Low Isles, Fitzroy Island, Normanby Island, Dunk Island, Orpheus Island, Magnetic Island, Cape Cleveland, Pioneer Bay, Outer Whitsunday, Sarina Inlet, North Keppel Island) within 20km of the Queensland coast. The monitoring year for routine pesticide sampling is from May to April. The year is arbitrarily divided into “Dry Season” (May to October) and “Wet Season” (November– April) sampling periods for reporting purposes. Within each dry season, samplers are typically deployed for two months (maximum of three monitoring periods) and within each wet season, samplers are typically deployed for one month (maximum of six monitoring periods). The maximum number of samples which should be obtained from each location within each monitoring year is nine. Exposure to chemicals in the water is assessed with passive samplers. Passive samplers accumulate organic chemicals such as pesticides and herbicides from water until equilibrium is established between the concentration in water (CW ng.L-1) and the concentration in the sampler (CS ng.g-1). The concentration of the chemical in the water is estimated from calibration data obtained under controlled laboratory conditions (Booij et al., 2007). This calibration data consists of either sampling rates (RS L.day-1) for chemicals which are expected to be in the time-integrated sampling phase or sampler-water equilibrium partition coefficients (KSW L.g-1) for chemicals which are expected to be in the equilibrium sampling phase. Different types of organic chemicals need to be targeted using different passive sampling phases. The passive sampling techniques which are utilized in the MMP include: SDB-RPS Empore™ Disk (ED) based passive samplers for relatively hydrophilic organic chemicals with relatively low octanol-water partition coefficients (logKOW) such as the Photosystem II (PSII) herbicides (example: diuron). Polydimethylsiloxane (PDMS) and Semipermeable Membrane Devices (SPMDs) passive samplers for organic chemicals which are relatively more hydrophobic (higher log KOW) such as chlorpyrifos. The list of target chemicals was determined based on the following criteria: pesticides detected in recent studies, those recognised as a potential risk, analytical affordability, pesticides within the current analytical capabilities of Queensland Health Forensic and Scientific Services (QHFSS) and those likely to be accumulated within one of the passive sampling techniques (i.e. that exist as neutral species and are not too polar). Target Chemicals Bifenthrin, Fenvalerate (Pyrethroid, insecticides), Bromacilb , Tebuthiuron, Terbutrync, Flumeturon, Ametryn, Prometryn, Atrazine, Propazine, Simazine, Hexazinone, Diuron (PSII herbicides), Desethylatrazine, Desisopropylatrazine (PSII herbicide breakdown products (also active)), Oxadiazon Oxadiazolone (herbicide), Chlorfenvinphos , Chlorpyrifos, Diazinon, Fenamiphos, Prothiophos (Organophosphate insecticide), Chlordane, DDT, Dieldrin , Endosulphan, Heptachlor, Lindane (Organochlorine insecticides), Hexachlorobenzene (Organochlorine fungicide), Imidacloprid (Nicotinoid insecticide), Trifluralin (Dintiroaniline), Pendimethalin (Dinitroaniline herbicide), Propiconazole, Tebuconazole, (Conazole fungicides) Metolachlor (Chloracetanilide herbicide) Propoxur (Carbamate insecticide) PSII herbicides (ametryn, atrazine, diuron, hexazinone, flumeturon, prometryn, simazine and tebuthiuron and atrazine transformation products desethyl- and desiso-propyl – atrazine) sampled by the SDB-RPS ED samplers are also expressed as PSII herbicide equivalent concentrations (PSII-HEq) and are assessed against a PSII-HEq Index (Kennedy et al. 2010) for reporting purposes. PSII-HEq values were derived using relative potency factors (REP) collated from relevant laboratory studies for each chemical with respect to a reference PSII herbicide diuron (Jones and Kerswell, 2003; Mueller et al. 2008; Bengston-Nash et al 2005; Schmidt, 2005; Macova et al unpublished). If a given PSII herbicide is as potent as diuron, it will have a REP of 1. If it is more potent than diuron it will have a REP of >1, while if it is less potent than diuron it will have an REP of <1. Data Location: This dataset is saved in the eAtlas enduring data repository at: data\RRMMP\UQ_Mueller_Inshore-pesticides\GBR_RRMMP_UQ_Inshore-pesticides-2011

  • Categories    

    This dataset demonstrates the suitability of microsatellite markers to discriminate between species of coral trout (Plectropomus spp.) and identify parent-offspring relationships in natural populations. A total of 285 adult P. leopardus collected from the Capricorn Bunkers and 285 adult P. maculatus from the Keppel islands were genotyped at 25 microsatellite loci. Each locus was also tested on 7 additional species within the genus. The multiplex PCRs developed here provide a reliable and cost-effective strategy to investigate the evolutionary and ecological dynamics of coral trout. Microsatellite loci are commonly used in ecology to measure genetic variability within and among populations. Their high allelic diversity and relative ease of development also make them ideal for individual genotyping to assist in species identification, to uniquely identify individuals and to infer phylogenetic or genealogical relationships. In the marine environment, these genetic tools may be the only means to measure important ecological processes such as larval dispersal, adult migrations and reproductive success. However, applying these methods accurately can require numerous, highly polymorphic markers and optimised PCR multiplexes can maximise the cost-effectiveness of using microsatellites. Methods: Microsatellite loci were identified from a microsatellite-enriched cloning library developed for P. maculatus and 454 pyrosequencing libraries for both P. leopardus and P. maculatus. The isolation of microsatellite loci, their integration to multiplex PCR and suitability for species discrimination can be found in Harrison et al. (2014). Limitations: This datasets is intended for the purpose of describing the suitability of microsatellite markers for species discrimination and parentage analysis in P. leopardus and P. maculatus. Format: Excel file includes: 1. Microsatellite data - Individual identifier - Species name - 25 codominant microsatellite loci 2. Description of 25 microsatellite loci - Locus name - Forward primer sequence - Reverse primer sequence - Genbank digital repository accession number - Library microsatellite were isolated from - PCR multiplex dye label - Repeat motif - PCR reaction concentration - Size range 3. Locus characteristics for P. leopardus and P. maculatus - Locus name - Number of alleles per locus - Observed heterozygosity - Expected heterozygosity - Hardy-Weinberg equilibrium - Probability of exclusion - Cumulative probability of exclusion 4. Locus transferability inPlectropomus spp. - Locus name - Number of samples tested - Number of observed alleles - Size range References: Harrison HB, Feldheim KA, Jones GP, Ma K, Mansour H, Perumal S, Williamson DH and Berumen ML (2014). Validation of microsatellite multiplexes for parentage analysis and species discrimination in two hybridizing species of coral reef fish (Plectropomus spp., Serranidae”. Ecology and Evolution, DOI: 10.1002/ece3.1002