In the Florida Panhandle region, bottlenose dolphins (Tursiops truncatus) have been highly susceptible to large-scale unusual mortality events (UMEs) that may have been the result of exposure to blooms of the dinoflagellate Karenia brevis and its neurotoxin, brevetoxin (PbTx). Between 1999 and 2006, three bottlenose dolphin UMEs occurred in the Florida Panhandle region. The primary objective of this study was to determine if these mortality events were due to brevetoxicosis. Analysis of over 850 samples from 105 bottlenose dolphins and associated prey items were analyzed for algal toxins and have provided details on tissue distribution, pathways of trophic transfer, and spatial-temporal trends for each mortality event. In 1999/2000, 152 dolphins died following extensive K. brevis blooms and brevetoxin was detected in 52% of animals tested at concentrations up to 500 ng/g. In 2004, 105 bottlenose dolphins died in the absence of an identifiable K. brevis bloom; however, 100% of the tested animals were positive for brevetoxin at concentrations up to 29,126 ng/mL. Dolphin stomach contents frequently consisted of brevetoxin-contaminated menhaden. In addition, another potentially toxigenic algal species, Pseudo-nitzschia, was present and low levels of the neurotoxin domoic acid (DA) were detected in nearly all tested animals (89%). In 2005/2006, 90 bottlenose dolphins died that were initially coincident with high densities of K. brevis. Most (93%) of the tested animals were positive for brevetoxin at concentrations up to 2,724 ng/mL. No DA was detected in these animals despite the presence of an intense DA-producing Pseudo-nitzschia bloom. In contrast to the absence or very low levels of brevetoxins measured in live dolphins, and those stranding in the absence of a K. brevis bloom, these data, taken together with the absence of any other obvious pathology, provide strong evidence that brevetoxin was the causative agent involved in these bottlenose dolphin mortality events.
Citation: Twiner MJ, Flewelling LJ, Fire SE, Bowen-Stevens SR, Gaydos JK, Johnson CK, et al. (2012) Comparative Analysis of Three Brevetoxin-Associated Bottlenose Dolphin (Tursiops truncatus) Mortality Events in the Florida Panhandle Region (USA). PLoS ONE 7(8): e42974. https://doi.org/10.1371/journal.pone.0042974
Editor: Andreas Fahlman, Texas A&M University-Corpus Christi, United States of America
Received: April 25, 2012; Accepted: July 13, 2012; Published: August 15, 2012
This is an open-access article, free of all copyright, and may be freely reproduced, distributed, transmitted, modified, built upon, or otherwise used by anyone for any lawful purpose. The work is made available under the Creative Commons CC0 public domain dedication.
Funding: This work was supported by the National Oceanographic and Atmospheric Administration Marine Biotoxins Program, the state of Florida, and the National Oceanographic and Atmospheric Administration Center for Sponsored Coastal Ocean Research Harmful Algal Bloom Event Response Fund (2004). The funders had no role in study design, data collection and analysis, decision to publish, or preparation of the manuscript.
Competing interests: The authors have declared that no competing interests exist.
Harmful algal blooms (HABs) are commonly known for their detrimental impacts on aquatic organisms (including marine mammals), human health, and local economies –. Karenia brevis blooms, often referred to as “Florida red tide”, occur in the Gulf of Mexico (Florida, USA) on a nearly annual basis . This dinoflagellate produces a suite of neurotoxins known as brevetoxins (PbTxs or BTXs), which are heat-stable, lipid-soluble, polyether compounds –. The proximate mammalian pharmacological target of brevetoxin(s) is site 5 on the voltage-gated sodium channel , where it binds with high affinity (Kd 1–50 nM; ). Once bound, these toxins alter the voltage sensitivity of the channel by interfering with the voltage sensor and inactivation gate, ultimately resulting in nerve inhibition , .
Human health effects from brevetoxins generally result from neurotoxic shellfish poisoning (NSP)  and/or respiratory illness caused by inhalation of aerosolized toxin . The former can occur following consumption of contaminated shellfish that have accumulated sufficient levels of toxin while filter feeding the algal assemblage including K. brevis. NSP typically affects the nervous and gastrointestinal systems; however, all symptoms are reversible and to date there have been no human associated deaths , . Humans can also be exposed to aerosolized brevetoxins after the fragile, unarmored K. brevis cells lyse due to wave action, releasing toxins into the air  and causing irritation and burning of the throat and upper respiratory tract  following inhalation. In addition to brevetoxins acting as potent ichthyotoxins , Bossart et al.  observed brevetoxin immunoreactivity in the lung, liver, and lymphoid tissues of manatees collected during a 1996 mortality event, suggesting that brevetoxins can be absorbed by mammals via the inhalation of aerosolized toxins , .
Although a comprehensive understanding of brevetoxin trophic transfer is lacking, it is clear that finfish – and certain types of seagrasses (i.e., Thalassia testudinum) can accumulate or vector brevetoxins and play a primary role in brevetoxin-induced marine mammal mortality events or strandings , . If the mortality event is deemed “a stranding that is unexpected; involves a significant die-off of any marine mammal population; and demands immediate response”, it may be declared an unusual mortality event (UME) under the authority of the Marine Mammal Protection Act (www.nmfs.noaa.gov/pr/laws/mmpa/). Historically, bottlenose dolphin (Tursiops truncatus) mass mortality events in the Gulf of Mexico have long been thought to be associated with K. brevis , with the first documented incident of dolphin mortalities occurring simultaneously with an 8-month long bloom in southwest Florida that began in November 1946 . However, at that time linking the deaths to the K. brevis bloom was not possible due to the fact that the relationship between K. brevis and brevetoxin had not been identified . Despite all of the advances since this time, the mechanisms that lead to marine mammal death as a result of brevetoxicosis remain unresolved. Given that experimentation on protected species is prohibited, a level that constitutes a lethal dose of brevetoxin for a marine mammal may never be definitively known.
Another HAB toxin found in the Gulf of Mexico is domoic acid (DA), which is produced by members of the diatom genus Pseudo-nitzschia. DA is a neurotoxin that can cause amnesic shellfish poisoning (ASP) in humans  and large-scale mortality of sea birds , pinnipeds , , and cetaceans . DA is an analog of the neurotransmitter glutamate and a partial agonist that binds with high affinity to kainate receptors and intermediate affinity to α-amino-3-hydroxyl-5-methyl-4-isoxazole-propionate glutamate receptor subunits . Trophic transfer of DA via zooplankton into higher organisms has been well documented in krill , shellfish , sand crabs , and fish . In the Texas region of the Gulf of Mexico, DA was first reported in phytoplankton in 1989  with Nitzschia pungens f. multiseries (syn. P. multiseries) identified as the putative producer of DA , . A consortium of Pseudo-nitzschia species was subsequently identified (P. pseudodelicatissima, P. delicatissima, P. multiseries, P. pungens, P. subfraudulenta) in nearby Louisiana coastal waters . The most dominant species, P. pseudodelicatissima, was shown to produce DA in situ  and in culture  at levels that are not unlike Pseudo-nitzschia isolates found in other coastal regions susceptible to DA-related UMEs and/or ASP events. A region documented to have relatively high numbers of Pseudo-nitzschia spp. has been identified in the northern Gulf of Mexico, near coastal Louisiana, near Mobile Bay, Alabama, and near Perdido Bay, Florida, that appears to be highly influenced by high nutrient, submarine waters .
As top predators, bottlenose dolphins are considered sentinels for ecosystem health ,  and studies examining the health of coastal dolphin populations have suggested pathways for transport of brevetoxin through the marine food web. One long-term study of a population in Sarasota Bay, Florida  has shown that a major route of exposure to brevetoxin for bottlenose dolphins appears to be consumption of finfish such as pinfish (Lagodon rhomboides), pigfish (Orthopristis chrysoptera), striped mullet (Mugil cephalus), and spot (Leiostomus xanthurus) , , which are among the primary prey items for bottlenose dolphins in the Sarasota Bay region , . These dolphins and their prey items are both known to heavily utilize seagrass habitats within the bay, and the dolphins' home ranges and dietary analysis indicate that they are year-round, permanent residents of the inshore bay system and up to 1 km offshore , . Although K. brevis blooms have been shown to affect fish population diversity and community structure , , detectable levels of brevetoxin have been identified in shellfish and finfish for up to one year following a K. brevis bloom , , , although the absence of cells at bloom concentrations does not necessarily infer the absence of brevetoxin in the system . In contrast to studies involving brevetoxin, there have been few studies examining the presence or effects of DA or DA-producing Pseudo-nitzschia species on the bottlenose dolphin population in Sarasota Bay. Nonetheless, a recent study in this population illustrated the chronic exposure and accumulation of DA (concurrent with brevetoxin) in bottlenose dolphins . These exposures appear to correlate with indices of immunomodulation.
Although red tides are almost annual along the central west coast of Florida, bloom events in the Florida Panhandle region of the Gulf of Mexico are less common . From the late 1990s, two red tide events in this region coincided with two bottlenose dolphin UMEs, while in 2004 another bottlenose dolphin UME was not obviously associated with a concurrent red tide bloom. The primary objective of this study therefore was to assess and compare these three distinct bottlenose dolphin UMEs that were putatively associated with brevetoxin and the Florida red tide in 1999/2000, 2004, and 2005/2006. In total, over 850 samples from 105 bottlenose dolphins were analyzed for algal toxins using various detection strategies. For the first time, these data have been used to determine the routes of trophic transfer, extent of exposure and accumulation, and toxin distribution in a protected marine mammal species and its prey from exposure to two lethal algal toxins.
Materials and Methods
2.1 Water collections and cell count data
Before the unusual dolphin mortality of 2004, HAB sampling in the Florida Panhandle was not routine and was mainly initiated in response to discolored water, fish kills, or aquatic animal strandings or mortalities. Since 2004 routine HAB monitoring and HAB research efforts in this region have increased. K. brevis and Pseudo-nitzschia spp. cell counts reported here were obtained from FWC-FWRI's Harmful Algal Bloom database, which contains statewide HAB data collected for monitoring, research, and event response. The samples were collected by staff from multiple state agencies as well as volunteer members of the FWRI Red Tide Offshore Monitoring Program and local non-profit organizations. FWC-FWRI HAB staff utilized standard protocols for sampling, identifying, and counting HAB species , . The detection limit (dl) for each species was 333 cells/L. In a subset of samples, particulate and dissolved brevetoxins in water were analyzed according the methods described by Pierce et al.  and Twiner et al. .
2.2 Stranding data
Level A stranding data associated with dead bottlenose dolphins were collected on location and during post-mortem examinations. Data included geographical location, species identification, gender, estimated length-determined age class, and carcass condition code (ranging from 1 to 5 with 1 live and 5 severely decomposed). In the absence of tooth growth layer data for aging, animal length has been used as proxy for age class and is based on the following scale: neonates included total length up to 137 cm, yearlings were 138–186 cm, juveniles were 187–227 cm, subadults were 228–247 cm, and adults were 248 cm or longer , . Due to concerns over carcass decomposition, only code 1–3 animals (code 1 = live, code 2 = fresh dead, code 3 = mild decomposition) were subject to algal toxin analysis.
2.3 Bottlenose dolphin carcass and tissue collections
Samples for histopathology, toxicology and other ancillary tests such as microbiology and virology were collected from stranded bottlenose dolphins by members of the Southeast Marine Mammal Stranding Network during all three UMEs along the Florida Panhandle (Figure 1). Algal toxin sampling strategies evolved over this time frame. In 1999–2000, analyses focused on liver, kidney and spleen. However, subsequent to that investigation we found that the samples most useful for the rapid confirmation of algal toxin exposure in marine mammals are stomach contents, urine, and feces (unpublished data); therefore, in 2004 and 2005–2006 these samples were initially screened for the presence of brevetoxin and/or DA. Following the confirmation of either algal toxin, further analyses were carried out to gain insight into their tissue distribution in liver, kidney, spleen, blood, brain, and lung. In 2004 and 2005–2006 blood samples were also collected on blood spot cards  in cases where samples were sufficiently fresh that blood was not coagulated. Not all samples were collected from all animals, depending on body condition and the availability of field assistance. All samples were stored frozen at 20°C and shipped to toxin analysis laboratories at the NOAA Marine Biotoxins Program (Charleston, SC) and the Florida Fish and Wildlife Conservation Commission's Fish and Wildlife Research Institute (St. Petersburg, FL; 2004 and 2005–2006 only).
2.4 Prey item collections
Various fish species and crustaceans were collected from bottlenose dolphin stomach contents and by cast net in the study areas. Whole fish were identified, sorted according to species, weighed, and frozen at −20°C . Viscera (all organs in intracoelomic cavity), stomach contents, liver, and muscle, were dissected, weighed, and extracted for algal toxins. If the prey item was too small, it was analyzed whole.
2.5 Algal toxin analysis
Brevetoxins were the primary algal toxin class investigated based on the presence of K. brevis blooms concurrent with the mortality events (i.e., 1999/2000, 2005/2006)  or because of their known impacts of marine mammals in the region (i.e., 2004) , . For brevetoxin screening assays, we used a competitive enzyme-linked immunosorbent assay (ELISA), a receptor binding assay (RBA), or a radioimmunoassay (RIA). Many of the samples testing positive in one of the screening assays were confirmed by HPLC-tandem mass spectrometry (LC-MS/MS). In the 2004 and 2005/2006 UMEs, DA was also analyzed in the blood, urine, stomach contents, liver, kidney, lung, and muscle samples of stranded animals. An ELISA for DA was used as a rapid screen, followed by LC-MS/MS confirmation of DA on positive samples. Since many samples were analyzed using two or more independent methods, all data are presented as a mean of the independent analyses. The only exception are the data presented in Tables S1, S2, and S3.
2.5.1 Brevetoxin extraction.
Urine, gastric fluid, and liquid fecal samples were centrifuged at 13000×g for 10 minutes at 25°C, the supernatant was removed and filtered through a 0.45 µm syringe filter prior to analysis to remove particulates, and analyzed without solvent extraction. Solid samples (stomach contents, feces, liver, kidney, spleen, brain, lung) were homogenized and extracted in acetone four times (3 volumes or 3 mL minimum, depending on sample mass: typically 10 grams), filtered through a 0.45 µm syringe filter, dried under nitrogen gas, resuspended in 80% aqueous methanol (6 volumes or 30 mL), twice solvent partitioned with hexane (3 volumes or 30 mL), and the methanolic layer collected, dried under nitrogen gas and resuspended in 100% methanol (0.5 or 5 mL). Extracts were stored at −20°C until analysis. For some of the 2005/2006 samples, we used a modification of this method: 2 grams of sample were extracted twice in 9 mL 80% methanol, each time heated to 60°C for 20 min, combined and brought to 20 mL. An 8 mL aliquot of the extract was then washed with 10 mL hexane and the methanolic layer retained for analysis.
Blood card samples (100 µL blood) were extracted for brevetoxins using 0.8 mL of a phosphate buffered saline amended with (6%) methanol followed by adding 2.4 mL of acetonitrile to precipitate proteins. Samples were centrifuged at 4000×g for 15 min at 4°C and the supernatant was removed for analysis.
2.5.2 Brevetoxin analysis by receptor binding assay (RBA).
Clarified or extracted urine, feces, liver, gastric fluid, and stomach content samples were analyzed using a brevetoxin RBA. The RBA is a functional bioassay in which an unknown quantity of non-radiolabled brevetoxin (standards or samples) competes with radiolabeled brevetoxin (3H-PbTx-3; Amersham, NJ, USA) for the site 5 receptor of the voltage-gated sodium channel , . Data are expressed as PbTx-3 equivalents (equiv.), representing the toxic potency of the extract towards the pharmacological target relative to dihydrobrevetoxin-B (brevetoxin-3 or PbTx-3). Depending on the sample type, the detection limit (dl) ranged from 5–20 ng PbTx-3 equiv./g or /mL.
2.5.3 Brevetoxin analysis by enzyme-linked immunosorbent assay (ELISA).
The brevetoxin ELISA determines the presence of brevetoxins and brevetoxin metabolites based on cross-reactivity with an anti-brevetoxin polyclonal antibody (i.e., raised in sheep or goat). Two brevetoxin ELISAs were used within this study , . Both are direct competitive ELISAs performed in 96-well plate format where brevetoxin-3 was used as the standard. Depending on the sample type, the dl ranged from 2–8 ng PbTx-3 equiv./g or /mL.
2.5.4 Brevetoxin analysis by radioimmunoassay (RIA).
The brevetoxin RIA determines the presence of brevetoxins and brevetoxin metabolites based on a sheep antiserum prepared against a brevetoxin-2 conjugate , . The RIA measures the competition between radiolabeled brevetoxin-3 (3H-PbTx-3) and unknown samples for the anti-brevetoxin-2 antiserum. The dl of this assay was ∼5 ng PbTx per g (or mL) sample.
2.5.5 Brevetoxin analysis by liquid chromatography-mass spectrometry (LC-MS/MS).
LC-MS/MS methodologies underwent significant evolution over the course of the three UMEs assessed within this study. In 1999–2000, only one brevetoxin congener, brevetoxin-3, was analyzed. By 2004, the availability of additional standards and knowledge of structural information enabled the analysis of multiple metabolites.
For 1999–2000 samples, liquid chromatography was performed on a C18 column using an Agilent Technologies Model 1100 liquid chromatography (LC) system. Five µl of sample extract was separated using a gradient of 1–95% methanol in 0.1% trifluoroacetic acid at a flow rate of 0.2 mL/min. The eluent was introduced into an Applied Biosystems SCIEX API III triple quadrupole mass spectrometer, with an Atmospheric Pressure Chemical Ionization source operated in positive ion mode and nitrogen serving as the nebulization gas. The detection of brevetoxin-3 by mass spectrometry was achieved by multiple reaction monitoring (MRM) with a parent ion of m/z 897. Fragment ions characteristic of brevetoxin-3 were obtained at 725, 752, 769 and 807 Daltons. Quantification of brevetoxin-3 was carried out using the 725 Dalton fragment ion by comparison with a standard curve of brevetoxin-3 dilutions (0.1 ng/mL − 10 µg/mL).
For 2004 and 2005/2006 samples, liquid chromatography (LC) separations were performed on a Luna C8(2) 150×2 mm column using an Agilent Technologies Model 1100 LC system followed by mass spectrometry using an AB SCIEX 4000 QTRAP hybrid quadrupole/linear ion trap mass spectrometer equipped with a TurboVTM source interface. The detection and quantification of PbTx congeners by mass spectrometry was achieved by MRM and selected ion monitoring as previously described , –. In 2004, only brevetoxin-3 and -9 (tetrahydrobrevetoxin-B) were quantified with a dl of <1.0 ng/mL. In 2005/2006, brevetoxin-3 (B backbone) and brevetoxin-7 (A backbone; dihydrobrevetoxin-A) were quantified. Product ion spectra were used to identify, but not quantify, additional brevetoxin congeners.
2.5.6 Domoic acid extraction.
Stomach content and liver samples were extracted by adding four volumes of 50% aqueous methanol and homogenized. The homogenized samples and urine samples were centrifuged at 3000×g, and the supernatant passed through a 0.45 µm filter prior to analysis. Blood card samples were extracted for DA using a water (60%)/methanol (40%) solution (2.0 mL). Card extracts were sonicated and extracted for 12 h at 4°C. Extracts were dried under nitrogen gas and resuspended in 100 µL of 10 mM phosphate buffered saline amended with 0.05% Tween All extracts were stored at −20°C until analysis.
2.5.7 Domoic acid analysis by ELISA.
A direct competitive DA ELISA (Biosense Laboratories, Norway)  was used to screen the samples. This assay measures DA in a sample through its competition with DA coated onto microplate wells for anti-DA antibodies in solution. Extracts were diluted at least 1/20 with ELISA diluent prior to analysis. The dls were variable depending on the sample type and ranged from 0.1 ng/mL up to 60 ng/g.
2.5.8 Domoic acid analysis by LC-MS/MS.
Samples or extracts were analyzed for the presence of DA using tandem mass spectrometry coupled with liquid chromatographic separation (LC-MS/MS) using an Agilent 1100 LC coupled to an AB SCIEX API4000 triple quadrupole mass spectrometer in positive ion multiple reaction monitoring mode with methods previously outlined , . The DA fragments monitored were m/z 266, m/z 248, and m/z 193. The dl of this method was 1.0 ng DA/mL (urine and blood) and 4.0 ng DA/g (all other samples).
2.6 Statistical analysis
All documented T. truncatus strandings and K. brevis blooms from 1995 to 2006 in the seven Florida Panhandle counties were used to evaluate the temporal relationship between K. brevis blooms and T. truncatus strandings. Time series cross correlation statistics with month long time lags were used to examine the relationship between monthly bottlenose dolphin strandings and documented K. brevis bloom activity each month. To characterize the extent of K. brevis bloom in the area of dolphin strandings, the number of documented K. brevis reports and the highest K. brevis level each month were calculated for the region. Data from the March 2004 event when 105 dolphins stranded with signs of acute intoxication but K. brevis was not detected in local waters were excluded from the time series analysis. Statistical analyses were conducted using STATA SE 11.1 (StataCorp, College Station, TX, USA).
Results and Discussion
3.1 Florida Panhandle bottlenose dolphin strandings
In the Panhandle region of Florida (USA) (Figure 1) between 1996 and 2007, at least 543 bottlenose dolphins strandings were recorded, averaging 3.8±9.8 strandings per month (Figure 2). Within this region over the 11-year period, three bottlenose dolphin unusual mortality events (UMEs) have been declared by the Office of Protected Resources (NOAA Fisheries); August 1999 to May 2000, February to April 2004, and September 2005 to April 2006. For the 1999/2000 and 2005/2006 events, brevetoxin-producing K. brevis was concurrently present (see below), circumstantially suggesting that brevetoxin exposure may have been the cause of death.
3.2 1999/2000 Unusual Mortality Event
3.2.1 Harmful algae occurrence.
Between August 1999 and January 2000, high densities of K. brevis (up to 1.6×107 cells/L) were consistently observed in Panhandle bays (Figure 3) and coastal waters. Reports of fish kills to the FWC Fish Kill Hotline during this UME period reflect the observed bloom conditions. Between August 1999 and December 2000, the FWC Fish Kill Hotline received more than 50 reports of red tide-related fish kills in Panhandle (Franklin to Escambia counties). No reports were received between January and May 2000.
Cell count data (points) are individual measurements from within each Bay at various sites and depths. Stranding data (bars) are compiled based on monthly strandings per county (Apalachicola Bay = Franklin County, St. Joseph Bay = Gulf County, St. Andrew Bay = Bay County, and Choctawhatchee Bay = Okaloosa and Walton Counties).
Although the site of bloom initiation is unknown, blooms were initially observed in Apalachicola Bay and St. Joseph Bay before appearing in St. Andrew Bay and then Choctawhatchee Bay from October 1999 until January 2000. This bloom did not enter Pensacola Bay but elevated counts of K. brevis (up to 6.0×105 cells/L) were observed in the Pensacola Beach region in late September 1999. Seawater samples collected from St. Joseph Bay in late September 1999 had detectable brevetoxin concentrations in both the intracellular and extracellular fractions . These cell and toxin concentrations are not abnormally high relative to bloom concentrations frequently encountered on the southwest coast of Florida , where bottlenose dolphins are exposed to K. brevis red tides on an almost annual basis. An ECOHAB-FL cruise in the same near shore waters off Panama City during September 2000 documented similar toxin concentrations within a bloom patch , a time period during which there was no apparent increase in bottlenose dolphin mortalities. However, much less information about the extent and breadth of this bloom is available.
Over the 40-week 1999/2000 UME period, 152 bottlenose dolphins stranded in two temporally- and spatially-distinct peaks. Peak I from August to September 1999 primarily occurred in St. Joseph Bay whereas Peak II was from December 1999 until January 2000 and primarily occurred in Choctawhatchee Bay (Figure 3). Peak I mortalities began abruptly in St. Joseph Bay with 25 stranded animals in August 1999, 11 in September and 4 in October. Peak II mortalities in Choctawhatchee Bay were well above the historical average in October 1999 (n = 10), low in November (n = 1), followed by mass mortalities in December 1999 (n = 29) and January 2000 (n = 19). Over the course of this event, there were also a significant number of strandings (n = 15) in the Pensacola Bay region. Animals had no overt signs of infectious disease(s) and no consistent gross and histological findings . All stranded bottlenose dolphins tested (n = 68) were of the coastal morphotype according to mitochondrial DNA (P. Rosel, pers. comm.), had a sex ratio of 1∶1, and animals of length 201–239 cm were most common. Although K. brevis was continuously present for up to 6 weeks and occasionally exceeded densities of 105 cells/L in both St. Andrew Bay and Apalachicola Bay, very few strandings were observed in these areas (<5 per month). Spatial and temporal trends of bottlenose dolphin strandings and K. brevis densities can be viewed in Video S1. No blooms of Pseudo-nitzschia were observed in samples collected during this period. Most of the stranded animals were large and robust, but were severely decomposed (code 4 or 5), leaving few (n = 25) animals suitable for algal toxin analysis.
3.2.3 Algal toxin distribution.
Brevetoxin was detected in 52% (n = 25) of the animals tested. Liver (n = 23) and kidney (n = 11) composed the majority of samples, following the approach taken in the 1996 Florida manatee mortality investigation , with few stomach contents samples being collected. All 4 stomach contents samples analyzed were positive for brevetoxins by RBA and confirmed positive by LC-MS/MS, at concentrations up to >500 ng PbTx-3 equiv./g, strongly suggesting oral exposure. Seven of 22 liver samples and 4 of 11 kidney samples tested positive for brevetoxins, at concentrations up to 138 and 4.4 ng/g, respectively. Brevetoxin was not detected in spleen (n = 5) or lung (n = 10) samples. The distribution of brevetoxin in the various sample types (Figure 4) is similar to the tissue distribution seen in rats following an oral dose of brevetoxin  and in other brevetoxin-related marine mammal mortalities , . The observation that brevetoxin was highest in stomach and liver suggests that the primary route of exposure in bottlenose dolphins was by ingestion of contaminated prey.
Values are reported in ng brevetoxin-3 equiv./g. Data are median, quartile, and minimum/maximum values indicated by the midline, box, and whisker lines; respectively. Note: ‘na’ denotes samples were not available for analysis and “<dl” denotes below the detection limit. The number of animals analyzed for each sample type is represented by ‘n = ’.
Although limiting in total sample number, there appears to be some temporal trends of brevetoxin concentrations. Stomach contents positive for brevetoxin were from animals stranding in September 1999 and early January 2000 whereas positive liver samples were observed throughout the event (Table S1). Spatially, animals positive for brevetoxin stranded throughout most of the Panhandle coastline with the greatest number of animals available for toxin analysis stranding in the Choctawhatchee Bay area (n = 11; Figure 5). Of these animals, 5 tested positive for brevetoxin (45%). Although a higher proportion of animals were positive for brevetoxin in St. Joseph Bay (100%), this only constituted 2 animals. Out of the 15 animals that stranded in the Pensacola region, one was shown to contain brevetoxin (Figure 5). Although limited by the lack of sample number, no distinguishable trends were observed in toxin distributions between males and females and length-determined age class (data not shown).
The LC-MS analyses performed at the time were limited to just brevetoxin-3 and its backbone analogs. To investigate for the presence of other congeners and/or metabolites, liver and stomach extracts were fractionated by HPLC and column fractions were collected and tested for cross-reactivity with an anti-brevetoxin antibody using the method of Poli et al. . Fractionation and analysis were performed by Dr. Mark Poli (U.S. Army Medical Research Institute for Infectious Diseases). Brevetoxin-3 was predominant in the 4 stomach contents tested, which were made up primarily of partially digested fish. The presence of brevetoxin-3 in the stomach samples supports the hypothesis that these animals acquired toxin through oral exposure since brevetoxin-3 is the reduced form of brevetoxin-2 that is the predominant toxin analog produced by K. brevis . Ten of the 12 brevetoxin-positive livers examined by RIA contained only brevetoxin-3, while two samples had a peak that co-eluted with brevetoxin-2 (data not shown). The identity of this peak was not confirmed due to method limitations at the time, however, it may have represented a metabolite rather than brevetoxin-2, given its known rapid metabolism in other organisms .
3.2.4 Algal toxin trophic transfer.
At the time of this event, little was known about the capacity for live fish to vector brevetoxins to higher trophic levels, and no live fish were collected as a part of this UME investigation. However, a NOAA-funded ECOHAB research cruise to investigate (in part) fate and effects of K. brevis in the food web was coincidentally conducting surveys in the Panhandle region near the onset of this event. During the cruise in late September 1999, several live and apparently healthy Atlantic thread herring (Opisthonema oglinum, n = 19) were collected from alongshore of Miramar Beach near Choctawhatchee Bay and analyzed for brevetoxins using a novel detection method (micellar electrokinetic capillary chromatography with laser induced fluorescence detection ). K. brevis cell densities at the collection site were ranged from 1.2 to 3.0×106 cells/L. Brevetoxins were putatively detected, but not confirmed, at low levels in the stomach and GI tracts (n = 17), in the gills (n = 13), and in the liver (n = 4) . No toxin was detected in the muscle of any of the thread herring.
3.3 2004 Unusual Mortality Event
3.3.1 Harmful algae occurrence.
Satellite imagery of the northern Gulf of Mexico indicated elevated chlorophyll levels in the UME area from March 9 to 11, 2004, however, nearly all attempts to document K. brevis in the region were unsuccessful (Figure 6). Out of 235 total surface and sub-surface water samples collected only 2 samples were recorded as having low concentrations of K. brevis (1000 cells/L). These samples were from St. Joseph Bay and Choctawhatchee Bay on March 18 and March 31, respectively. Out of 82 near-shore and off-shore samples tested for brevetoxin, only 12 samples tested positive but at very low concentrations (<2 μg/L; data not shown). Coincidently, 9 of these samples were from St. Joseph Bay and suggest that a bloom may have been present before, possibly subsurface, in this bay and was just not observed. In contrast, Pseudo-nitzschia spp. cell counts in St. Joseph Bay were high between March 12 and March 25 with densities exceeding 105 cells/L in most samples (Figure 6). In the other three bays, Pseudo-nitzschia spp. cells were detected but at much lower densities. Unfortunately, Pseudo-nitzschia identifications were not made to species level and water samples for DA analysis were all negative (n = 14; unpublished data).
Cell count data (points) are individual measurements from within each Bay at various sites and depths. Stranding data (bars) are compiled based on 5 day total strandings per county (Apalachicola Bay = Franklin County, St. Joseph Bay = Gulf County, St. Andrew Bay = Bay County, and Choctawhatchee Bay = Okaloosa and Walton Counties).
Over a four week period starting March 10 and ending April 13, 2004 at least 105 bottlenose dolphins stranded in the Panhandle region with the majority of strandings occurring in St. Joseph Bay (70%, n = 71) and the proximate St. Andrew Bay (17%, n = 18) areas over the first 15 days (Figure 6). Specifically between March 10 and March 19, 55 bottlenose dolphins stranded in St. Joseph Bay resulting in a rapid response by the stranding network. Due to this rapid and massive response, the animal samples that were collected for analysis were of fair condition or better (code 2, 3, or 4) and no overt signs of the cause of death were observed. Stranded bottlenose dolphins had good nutritional status with no evidence of infectious disease(s) (i.e., morbillivirus negative) and no consistent gross and histological findings (pers. comm., D. Rotstein) . All stranded bottlenose dolphins tested (65) were of the coastal morphotype according to mitochrondrial DNA (P. Rosel, pers. comm.), had a sex ratio of 1∶1, and were mostly >240 cm in length. Stranding and cell count data for K. brevis and Pseudo-nitzschia spp. are spatially and temporally represented in Videos S2 and S3, respectively.
3.3.3 Algal toxin distribution.
Samples from 39 of the 107 bottlenose dolphins that stranded were collected for algal toxin analysis. All bottlenose dolphins tested had very high levels of brevetoxin in their stomach contents with mean ranges between 174 and 6235 ng PbTx-3 equiv./g (Figure 7; Table S2). The stomachs were unusually full of fish prey (mean stomach content weight 773 g) with 10 of 39 samples weighing >1000 g (maximum: 2258 g)  suggesting the bottlenose dolphins had just previously fed on and started digesting fish. In many cases, fish from stomach contents were identifiable and available for toxin analysis. Two stomach content samples from animals stranding March 10 and March 11, 2004 were tested using the NSP regulatory mouse bioassay  and found to be acutely toxic to mice at levels considered unsafe for humans (30–61 mouse units/100 g). Mean brevetoxin concentrations in gastric fluid ranged from <dl to 29126 ng PbTx-3 equiv./mL, feces (colon contents) from 47 to 1153 ng PbTx-3 equiv./g, and liver from <dl to 104 ng PbTx-3 equiv./g. Urine samples (n = 10) ranged from <dl to 143 ng/mL. Two of these urine samples were tested by LC/MS and confirmed positive for brevetoxin. Studies of brevetoxin metabolism in rats have shown that much of the toxin in urine to be in the form of cysteine-PbTx2 or the oxidized A-ring . Brevetoxin was also identified in all other sample types (kidney, blood, lung, cerebellum) except spleen (as determined by the RBA; Figure 7). The mean order of tissue brevetoxin concentrations (ng/g or ng/mL) were: gastric fluid (2697.3) ∼ stomach contents (2256.9) >> feces (633.0) >> liver (47.9) > urine (29.1) > kidney (18.1) > lung (16.8) > blood (7.2) > cerebellum (4.7) > spleen (<dl).
Values (mean calculations of all available assay data) are reported in ng brevetoxin-3 equiv./g or ng/mL. Data are median, quartile, and minimum/maximum values indicated by the midline, box, and whisker lines; respectively. Note: “<dl” denotes below the detection limit. The number of animals analyzed for each sample type is represented by ‘n = ’.
All animals tested (n = 39) for brevetoxin were positive with all but one (coastal west of St. Andrew Bay) of these animals stranding in St. Joseph Bay (Figure 8). The temporal variability in brevetoxin distribution appears to be unremarkable over the short duration of this event (Table S2) with toxin concentrations in each sample type remaining relatively constant in stranded animals from March 10 until March 27. In fact, of the primary samples analyzed and illustrated in Figure 7 (blood, feces, gastric fluid, liver, stomach contents, urine), only 6 samples were <dl for brevetoxin. Similarly, distinguishable differences were not observed in brevetoxin sample concentrations related to animal sex and age-class over time (data not shown).
Samples from nine bottlenose dolphins were also tested for DA (Table 1). In total, 89% (8 out of 9) of the tested animals were positive for DA. Although all tested liver, kidney, lung, and muscle samples were negative for DA (n = 20), the majority of blood, urine and stomach content samples (87%; 13 out of 15) were positive for low concentrations of DA (<10 ng/g or mL). This is not the first observation of marine mammal exposure to DA in the Gulf of Mexico as DA has been observed in live bottlenose dolphins in Sarasota Bay  and in St. Joseph Bay . Although in some cases DA correlated with eosinophilia and putative immunomodulation , it is important to note that these levels of DA are 1–2 orders of magnitude lower than the DA concentrations found in lethally poisoned California sea lions on the west coast . Initially it was hypothesized that this finding may help explain the enhanced sensitivity of Panhandle animals to brevetoxin versus Central West Florida animals, however data obtained shortly after the 2004 event using acute, single dose exposures did not suggest any synergistic effects between brevetoxin and DA on mouse lethality (data not shown) or on the cytotoxicity of neuroblastoma cells (Y. Bottein, pers. comm.).
3.3.4 Algal toxin trophic transfer.
Stomach content prey items were dominated by Clupeidae and Sciaenidae . Menhaden (Brevoortia sp.) was dominant in 14 of 28 (50%) animals examined, sciaenids (i.e., spot, silver perch, kingfish) were dominant in 11 (39%), and mixed taxa including shrimp in the remainder. Several intact or only slightly-digested prey items retrieved from the stomach contents of 19 bottlenose dolphins were analyzed for algal toxins that included fish identified as menhaden (Brevoortia sp.), silver perch (Bairdiella chrysoura), spot (Leiostomus xanthurus), pinfish (Lagodon rhomboides), kingfish (Menticirrhus sp.), puffer (species unknown), and unidentified teleosts . In many cases the whole fish was homogenized and extracted. All prey items contained high concentrations of brevetoxins with the highest levels measured in the menhaden (Table 2). Whole menhaden (n = 11) ranged from 844 to 15,361 ng PbTx-3 equiv./g and averaged 3,903 ng PbTx-3 equiv./g. Menhaden viscera analyzed separately (n = 3) contained an average concentration of 23,351 ng PbTx-3 equiv./g, and brevetoxins in menhaden muscle averaged 424 ng PbTx-3 equiv./g (n = 6). The importance of menhaden acting as vectors for brevetoxin transfer and for their role in marine mammal brevetoxicosis has been reported previously , . Spot and pinfish are also known vectors of brevetoxin into bottlenose dolphins  and in this event contained significant levels (181–2048 ng PbTx-3 equiv./g).
Live fish species (66 fish total) caught in the St. Joseph Bay area between March and May, 2004 were analyzed for brevetoxins. Some of these data were previously reported and similarly found that brevetoxins were detected in all fish collected in March 2004 during the UME (Table 3) , . Among the March 2004 fish results reported here (n = 12), highest concentrations were measured in the muscle (414 ng PbTx-3 equiv./g.) and stomach contents (3,955 ng PbTx-3 quiv./g) of a spotted seatrout (Cynoscion nebulosus). In general, concentrations were lower in fish collected in April 2004 (n = 50), but high concentrations were measured in the liver (mean = 2334 ng PbTx-3 equiv./g) and stomach contents (mean = 228 ng PbTx-3 equiv./g) of sheepshead (Archosargus probatocephalus). Similar concentrations were measured in the liver (mean = 2369 ng PbTx-3 equiv./g) and stomach contents (mean = 251 ng PbTx-3 equiv./g) of spotted seatrout from early May 2004 (n = 4). An undigested clupeid fish recovered from the stomach of one spotted seatrout contained brevetoxin concentrations of 376 and 9075 ng PbTx-3 equiv./g in the muscle and viscera, respectively. The viscera or whole fish of three species (burrfish, pinfish, and spot) were positive for brevetoxin, containing between 3985 and 7755 ng PbTx-3 equiv./g (Table 3).
3.4 2005/2006 Unusual Mortality Event
3.4.1 Harmful algae occurrence.
In early October 2005, high densities of K. brevis (up to 1.3×106 cells/L) were first observed in Apalachicola Bay and remained elevated until December. Similarly to the west in St. Andrews Bay, cell densities increased over the month of October before peaking at 3.5×106 cells/L in late October and early November and then rapidly declining in December. Over these same time periods, K. brevis was observed in Choctawhatchee Bay but at much lower cell densities (up to 2×105 cells/L). Cells were only briefly observed in St. Joseph Bay but reached as high as 2.5×106 cells/L, with maximum brevetoxin concentrations of >80 µg/L . An intense Pseudo-nitzschia diatom bloom (up to ∼5×106 cells/L) followed K. brevis in St. Joseph Bay, an area that often experiences large diatom blooms (FWC-FWRI's Harmful Algal Bloom database), and in Choctawhatchee Bay but not in the other two Bay systems. Of the water samples collected for DA analysis in St. Joseph Bay in September and November 2005 and March 2006, Pseudo-nitzschia spp. were only present at bloom levels (maximum of 7.3×105 cells/L) and DA at concentrations ranging from <dl to 0.7 µg/L in September 2005 (O Dea et al. in prep.).
Over the 29-week UME event between September 19, 2005 and April 30, 2006, 90 bottlenose dolphins stranded in the Panhandle region with the majority (56%) of these stranding occurring in Choctawhatchee Bay from November 2005 until April 2006 (Figure 9). While strandings were clearly elevated above historical levels from December 2005 to April 2006, there appears to be two peaks of stranded animals; the first peak during the presence of K. brevis and the second peak several months following the disappearance of K. brevis cells. Maximum strandings in St. Andrew Bay (n = 5) occurred during the bloom whereas maximum strandings in Apalachicola Bay (n = 6) occurred in March 2006, several months after the apparent bloom decline. These animals were generally of fresh to poor condition (code 2, 3, or 4) with some decomposition and no overt signs of the cause of death. They had good nutritional status with no evidence of infectious disease(s) and no consistent gross and histological findings (D. Rostein, pers. comm.). Most stranded bottlenose dolphins tested (62 of 64) were of the coastal morphotype according to mitochondrial DNA (P. Rosel, pers. comm.), had a sex ratio of 1∶1, and were mostly of the 201–240 cm length size class. Bottlenose dolphin stranding and algal cell count data for K. brevis and Pseudo-nitzschia spp. are spatially and temporally represented in Videos S4 and S5, respectively.
Cell count data (points) are individual measurements from within each Bay at various sites and depths. Stranding data (bars) are compiled based on monthly strandings per county (Apalachicola Bay = Franklin County, St. Joseph Bay = Gulf County, St. Andrew Bay = Bay County, and Choctawhatchee Bay = Okaloosa and Walton Counties).
3.4.3 Algal toxin distribution.
Samples from 41 of the 89 bottlenose dolphins that stranded were collected for algal toxin analysis (Figure 10). Stomach contents contained brevetoxin levels similar to gastric fluid (<dl to 2724 ng PbTx-3 equiv./mL) and liver samples contained brevetoxin at concentrations (<dl to 278 ng PbTx-3 eq./g) similar to the 1999/2000 UME events (<dl to 138 ng PbTx-3 equiv./g) and 2004 (<dl to 104 ng PbTx-3 equiv./g). Many of the blood samples tested positive for brevetoxin, as did kidney, lung, cerebellum, with the occasional blubber and muscle sample also positive. In contrast to the 2004 data, 5 out of 8 spleen samples from 2005/2006 were positive. However, this discrepancy may be a result of the different assays used between these two events, since the ELISA method used to analyze spleen samples in 2005/2006 is more sensitive than the RBA method used in 2004. Unlike the acute 2004 UME, many of the feces and urine samples from 2005/2006 tested negative suggesting different toxin elimination kinetics and likely exposure scenarios between these events. The mean order of tissue brevetoxin concentrations (ng/g or ng/mL) were: gastric fluid (508.6) ∼ stomach contents (351.6) >> liver (31.0) ∼ feces (21.7) > spleen (13.4) ∼ kidney (10.8) ∼ urine (7.6) ∼ blood (5.2) > lung (1.8).
Values (mean calculations of all available assay data) are reported in ng brevetoxin-3 equiv./g or ng/mL. Data are median, quartile, and minimum/maximum values indicated by the midline, box, and whisker lines; respectively. Note: The number of animals analyzed for each sample type is represented by ‘n = ’.
An interesting occurrence within this event was the recovery of 2 sets of mother – fetal pairs for algal toxin analysis that appear to represent unique scenarios. Data gathered via a rodent model has shown that pregnant mothers exposed to brevetoxin-3 can transfer this toxin to their fetuses via placental transport . In PCNMFS-06-07 mother, all samples (including amniotic fluid) were negative for brevetoxin with the exception of 9 ng PbTx-3 equiv./g in the liver (Table S3) suggesting a previous low dose or protracted exposure. Nonetheless, the stomach contents and liver collected from the fetus of PCNMFS-06-07 were negative for brevetoxin. The female FLCB030206-11 had at least one brevetoxin-positive shrimp in the stomach (780 ng PbTx-3 equiv./g), brevetoxin in the blood, liver, kidney, spleen, and amniotic fluid, but not in the gastric fluid, lungs, or muscle. However, no brevetoxin was found in the liver or feces of the fetus. Collectively, these data suggest that maternal transfer may be possible but firm conclusions cannot be made due to limitations in sample size.
Thirty-eight of the 41 tested animals (93%) were positive for brevetoxin with the majority of strandings occurring in Choctawhatchee Bay (Figure 11). Temporal variability in brevetoxin tissue/sample concentrations appears to be unremarkable over the duration of this event (Table S3) with toxin concentrations in each sample type remaining relatively constant in stranded animals from November 2005 until April 2006. Similarly, distinguishable differences were not observed in brevetoxin sample distributions related to animal sex and age-class over time (data not shown). However, a disproportionate number of dolphins with length ranges of 200–240 cm were analyzed relative to the higher number of dolphins in this length range that stranded.
After measuring low levels of DA in some 2004 UME bottlenose dolphin samples (<dl to 9 ng/g or ng/mL; Table 1), DA was assessed in bottlenose dolphin samples collected during the 2005/2006 event. Using ELISA, liver (n = 5), stomach contents (n = 5), and urine (n = 9) all tested negative for DA (data not shown). This absence of DA was not due to the absence of Pseudo-nitzschia spp. cells in the area since from December 2005 until April/May 2006 cell counts in St. Joseph Bay and Choctawhatchee Bay remained high and at times exceeded 106 cells/L (Figure 9). Furthermore, in September 2005 DA was identified in the area (O Dea et al. in prep.).
3.4.4 Algal toxin trophic transfer.
Most animals (20 of 27) had at least one food item in their stomachs that tested positive for brevetoxin (range <dl to 2034 ng PbTx-3 equiv./g; Table 4), however the concentrations tended to be several fold lower than concentrations observed during the 2004 UME (range 401 to 10080 ng PbTx-3 equiv./g) (Table 2)  but greater than the 1999 UME event (range 28 to 393 ng PbTx-3 equiv./g). Although limited in number due to advanced stages of digestion, stomach content analysis identified many small fish species including menhaden and spot that contained brevetoxin. In particular, spot have been found in greater abundance in dolphin stomachs during and shortly after blooms of K. brevis compared to dolphin stomach samples collected in the absence of bloom activity . For the first time, we also observed an abundance of shrimp in the stomach contents of these animals. Although highly variable, many of these shrimp also contained brevetoxin (<dl to 760 ng PbTx-3 equiv./g; Table 4), possibly representing an additional undocumented trophic route distinct from planktivorous fish. We found a high prevalence of brevetoxins in live fish collected during and immediately after the K. brevis bloom, with maximum concentrations reaching 414 ng PbTx-3 equiv./g in muscle and 4655 ng PbTx-3 equiv./g in liver (Table 3). In a 2-year follow-up study focused on St. Joseph Bay by Naar et al. , brevetoxins continued to be present in the livers of live fish for more than a year after the cessation of the bloom. A multispecies persistent fish kill in Choctawhatchee Bay from mid-January to May 2006, with juvenile spot being the most affected, correlated with high tissue concentrations of brevetoxins (up to 6438 ng PbTx-3 equiv./g in intestinal content), even in the apparent absence of K. brevis cells . These data support the role of brevetoxin trophic transfer in both acute mortalities during K. brevis blooms (i.e., Choctawhatchee Bay, December 2005), and the delayed or protracted impacts on bottlenose dolphins many months following a K. brevis bloom due to complex retention and distribution throughout the food web (i.e., Choctawhatchee Bay, March 2006) potentially contributing to spatial and temporal lags in animal exposures to toxins. Alternatively, the March 2006 elevation in strandings could have been the result of a K. brevis bloom that went undetected; not unlike what is speculated for the 2004 UME.
3.5 Correlations between Karenia brevis and bottlenose dolphin strandings
K. brevis was documented in one or more of the seven Florida panhandle counties 1945 times between June 1995 and December 2006, including 55 of the 144 months. During the same time period 567 bottlenose dolphin strandings were documented representing 101 of the 144 months. Dolphin strandings were marginally correlated with the number of K. brevis reports each month (Pearson cross correlation coefficient 0.16, P = 0.051). Strandings were significantly positively correlated with the number of K. brevis reports each month when the bloom data were time lagged so they preceded strandings by 1, 3, 4 and 5 months. The strongest positive correlations were detected when K. brevis bloom data preceded stranding data by 3, 4, and 5 months with cross correlation coefficients 0.272. 0.274, and 0.256, respectively (p<0.05). Bottlenose dolphin strandings were similarly correlated in time when K. brevis activity was measured using the highest K. brevis count reported for that month. While strandings and bloom level were not significantly correlated in real time (Pearson correlation coefficient 0.143, P = 0.086), highest monthly bloom level was highly correlated with strandings when bloom data preceded strandings by 1 month (Pearson correlation coefficient 0.345, P<0.05). As was noted for the other measure of local K. brevis activity, significant correlations were detected when data on highest monthly K. brevis count preceded strandings by 3, 4, and 5 months .
4.1 Algal toxin-related UMEs in Florida
According to the Marine Mammal Protection Act, the declaration of a UME is based on “a stranding that is unexpected, involves a significant die-off of any marine mammal population, and demands immediate response”. Between 1999 and 2006, there were three UMEs involving the mass mortality of bottlenose dolphins in the Florida Panhandle region. Although cursory circumstantial evidence had suggested the involvement of K. brevis, substantive toxin data confirming exposure to brevetoxins have not been forthcoming until now. Based on the analysis of 105 stranded animals and over 850 analytical or bioassay methods (i.e., ELISA, receptor binding assay, radioimmunoassay, LC-MS/MS) that have confirmed the presence of brevetoxin in 86% of the stranded animals tested, our data provide the first link between the deaths of Panhandle bottlenose dolphins and K. brevis and/or brevetoxins in each of the 1999/2000, 2004, and 2005/2006 mortality events.
An interesting discrepancy in the Gulf of Mexico is that documented K. brevis cell counts in the Panhandle region are no higher (and in many cases lower) than those typically and frequently observed during blooms along the Central West Florida region  with known exposures to local bottlenose dolphin populations ,  (Table 5), but yet the impacts on bottlenose dolphins and their contribution to mass mortalities are vastly different. Over the 1999–2006 study period, there were two known K. brevis bloom events (1999/2000 and 2005/2006) in the Panhandle region and each of these events coincided with major mortality events that were declared UMEs. However, during the same period in Central West Florida, there were major blooms nearly every year but only one UME bottlenose dolphin mortality event in 2005/2006 (Table 5). This difference in susceptibility could be due to the observation that Panhandle blooms have a tendency to become trapped in embayments such as St. Joseph Bay, thereby potentially increasing brevetoxin exposure periods and/or potentially higher accumulation in the prey base of the local trophic system. In addition, this study and a study involving live bottlenose dolphins also highlight the presence of another algal toxin, domoic acid (DA), that is present in Panhandle bottlenose dolphins . However, the levels of DA were very low when compared to stranded marine mammals on the west coast of North America  and DA has just recently been documented in live Sarasota Bay bottlenose dolphins that reside in the Central West Florida region . Another explanation for the sensitivity discrepancy between the Pandhandle and Central West Florida dolphin populations is that since K. brevis blooms are nearly annual events in Central West Florida, the resident bottlenose dolphins in these areas have become desensitized to the harmful effects of brevetoxin. Alternatively, the bottlenose dolphins residing in the Panhandle region are much more sensitive to the harmful effects of brevetoxin. This difference in susceptibility between the two regions does not appear to be due to population genetic differences related to morphotype. DNA analysis of the bottlenose dolphins affected by the two concurrent 2005/2006 UMEs determined that both populations were dominated by the coastal morphotype (P. Rosel, pers. comm.). Finally, differences in feeding habits between Panhandle and Central West Florida dolphin populations may be another factor in resolving this discrepancy. Sarasota Bay dolphins generally feed on solitary, seagrass-associated fish that are a mix of herbivores, carnivores, detritivores and omnivores , , whereas the 2004 Panhandle UME dolphins were intoxicated by feeding on menhaden, which are offshore, pelagic planktivores . The fact that dolphins from these two regions may be feeding at multiple trophic levels may result in differential brevetoxin exposure that cannot be resolved by simply comparing brevetoxin concentration ranges during UMEs. Despite the regional differences in sensitivity, it is quite clear that in both regions the presence of highly dense K. brevis blooms results in a higher percentage of animals exposed to brevetoxin, higher concentrations of brevetoxin in various tissues/fluids, and a greater chance for an UME (Table 5). This is particularly evident when compared to samples obtained during live dolphin health assessments in St. Joseph Bay and Sarasota Bay, FL during periods of low bloom activity (i.e., K. brevis cells counts <1000 cells/L) , .
4.2 Contributions to a case definition of brevetoxicosis for bottlenose dolphins
Data from the three distinct UMEs presented in this study will significantly contribute to a brevetoxicosis case definition for bottlenose dolphins, which has been identified as a priority need to better understand the acute and chronic impacts of brevetoxin exposure on individuals and populations of bottlenose dolphins . Criteria may include evidence of brevetoxin exposure via the detection of brevetoxin in the gastrointestinal compartment (i.e., stomach contents, gastric fluid, and/or feces) as well as evidence of brevetoxin uptake via the detection of brevetoxin in internal fluids (i.e., blood, urine) and/or tissues (liver, kidney, etc). However, specific threshold levels will be difficult to ascribe because of the various rates associated with distribution and/or metabolism specific to each compartment/fluid/tissue. As well, carcass condition and age presumably affects toxin levels, particularly degradation. Blooms of brevetoxin-producing K. brevis may or may not be present. Additionally, other causes of death should be ruled out, including physical injuries (i.e., ship strikes, natural predators, fishing gear entanglements), age, and exposure to pathogenic microbes (viruses and bacteria) and parasites. Exposure to other contaminants (i.e., organochlorines, metals, etc) should be at non-concerning levels. With these toxicological factors in mind, it seems appropriate that all three events presented in this study (1999/2000, 2004, and 2005/2006 UMEs) would be classified as events of brevetoxicosis.
4.3 Factors necessary for brevetoxin-induced UME
Although there are certainly differences between the three UMEs outlined in the current study, there are distinct commonalities that appear to precede a bottlenose dolphin UME in the Gulf of Mexico. First and foremost, whether it is possible to detect it or not, there must be a dense K. brevis bloom producing brevetoxin. K. brevis cells must then subsequently be consumed by planktivorous organisms such as fish (i.e., menhaden) or benthic organisms such as shrimp. These toxin-containing fish or invertebrates can be directly consumed by bottlenose dolphins or consumed by small piscivorous fish (i.e., seatrout), that biomagnify brevetoxin and can then be consumed by dolphins or alternately retain the toxin for as long as one year following their initial exposure –. The lag time between a K. brevis bloom and dolphin mortality is probably related to the degree of trophic transfer and toxin dispersal that occurs between the bloom and dolphin consumption of toxin-containing fish  and the feeding preferences of the dolphins. More direct transfer of toxin to dolphins likely results in dolphin mortality and stranding in conjunction with or closely following a bloom of K. brevis and was likely the case in St. Joseph Bay in 1999 and 2004 as well as in Choctawhatchee bay in 2005. Although much more difficult to ascertain, evidence within this study and others ,  suggest that there were alternate and more protracted (spatially and temporally) routes of trophic transfer that likely account for the significant time lag between a K. brevis bloom and the second peak of the 1999/2000 UME as well as the 2005/2006 dolphin stranding event. This alternate trophic route appears to have involved more demersal (i.e., benthic) fish species such as spot, pinfish, and kingfish that may accumulate brevetoxins from the sediments, seagrass, and/or benthic invertebrates .
4.4 Future directions
It is generally acknowledged that there is an apparent increase in the incidence and intensity of HABs ,  that potentially is influenced by natural and anthropogenic factors, including eutrophication  and global climate change . If this represents an actual increase in the frequency and duration of bloom events such as brevetoxin-producing K. brevis and DA-producing Pseudo-nitzschia spp., there will likely be a greater chance of concurrent and synergistic exposure of aquatic organisms such as fish and marine mammals to these types of HAB toxins resulting in mass mortality events . It is therefore imperative that future studies attempt to gain a better understanding of the ecological circumstances that result in algal toxin-related marine mammal exposure and mortality.
Dolphin strandings and K. brevis cell counts across space and time in the Florida Panhandle region, USA during the 1999/2000 UME event.
Dolphin strandings and K. brevis cell counts across space and time in the Florida Panhandle region, USA during the 2004 UME event.
Dolphin strandings and Pseudo-nitzschia spp. cell counts across space and time in the Florida Panhandle region, USA during the 2004 UME event.
Dolphin strandings and K. brevis cell counts across space and time in the Florida Panhandle region, USA during the 2005/2006 UME event.
Dolphin strandings and Pseudo-nitzschia spp. cell counts across space and time in the Florida Panhandle region, USA during the 2005/2006 UME event.
Brevetoxin concentrations in various tissues from stranded dolphins in the 1999/2000 UME. Values are reported in ng PbTx-3 equiv./g.
Brevetoxin concentrations in various tissues from stranded dolphins in the 2004 UME. Values are reported in ng PbTx-3 equiv./g or ng/mL.
In recognition of his dedication to marine mammal research, particularly the feeding ecology of bottlenose dolphins, the authors wish to dedicate this publication to Dr. Nélio B. Barros (23 January 1960 to 10 February 2010). For many of the authors on this paper, Nélio was a dear friend and colleague who passed along far too soon after a fierce battle with stomach cancer.
The authors wish to acknowledge the members of the Southeast Marine Mammal Stranding Network, who dedicated a tremendous amount of time and effort responding to these large-scale mortality events, and the large number of individuals and organizations who participated in various aspects of the investigations. Water samples included in this study were collected in response to the dolphin mortality events as well as for HAB monitoring and research by staff from the Florida Fish and Wildlife Conservation Commission (FWC), the Florida Department of Environmental Protection, Florida Department of Agriculture and Consumer Services, the Apalachicola National Estuarine Research Reserve, and volunteer members of the FWC-FWRI Red Tide Offshore Monitoring Program and the Choctawhatchee Bay Alliance. Karenia brevis and Pseudo-nitzschia identification and enumeration were performed by Dr. Earnest Truby and Jennifer Wolny (FWC-FWRI). Stranding data were queried from the NOAA National Marine Mammal Health and Stranding Response Database. The authors would like to thank Kathryn Evans Schneider, Leigh Davidson-DeHoll, Hannah Giddens, Karen Mao, Jen Maucher-Fuquay, and Seana Powers-Cherin (NOAA) and Karen Atwood and April Granholm (FWC-FWRI) for technical help;Jeff Adams and Dr. Laura Kracker for GIS help; Dr. Patricia Rosel (NOAA Fisheries) and the SEFSC Marine Mammal Molecular Genetics Lab for bottlenose dolphin morphotyping; Dr. John Schwacke (Medical University of South Carolina) for production of the video graphics; and Dr. Cynthia A. Heil, for providing K. brevis and Pseudo-nitzschia spp. cell count data.
Disclaimer: This publication does not constitute an endorsement of any commercial product or intend to be an opinion beyond scientific or other results obtained by the National Oceanic and Atmospheric Administration (NOAA). No reference shall be made to NOAA, or this publication furnished by NOAA, to any advertising or sales promotion which would indicate or imply that NOAA recommends or endorses any proprietary product mentioned herein, or which has as its purpose an interest to cause the advertised product to be used or purchased because of this publication.
Conceived and designed the experiments: MJT LJF SRB-S JHL TAL BM-G LS FMV TKR. Performed the experiments: MJT LJF SRB-S TAL BM-G ZW. Analyzed the data: MJT LJF SF SRB-S JKG CKJ TAL LS FMV ZW. Wrote the paper: MJT LJF SF.
- 1. Rossini GP, Hess P (2010) Phycotoxins: chemistry, mechanisms of action and shellfish poisoning. In: Luch A, editor. Molecular, Clinical and Environmental Toxicology: Birkhäuser Basel. 65–122.
- 2. Anderson DM, Hoagland P, Kaoru Y, White AW (2000) Estimated annual economic impacts from harmful algal blooms (HABs) in the United States. Woods Hole Oceanographic Institution Tech. Rept., WHOI-2000-11. WHOI-2000-11 WHOI-2000-11.
- 3. Van Dolah FM (2000) Marine algal toxins: origins, health effects, and their increased occurrence. Environmental Health Perspectives 108: 133–141.
- 4. Steidinger KA, Vargo GA, Tester PA, Tomas CR (1998) Bloom dynamics and physiology of Gymnodinium breve with emphasis on the Gulf of Mexico. In: Anderson DM, Cembella AD, Hallegraeff GM, editors. Physiological ecology of harmful algal blooms: NATO ASI series. 133–153.
- 5. Catterall WA, Risk M (1981) Toxin T4(6) from Ptychodiscus brevis (formerly Gymnodinium breve) enhances activation of voltage-sensitive sodium channels by veratridine. Mol Pharmacol 19: 345–348.
- 6. Lin Y-Y, Risk M, Ray SM, Van Engen D, Clardy J, et al. (1981) Isolation and structure of brevetoxin B from the “red tide” dinoflagellate Ptychodiscus brevis (Gymnodinium breve). J Am Chem Soc 103: 6773–6775.
- 7. Baden DG, Mende TJ, Poli MA, Block RE (1984) Toxins from Florida's red tide dinoflagellate Ptychodiscus brevis. In: Ragelis EP, editor. Seafood toxins: American Chemical Society. 359–367.
- 8. Poli MA, Mende TJ, Baden DG (1986) Brevetoxins, unique activators of voltage-sensitive sodium channels, bind to specific sites in rat brain synaptosomes. Mol Pharmacol 30: 129–135.
- 9. Huang JM, Wu CH, Baden DG (1984) Depolarizing action of a red-tide dinoflagellate brevetoxin on axonal membranes. J Pharmacol Exp Ther 229: 615–621.
- 10. Ramsdell JS (2008) The molecular and integrative basis to brevetoxin toxicity. In: Botana LM, editor. Seafood and Freshwater Toxins: Pharmacology, Physiology, and Detection. Boca Raton: CRC Press. 519–558.
- 11. McFarren EF, Tanabe H, Silva FJ, Wilson WB, Campbell JE, et al. (1965) The occurrence of a ciguatera-like poison in oysters, clams, and Gymnodinium breve cultures. Toxicon 3: 111–123.
- 12. Kirkpatrick B, Fleming LE, Squicciarini D, Backer LC, Clark R, et al. (2004) Literature review of Florida red tide: implications for human health effects. Harmful Algae 3: 99–115.
- 13. Woodcock AH (1948) Note concerning human respiratory irritation associated with high concentrations of plankton and mass mortality of marine organisms. J Mar Res 7: 56–62.
- 14. Asai JS, Krzanowski JJ, Lockey RF, Anderson WH, Martin DF, et al. (1984) Site of action of Ptychodiscus brevis toxin within parasympathetic axonal sodium channel h gate in airway smooth muscle. J Allergy Clin Immunol 73: 824–828.
- 15. Steidinger K, Burklew MA, Ingle RM (1972) The effects of Gymnodinium breve toxin on estuarine animals. In: Martin DF, Padilla GM, editors. Marine Pharmacognosy. New York: Academic Press. 179–202.
- 16. Bossart GD, Baden DG, Ewing RY, Roberts B, Wright SD (1998) Brevetoxicosis in manatees (Trichechus manatus latirostris) from the 1996 epizootic: gross, histologic and immunohistochemical features. Toxicol Pathol 26: 276–282.
- 17. Mase B, Jones W, Ewing R, Bossart GD, Van Dolah FM, et al.. (2000) Epizootic in bottlenose dolphins in the Florida panhandle: 1999–2000. In: Baer CK, editor. Proceedings of the American Association of Zoo Veterans and International Association for Aquatic Animal Medicine. New Orleans, LA. 522–525.
- 18. Naar JP, Flewelling LJ, Lenzi A, Abbott JP, Granholm A, et al. (2007) Brevetoxins, like ciguatoxins, are potent ichthyotoxic neurotoxins that accumulate in fish. Toxicon 50: 707–723.
- 19. Fire SE, Flewelling LJ, Naar J, Twiner MJ, Henry MS, et al. (2008) Prevalence of brevetoxins in prey fish of bottlenose dolphins in Sarasota Bay, Florida. Marine Ecology Progress Series 368: 283–294.
- 20. Flewelling LJ, Naar JP, Abbott JP, Baden DG, Barros NB, et al. (2005) Brevetoxicosis: red tides and marine mammal mortalities. Nature 435: 755–756.
- 21. Landsberg JH, Flewelling LJ, Naar J (2009) Karenia brevis red tides, brevetoxins in the food web, and impacts on natural resources: Decadal advancements. Harmful Algae 8: 598–607.
- 22. Van Dolah FM (2005) Effects of harmful algal blooms. In: Reynolds JE, Perrin WF, Reeves RR, Montgomery S, Ragen TJ, editors. Marine Mammal Research: Conservation beyond crisis. Baltimore, MD: Johns Hopkins University Press. 85–101.
- 23. Gunter G, Williams RH, Davis CC, Walton Smith FG (1948) Catastrophic mass mortality of marine mammals and coincident phytoplankton bloom on the west coast of Florida, November 1946 to August 1947. Ecological Monographs 18: 309–324.
- 24. Wright JLC, Quilliam M (1989) The amnesic shellfish poisoning mystery. Anal Chem 18: 1053a–1061a.
- 25. Work TM, Bar B, Beale AM, Fritz L, Quilliam M, et al. (1992) Epidemiology of domoic acid poisoning in brown pelican's (Pelecanus occidentalis) and Brandt's cormorants (Phalacrocorax penicillatus) in California. J Zoo Wildl Med 24: 54–62.
- 26. Scholin CA, Gulland F, Doucette GJ, Benson S, Busman M, et al. (2000) Mortality of sea lions along the central California coast linked to a toxic diatom bloom. Nature 403: 80–84.
- 27. Lefebvre KA, Powell CL, Busman M, Doucette GJ, Moeller PDR, et al. (1999) Detection of domoic acid in northern anchovies and california sea lions associated with an unusual mortality event. Natural Toxins 7: 85–92.
- 28. Hampson D, Manalo J (1998) The activation of glutamate receptors by kainic acid and domoic acid. Natural Toxins 6 153–158.
- 29. Bargu S, Powell CL, Coale SL, Busman M, Doucette GJ, et al. (2002) Krill: a potential vector for domoic acid in marine food webs. Mar Ecol Prog Ser 237: 209–216.
- 30. Blanco J, Acosta CP, Bermudez de la Puente M, Salgado C (2002) Depuration and anatomical distribution of the amnesic shellfish poisoning (ASP) toxin domoic acid in the king scallop Pecten maximus. Aquatic Toxicol 60: 111–121.
- 31. Ferdin ME, Kvitek RG, Bretz CK, Powell CL, Doucette GJ, et al. (2002) Emerita analoga (Stimpson)–possible new indicator species for the phycotoxin domoic acid in California coastal waters. Toxicon 40: 1259–1265.
- 32. Dickey RW, Fryxell GA, Granade HR, Roelke D (1992) Detection of the marine toxins okadaic acid and domoic acid in shellfish and phytoplankton in the Gulf of Mexico. Toxicon 30: 355–359.
- 33. Fryxell GA, Reap ME, Valencic DL (1990) Nitzschia pungens Grunow f. multiseries Hasle: observations of a known neurotoxic diatom. Nova Hedwigia (Beih) 100: 171–188.
- 34. Parsons ML, Scholin CA, Miller PE, Doucette GJ, Powell CL, et al. (1999) Pseudo-nitzschia species (Bacillariophyceae) in Louisiana coastal water: Molecular probe field trials, genetic variability, and domoic acid analyses. J Phycol 35: 1368–1378.
- 35. Pan Y, Parsons ML, Busman M, Moeller P, Dortch Q, et al. (2001) Pseudo-nitzschia sp. cf. pseudodelicatissima- a confirmed producer of domoic acid from the northern Gulf of Mexico. Mar Ecol Prog Ser 220: 93–92.
- 36. Liefer JD, MacIntyre HL, Novoveská L, Smith WL, Dorsey CP (2009) Temporal and spatial variability in Pseudo-nitzschia spp. in Alabama coastal waters: A “hot spot” linked to submarine groundwater discharge? Harmful Algae 8: 706–714.
- 37. Wells RS, Rhinehart HL, Hansen LJ, Sweeney JC, Townsend FI, et al. (2004) Bottlenose dolphins as marine ecosystem sentinels: Developing a health monitoring system. EcoHealth 1: 246–254.
- 38. Schwacke LH, Zolman ES, Balmer BC, De Guise S, Hoguet J, et al. (2012) Anemia, hypothyroidism and immune suppression associated with PCB exposure in bottlenose dolphins (Tursiops truncatus). Proc R Soc B 279: 48–57.
- 39. Wells RS (2003) Dolphin social complexity: Lessons from long-term study and life history. In: de Waal FBM, Tyack PL, editors. Animal Social Complexity: Intelligence, Culture, and Individualized Societies. Cambridge, MA: Harvard University Press. 32–56.
- 40. Twiner MJ, Fire S, Schwacke L, Davidson L, Wang Z, et al. (2011) Concurrent exposure of bottlenose dolphins (Tursiops truncatus) to multiple algal toxins in Sarasota Bay, Florida, USA. PLoS ONE 6: e17394.
- 41. Barros NB, Wells RS (1998) Prey and feeding patterns of resident bottlenose dolphins (Tursiops truncatus) in Sarasota Bay, Florida. Journal of Mammalogy 79: 1045–4059.
- 42. Barros NB, Odell DK (1990) Food habits of bottlenose dolphins in the Southeastern United States. In: Leatherwood S, Reeves RR, editors. The Bottlenose Dolphin. San Diego, CA: Academic Press, Inc. 309–328.
- 43. Irvine AB, Scott MD, Wells RS, Kaufmann JH (1981) Movements and activities of the Atlantic bottlenose dolphin, Tursiops truncatus, near Sarasota. Florida Fish Bull 79: 671–688.
- 44. Gannon DP, Berens McCabe EJ, Camilleri SA, Gannon JG, Brueggen MK, et al. (2009) Effects of Karenia brevis harmful algal blooms on nearshore fish communities in southwest Florida. Mar Ecol Prog Ser 378: 171–186.
- 45. Flaherty KE, Landsberg JH (2011) Effects of a persistent red tide (Karenia brevis) bloom on community structure and species-specific relative abundance of nekton in a Gulf of Mexico estuary. Estuaries and Coasts 34: 417–439.
- 46. Plakas SM, Wang Z, El Said KR, Jester ELE, Granade HR, et al. (2004) Brevetoxin metabolism and elimination in the Eastern oyster (Crassostrea virginica) after controlled exposures to Karenia brevis. Toxicon 44: 677–685.
- 47. Steidinger KA, Penta HL, editors (1999) Harmful microalgae and associated public health risks in the Gulf of Mexico. Report for the U.S. EPA Gulf of Mexico Program by the Florida Department of Environmental Protection, Florida Marine Research Institute, St. Petersburg. http://research.myfwc.com/publications/publication_info.asp?id=39879. Accessed 2012 Jul 17.
- 48. Steidinger KA, Wolny JL, Haywood AJ (2008) Identification of Kareniaceae (Dinophyceae) in the Gulf of Mexico. Nova Hedwigia Beihefte 133: 269–284.
- 49. Pierce RH, Henry MS, Proffitt LS, deRosset AJ (1992) Evaluation of solid sorbents for the recovery of polyether toxins (brevetoxins) in seawater. Bull Environ Contam Toxicol 49: 479–484.
- 50. Twiner MJ, Bottein Dechraoui M-Y, Wang Z, Mikulski CM, Henry MS, et al. (2007) Extraction and analysis of lipophilic brevetoxins (PbTx) from the red tide dinoflagellate Karenia brevis. Anal Biochem 369: 128–135.
- 51. Fernandez S, Hohn AA (1998) Age structure, growth, and calving season of bottlenose dolphins stranded along the coast of Texas. Fish Bull 96: 357–365.
- 52. Read AJ, Wells RS, Hohn AA, Scott MD (1993) Patterns of growth in wild bottlenose dolphins, Tursiops truncatus. J Zool, London 231: 107–123.
- 53. Fairey ER, Shuart NG, Busman M, Moeller PD, Ramsdell JS (2001) Biomonitoring brevetoxin exposure in mammals using blood collection cards. Environmental Health Perspectives 109: 717–720.
- 54. NOAA (2007) Interim report on the bottlenose dolphin (Tursiops truncatus) unusual mortality event along the Panhandle of Florida, March-April 2004. http://www.nmfs.noaa.gov/pr/pdfs/health/ume_bottlenose_2004.pdf. Accessed 2012 Jul 17.
- 55. Van Dolah FM, Doucette GJ, Gulland FMD, Rowles TL, Bossart GD (2003) Impacts of algal toxins on marine mammals. In: Vos JG, Bossart GD, Fournier M, O'Shea TJ, editors. Toxicology of marine mammals. New York: Taylor & Francis.
- 56. Roth PB, Twiner MJ, Wang Z, Bottein Dechraoui M-Y, Doucette GJ (2007) Brevetoxin (PbTx) dynamics following lysis of Karenia brevis by algicidal bacteria: Toxin size fractions and characterization of open A-ring PbTx hydrolytics. Toxicon 50: 1175–1191.
- 57. Naar J, Bourdelais A, Tomas C, Kubanek J, Whitney PL, et al. (2002) A competitive ELISA to detect brevetoxins from Karenia brevis (formerly Gymnodinium breve) in seawater, shellfish, and mammalian body fluid. Environ Health Persp 110: 179–185.
- 58. Maucher JM, Briggs LM, Podmore C, Ramsdell JS (2007) Optimization of blood collection card method/enzyme-linked immunoassay for monitoring exposure of bottlenose dolphin to brevetoxin-producing red tides. Environ Sci Technol 41: 563–567.
- 59. Woofter RT, Bottein Dechraoui M-Y, Garthwaite I, Towers NR, Gordon CJ, et al. (2003) Measurement of brevetoxin levels by radioimmunoassay of blood collection cards after acute, long-term, and low-dose exposure in mice. Environ Health Persp 111: 1595–1600.
- 60. Poli MA, Rein KS, Baden DG (1995) Radioimmunoassay for PbTx-2-type brevetoxins: epitope specificity of two anti-PbTx sera. J AOAC Int 78: 538–542.
- 61. Fire SE, Flewelling LJ, Wang Z, Naar J, Henry MS, et al. (2008) Florida red tide and brevetoxins: Association and exposure in live resident bottlenose dolphins (Tursiops truncatus) in the eastern Gulf of Mexico, U.S.A. Marine Mammal Science. 24: 831–844.
- 62. Fire SE, Wang Z, Byrd M, Whitehead HR, Paternoster J, et al.. (2011) Co-occurrence of multiple classes of harmful algal toxins in bottlenose dolphins (Tursiops truncatus) stranding during an unusual mortality event in Texas; USA. Harmful Algae.
- 63. Wang Z, Plakas SM, El Said KR, Jester ELE, Granade HR, et al. (2004) LC/MS analysis of brevetoxin metabolites in the Eastern oyster (Crassostrea virginica). Toxicon 43: 455–465.
- 64. Maucher J, Ramsdell J (2005) Domoic acid transfer to milk: evaluation of a potential route of neonatal exposure. Environ Health Perspect 113: 461–464.
- 65. Schwacke LH, Twiner MJ, De Guise S, Balmer BC, Wells RS, et al. (2010) Eosinophilia and biotoxin exposure in bottlenose dolphins (Tursiops truncatus) from a coastal area impacted by repeated mortality events. Enviro Res 110: 548–555.
- 66. Wang Z, King KL, Ramsdell JS, Doucette GJ (2007) Determination of domoic acid in seawater and phytoplankton by liquid chromatography-tandem mass spectrometry. Journal of Chromatography A 1163: 169–176.
- 67. Pierce R, Henry M, Blum P (2008) Brevetoxin abundance and composition during ECOHAB-Florida field monitoring cruises in the Gulf of Mexico. Continental Shelf Research 28: 45–58.
- 68. Baden DG (1996) Analyses of biotoxins (red tide) in manatee tissues. Miami: Report #MR148, Marine and Freshwater Biomedical Sciences Cener, National Institute of Environmental Health Sciences, Rosenstiel School of Marine and Atmospheric Sciences.
- 69. Cattet M, Geraci JR (1993) Distribution and elimination of ingested brevetoxin (PbTx-3) in rats. Toxicon 31: 1483–1486.
- 70. FWC (2008) Florida manatee (Trichechus manatus latirostris) red tide mortality event in southwestern Florida March – April 2003. Final Report to the Working Group on Marine Mammal Unusual Mortality Events. Florida Fish and Wildlife Conservation Commission, Fish and Wildlife Research Institute. 52.
- 71. Poli MA, Musser S, Dickey RW, Eilers PP, Hall S (2000) Neurotoxic shellfish poisoning and brevetoxin metabolites: a case study from Florida. Toxicon 38: 981–993.
- 72. Radwan FFY, Ramsdell JS (2006) Characterization of in vitro oxidative and conjugative metabolic pathways for brevetoxin (PbTx-2). Toxicol Sci 89: 57–65.
- 73. Shea D (1997) Analysis of brevetoxins by micellar electrokinetic capillary chromatography and laser-induced fluorescence detection. Electrophoresis 18: 277–283.
- 74. Landsberg JH, Tester P, Pierce R, Shea D, Van Dolah F, et al. (2000) ECOHAB Florida: fate and effects of brevetoxins in selected biota, water and sediments along the west Florida shelf, USA. Symposium on Harmful Marine Algae in the US. Marine Biological Laboratory, Woods Hole, Massachusetts, 4–9 December 2000: 44.
- 75. APHA (1970) Subcommittee on laboratory methods for the examination of shellfish. Method for the bioassay of Gymnodinium breve toxin(s) in shellfish, Recommended procedures for the examination of sea water and shellfish, 4th Edition. Washington, D.C.: American Public Health Association.
- 76. Radwan FF, Wang Z, Ramsdell JS (2005) Identification of a rapid detoxification mechanism for brevetoxin in rats. Toxicol Sci 85: 839–846.
- 77. Flewelling LJ (2008) Vectors of brevetoxins to marine mammals. St. Petersburg, Florida: University of South Florida. 143 p.
- 78. Benson JM, Gomez AP, Statom GL, Tibbetts BM, Fleming LE, et al. (2006) Placental transport of brevetoxin-3 in CD-1 mice. Toxicon 48: 1018–1026.
- 79. Bowen-Stevens SR (2011) Diet of bottlenose dolphins (Tursiops truncatus) from the Northwest Florida Panhandle and foraging behavior near Savannah, Georgia: Savannah State University. 162 p.
- 80. Fire SE, Fauquier D, Flewelling LJ, Henry MS, Naar J, et al. (2007) Brevetoxin exposure in bottlenose dolphins (Tursiops truncatus) associated with Karenia brevis blooms in Sarasota Bay, Florida. Mar Biol 152: 827–834.
- 81. Gaydos JK (2006) Bottlenose dolphins and brevetoxins: A coordinated research and response plan. NOAA Technical Memorandum NMFS-OPR-32: 46.
- 82. Hallegraeff GM (1993) A review of harmful algal blooms and their apparent global increase. Phycologia 32: 79–99.
- 83. Anderson DM, Glibert PM, Burkholder JM (2002) Harmful algal blooms and eutrophication: Nutrient sources, composition, and consequences. Estuaries 25: 704–726.
- 84. Paerl HW, Huisman J (2009) Climate change: a catalyst for global expansion of harmful cyanobacterial blooms. Environ Microbiol Rep 1: 27–37.