This collection consists of a series of data sets assessing the sensitivity of 1-week-old (aposymbiotic) and 2-month-old (symbiotic) recruits of the coral Acropora millepora to the dissolved fraction of a commonly used heavy fuel oil under two light conditions: visible light in the absence of ultraviolet radiation and visible light in the presence of ultraviolet radiation. Data was collected on the sensitivity of recruit survival, growth, algal symbiont uptake, tissue colour, maximum quantum yield as well as latent survival and growth through laboratory experiments performed at the Australian Institute of Marine Science Townsville site following the December mass coral spawning event in 2017. The data was analysed using Bayesian dose-response modelling using the package bayesnec in the software R. For full methodological and analytical details please refer to the full research report, Nordbord et al. (2022) its supplementary materials and the associated GitHub repository (https://github.com/MNordborg/Nordborg-et-al.-2022-Recruit-HFO). Photographs collected before, during and after exposure of 1-week-old aposymbiotic recruits of the coral Acropora millepora as well as before, during and after exposure of 2-month-old (symbiotic) recruits of the coral Acropora millepora are available on request.

This collection consists of a series of data sets assessing the sensitivity of planula larvae of the coral Acropora millepora to dissolved, individual aromatic compounds under two light conditions: visible light in the absence of ultraviolet radiation and visible light in the presence of ultraviolet radiation. Data was collected on the sensitivity of larval survival, larval fragmentation and larval metamorphosis success through laboratory experiments performed at the Australian Institute of Marine Science Townsville site during the mass coral spawning events in November and December of 2016-2019. The data was analysed using Bayesian dose-response modelling using the package bayesnec in the software R. Parameters in this study: Larval survival, Larval fragmentation, Larval metamorphosis success For full methodological and analytical details please refer to the full research report: Nordborg et al. 2023, Effects of aromatic hydrocarbons and evaluation of oil toxicity modelling for larvae of a tropical coral (Marine Pollution Bulletin, Vol. 196, 115610, https://doi.org/10.1016/j.marpolbul.2023.115610) and its supplementary materials.

This dataset shows the effects of three insecticides (diazinon, fipronil, imidacloprid) and two fungicides (chlorothalonil, propiconazole) on larval metamorphosis in the coral Acropora tenuis. These five pesticides have been detected in the Great Barrier Reef lagoon and/or catchments. Settlement assays were conducted in Nov-Dec 2016 and Nov 2017. The aim of this research is to add toxicity data for inclusion into water quality guidelines. In order to improve water quality guidelines and subsequent risk assessments for pesticides in tropical marine ecosystems, the current study investigated the effects of three insecticides (diazinon, fipronil, imidacloprid) and two fungicides (chlorothalonil and propiconazole) on larval settlement and metamorphosis of the common reef-building coral Acropora tenuis larvae following 48 h exposures. Concentration-response curves were plotted to estimate no effect concentration (NEC) and effect concentration (ECx) values that inhibited larval settlement by 10% and 50% (EC10 and EC50, respectively). NEC is the concentration below which the pesticides are not expected to cause a reduction in larval metamorphosis. Methods: Gravid colonies (25-40 cm diameter) of the coral Acropora tenuis (Dana, 1846) were collected from 4 – 8 m depth in November 2016 from Trunk Reef (18°18.2’ S, 146°52.2’ E) and in November 2017 from Falcon Island (18°46’ S, 146°32’ E), GBR under Great Barrier Reef Marine Park Authority Permit G12/35236.1. Colonies were transported to the National Sea Simulator at the Australian Institute of Marine Science (AIMS) in Townsville and maintained in 1700 l flow-through holding tanks until spawning. Temperatures were held at 26-27°C, which was equivalent to the water temperature at the collection site. Gametes were collected from 8 parental colonies on each occasion, fertilised and symbiont-free larvae were cultured at approximately 500 larvae L-1 in 500 L flow-through tanks (Negri and Heyward, 2001, Nordborg et al., 2018). Larvae were competent to settle after 5 d and we used 7-10-day old A. tenuis larvae, each 800-1000 µm in length for consistency in the pesticide exposure experiments. The five pesticides in this study were > 98% pure and purchased from Sigma-Aldrich (NSW, Australia). Stock solutions (5 mg l-1) of all pesticides were dissolved in dimethyl sulfoxide (DMSO, final concentration < 0.01% (v/v) in exposures) and prepared in milli-Q water. A. tenuis larvae were exposed to diazinon (2.62 – 638 µg l-1), fipronil (1.57 – 1144 µg l-1), imidacloprid (3.88 – 947 µg l-1), chlorothalonil (0.69 – 507 µg l-1) and propiconazole (8.42 – 2053 µg l-1). Pesticide analyses were done by The University of Queensland, Queensland Alliance for Environmental Health Sciences (QAEHS), Woolloongabba, Australia. Static exposures were conducted in 20 mL glass scintillation vials containing 12-14 larvae made up to 10 mL filtered seawater (0.5 µm) with 6-7 concentrations (per pesticide) and 6 replicate vials per concentration. All tests included solvent controls containing identical concentrations of DMSO carrier. Seawater and solvent carrier controls were run in 12-18 replicate vials. Copper (CuCl2) was used as a reference toxicant at 6 concentrations between 1.12 – 36 µg L-1 and 6 replicate vials per concentration. Glass vials were transferred in random positions within a refrigerated shaking incubator (TLM-530, Thermoline Scientific) at 70 RPM to maintain gentle water movement which prevents larvae from attaching and undergoing metamorphosis in the containers (Negri et al., 2016). Larvae were exposed under a light intensity of approximately 60 µmol photons m-2 s-1 (12:12 h L:D cycle) and at 26.7 ± 0.7 °C (range). Vials were re-randomised at 24 h. After 48 h exposure larvae and treatment water were transferred into 6-well polystyrene culture plates (Nunc, NY, USA) and returned to the incubator but without water movement. Metamorphosis was initiated by the addition of crustose coralline algae (CCA) extract

This dataset shows the effects of herbicides (detected in the Great Barrier Reef catchments) on the growth rates (from cell density data) and photosynthesis (effective quantum yield) on the free-living form of the dinoflagellate coral symbiont Cladocopium goreaui during laboratory experiments conducted from 2017-2019. The aims of this project were to develop and implement standard ecotoxicology protocols to determine the effects of Photosystem II (PSII) and alternative herbicides on the growth and photosynthetic efficiency of the marine dinoflagellate Cladocopium goreaui. Bioassays were performed over 2-week exposures using herbicides that have been detected in the Great Barrier Reef catchment area (O'Brien et al., 2016). These toxicity data will enable improved assessment of the risks posed by PSII and alternative herbicides to coral endo-symbiotic algae for both regulatory purposes and for comparison with other taxa. Methods: A monoclonal strain of Cladocopium goreaui (formerly Symbiodinium clade C, (LaJeunesse et al., 2018) was isolated from the coral Acropora tenuis near Magnetic Island in Queensland, Australia (Australian Institute of Marine Science strain: SCF 055-01.10). Cultures were maintained in IMK media at 27 ± 1 °C and incubated at 14:10 h light:dark cycles under light intensity of 60-75 µmol m-2 s-1. C. goreaui cultures used for the bioassays were 14 days old and in the logarithmic growth phase. C. goreaui cells were transferred to 50 ml polypropylene tubes with IMK media to a final cell density of 1.7 -2.7 x 104 cells mL-1. Treatments were run with 3-6 replicates, including IMK media controls, solvent controls and a reference toxicant control (6 µg L-1 diuron). C. goreaui cells were exposed for 14 d and temperature maintained at approximately 27°C in a refrigerated incubator shaker. Cells were kept suspended with shaking at 130 rpm. Bioassays were conducted at similar conditions to the mother culture. Herbicide stock solutions were prepared using analytical grade products (Sigma-Aldrich 98-99.5% purity): diuron (CAS 330-54-1), metribuzin (CAS 21087-64-9), hexazinone (CAS 51235-04-2), tebuthiuron (CAS 34014-18-1), bromacil (CAS 314-40-9), propazine (CAS 139-40-2), simazine (122-34-9), imazapic (CAS 104098-48-8), haloxyfop-p-methyl (CAS 72619-32-0). Stock solutions (5 - 600 mg L-1) were prepared in Milli-Q® water or filtered seawater. Diuron and metribuzin were dissolved using the carrier solvent ethanol (final concentration < 0.002% v/v in all exposure treatments). Haloxyfop and simazine were dissolved in the carrier solvent dimethyl sulfoxide (DMSO; final concentration < 0.006% v/v in all exposure treatments). No solvent carrier was used for the preparation of the remaining herbicide stock solutions. Herbicide analysis was done at the Queensland Alliance for Environmental Health Sciences (QAEHS), The University of Queensland using HPLC-MS/MS (SCIEX Triple QuadTM 6500 QTRAP® mass spectrometer Shimadzu Nexera X2 uHPLC sytem) (Mercurio et al., 2015, Mercurio, 2016). Flow cytometry was used to quantify specific growth rates of C. goreaui using a BD Accuri C6 flow cytometer. Cell densities were determined by plotting a 2-dimensional cytogram with fixed gating. Gating of cells was used to differentiate between C. goreaui and degraded chloroplasts of senescing cells or microbes. Specific growth rate (SGR) was calculated as the logarithmic increase in cell density from day 0 to day 14. SGR relative to the control treatment was used to derive effect values for growth inhibition. Specific growth rates (SGR) were expressed as the logarithmic increase in cell density from day i (ti) to day j (tj) as per equation (1), where SGRi-j is the specific growth rate from time i to j; Xj is the cell density at day j and Xi is the cell density at day i (OECD, 2011). SGR i-j = [(ln Xj - ln Xi )/(tj - ti )] (day-1) (1) SGR relative to the control treatment was used to derive effect values for growth inhibition. Effects of herbicides on

The coral, Acropora millepora and the crustose coralline algae, Neogoniolithon fosliei were exposed to 3 photosystem II (PSII) herbicides (diuron, hexazinone and atrazine). Corals were collected at depths between 1 and 3m from Double Cone Island and Hayman Island in the Whitsunday group. The crustose coralline algae was collected from Davies Reef at depths between 5 and 7m.Experiments assessed the effects of the variables temperature (26, 30, 31, 32 °C) in combination with 3 herbicide concentrations, and exposure duration (up to 7 days) on photosynthetic efficiency and bleaching. To examine the effects of the herbicides diuron, atrazine and hexazinone in conjunction with increasing temperatures on coral and crustose coralline algae.

The U.S. Geological Survey (USGS) Coral Reef Ecosystems Studies (CREST) project (https://coastal.er.usgs.gov/crest/) provides science that helps Department of Interior and other resource managers tasked with the stewardship of coral reef resources. This data release contains data on coral physiology of the elkhorn coral, Acropora palmata, grown at five sites along the Florida outer reef tract including in Biscayne National Park, the Florida Keys National Marine Sanctuary, and Dry Tortugas National Park, from summer 2017 to autumn 2020. The data will be used to inform resource managers of the capacity for restoration and growth of this important, habitat-forming species of coral within U.S. waters. Some datasets included here were interpreted in Chapron and others (2023b). Chapron, L., Kuffner, I.B., Kemp, D.W., Hulver, A.M., Keister, E.F., Stathakopoulos, A., Bartlett, L.A., Lyons, E.O., and Grottoli, A.G., 2023, Heterotrophy, microbiome, and location effects on restoration efficacy of the threatened coral Acropora palmata: Communications Earth and Environment, vol. 4, art. 233, https://doi.org/10.1038/s43247-023-00888-1.

This dataset provides concentration-response data and associated general chemistry conditions for 32 experiments consisting of 177 toxicity tests regarding the acute toxicity of individual major ion salts and binary mixtures of major ions to Ceriodaphnia dubia; it also provides LC50 estimates and the estimated chemistries at the LC50 for each toxicity test. This dataset is associated with the following publication: Erickson, R., D. Mount, T. Highland, J. Hockett, D. Hoff, C. Jenson, T. Norberg-King, and B. Forsman. Acute Toxicity of Major Geochemical Ions to Fathead Minnows (Pimephales promelas). ENVIRONMENTAL TOXICOLOGY AND CHEMISTRY. Society of Environmental Toxicology and Chemistry, Pensacola, FL, USA, n/a - n/a, (2022).

Acropora cervicornis fragments of each genotype were evenly and haphazardly assigned to two nutrient treatments: ambient nutrients (Ambient) or elevated ammonium (NH4). Each nutrient treatment was replicated in four independent tanks (n = 3 fragments per genotype per tank). For ~1.5 months (47 d), Ambient tanks were maintained under nutrient levels consistent with the values in Virginia Key, FL, while elevated NH4 tanks were dosed with NH4Cl [3 mM] every 15 minutes using peristaltic pumps. The initial NH4 dose volume was 10 mL of the stock solution, targeting a ~10 μM increase in NH4 concentration. These values were calculated to account for the dilution of the nutrients resulting from adding new ambient seawater to the tanks (200 mL/min in a total tank volume of 180 L). After detecting higher than normal NH4 concentrations in the incoming seawater from Biscayne Bay, the NH4 dose volume was lowered to 5 mL of the stock solution, targeting ~5 μM NH4 increase above ambient values. The fragments were also assigned to disease vs. placebo treatments, the disease treatments involving exposure to homogenates of corals showing signs of white band disease following the protocol found in Rosales & Palacio-Castro (2024). Water samples (~40 mL) were collected to monitor NH4 levels in the treatments and immediately refrigerated at 4C. The elevated NH4 tanks were sampled daily, but the Ambient tanks were sampled less frequently (~2-3 days and no samples were collected during weeks 1 and 3 of the experiment). Nutrient concentrations were measured at NOAA-AOML using an AA3 nutrient analyzer (Seal Analytical, Southampton, UK). The instrument was calibrated before each run using standard solutions and procedures. Initially, only NH4 was monitored, but after high NH4 concentrations in the source seawater were detected, additional measurements of PO4 were included.