Monitoring the 2007 Florida east coast Karenia brevis (Dinophyceae) red tide and neurotoxic shellfish poisoning (NSP) event
Monitoring the 2007 Florida east coast Karenia brevis (Dinophyceae) red tide and neurotoxic shellfish poisoning (NSP) event
ALGAE. 2015. Mar, 30(1): 49-58
Copyright © 2015, The Korean Society of Phycology
This is an Open Access article distributed under the terms of the Creative Commons Attribution Non-Commercial License ( which permits unrestricted non-commercial use, distribution, and reproduction in any medium, provided the original work is properly cited.
  • Received : December 12, 2014
  • Accepted : February 02, 2015
  • Published : March 15, 2015
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About the Authors
Jennifer L. Wolny
Fish and Wildlife Research Institute, University of South Florida, Saint Petersburg, FL 33701, USA
Paula S. Scott
Fish and Wildlife Research Institute, Florida Fish and Wildlife Conservation Commission, Saint Petersburg, FL 33701, USA
Jacob Tustison
Fish and Wildlife Research Institute, Florida Fish and Wildlife Conservation Commission, Saint Petersburg, FL 33701, USA
Christopher R. Brooks
Division of Aquaculture, Florida Department of Agriculture and Consumer Services, Tallahassee, FL 32399, USA
In September 2007, reports of respiratory irritation and fish kills were received by the Florida Fish and Wildlife Conservation Commission (FWC) from the Jacksonville, Florida area. Water samples collected in this area indicated a bloom of Karenia brevis , the dinoflagellate that produces brevetoxin, which can cause neurotoxic shellfish poisoning. For the next four months, K. brevis was found along approximately 400 km of coastal and Intracoastal waterways from Jacksonville to Jupiter Inlet. This event represents the longest and most extensive red tide the east coast of Florida has experienced and the first time Karenia species other than K. brevis have been reported in this area. This extensive red tide influenced commercial and recreational shellfish harvesting activities along Florida’s east coast. Fourteen shellfish harvesting areas (SHAs) were monitored weekly during this event and 10 SHAs were closed for an average of 53 days due to this red tide. The length of SHA closure was dependent on the shellfish species present. Interagency cooperation in monitoring this K. brevis bloom was successful in mitigating any human health impacts. Kernel density estimation was used to create geographic extent maps to help extrapolate discreet sample data points into 5 km 2 radius values for better visualization of the bloom.
- History of east coast red tides
Karenia brevis red tides occur throughout the Gulf of Mexico and can be transported cross-shelf or along shore by currents and winds. K. brevis blooms almost annually along the West Florida shelf and occasionally along the Texas coastline ( Heil et al. 2014 ). The Gulf Stream has transported K. brevis red tides as far north as North Carolina ( Tester et al. 1991 ). The Gulf of Mexico’s Loop Current can create eddies that shed and move westward towards the Texan and Mexican coasts ( Paluszkiewicz et al. 1983 ). According to Tester and Steidinger (1997) , the Florida west coast is the epi-center of K. brevis red tides, however, since the 1940s red tide has also been recorded along Florida’s Keys, panhandle, and east coast.
Davis (1948) described K. brevis , as Gymnodinium brevis , from a 1946-1947 red tide along the west coast of Florida that was noted for respiratory irritation, extensive fish kills and other marine animal mortalities. In 1946, respiratory irritation and fish kills were reported at Jacksonville, suggesting that K. brevis red tides could occur on Florida’s east coast. However, it wasn’t until 1972 that the transport of K. brevis from the Florida west to east coasts via the Gulf Stream System was properly documented when a red tide came inshore at St. Lucie and Martin counties. Typical signs of red tide, including respiratory irritation and fish kills, were reported and water samples confirmed the presence of K. brevis ( Murphy et al. 1975 ). Roberts (1979) reported a similar red tide in 1977. In 1983, a Gulf Stream meander inoculated inshore areas near Jacksonville (Duval County) at the beginning of October. Over a 10-day period, the red tide moved south towards Cape Canaveral (Brevard County) and by the end of the month, the red tide had reached Sebastian Inlet (north Indian River County). Fish kills, discolored water, respiratory irritation and closures of shellfish harvesting areas (SHAs) were documented in this area through November ( Tester and Steidinger 1997 ). Transport of K. brevis from the west Florida coast to the east Florida coast via the Gulf Stream Current System has since been documented in 1990, 1997, and 1999. In each of these cases the blooms lasted about one month before dissipating.
The Florida Fish and Wildlife Conservation Commission (FWC) and the Florida Department of Agriculture and Consumer Services (FDACS) have been jointly monitoring Florida’s waters for K. brevis since the 1980s. Extensive efforts have been put forth to monitor and conduct large-scale research projects (i.e., Ecology and Oceanography of Harmful Algal Blooms [ECOHAB]: Karenia) on K. brevis by FWC and partners since the 1990s, and in 2000 FWC established a Volunteer Red Tide Offshore Monitoring Program to further expand the spatial and temporal collection of data ( Steidinger 1993 , Haverkamp et al. 2004 , Heil et al. 2014 ). Since 2002, routine monitoring by FWC and FDACS along Florida’s east coast have focused on the saxitoxin-producing dinoflagellate Pyrodinium bahamense ( Landsberg et al. 2006 , Phlips et al. 2011 ). Increased observations resulting from this FWC-FDCAS partnership and the expansion of FWC’s volunteer monitoring program to Florida’s east coast have not shown an increase in the frequency or duration of K. brevis blooms in this area. However, between September 2007 and January 2008, K. brevis , as well as four other Karenia spp., were found along approximately 400 km of coastal and Intracoastal waters from Jacksonville to Jupiter Inlet. This event represents the longest and most extensive K. brevis red tide documented on the east coast of Florida and the first time a multi-species Karenia bloom has been reported for this area.
- Neurotoxic shellfish poisoning (NSP) and management for public health
K. brevis produces the neurotoxin brevetoxin, which is responsible for causing serious human health effects and animal illness and mortalities. When K. brevis is present in SHAs, brevetoxins can accumulate in the shellfish tissues and can cause NSP when consumed ( Steidinger 1993 ). In humans, NSP is characterized by nausea, diarrhea, headaches, muscle aches, dizziness, and reversal of hot-cold temperature sensation with onset of symptoms within a few hours of eating contaminated shellfish ( Steidinger and Baden 1984 ). To date, there have been no human fatalities due to NSP; however, illness has been documented in people who have consumed unregulated or illegally harvested shellfish species ( Kirkpatrick et al. 2004 ).
The goal of the FDACS Division of Aquaculture is to provide maximum utilization of resources and reduce the risk of shellfish-borne illnesses ( Heil 2009 ). To achieve this goal FDACS works with the FWC to follow the National Shellfish Sanitation Program Model Ordinance’s Marine Biotoxin Monitoring for NSP. This plan calls for FDACS to maintain an early warning system by collecting water monthly from sentinel sites within SHAs for the analysis of K. brevis cell concentrations by FWC year round. If a K. brevis bloom is detected, FDACS changes their sampling strategy by increasing the number of sites collected within impacted SHAs on a weekly basis to determine the severity and extent of the bloom within SHAs. The detection of K. brevis in a concentration greater than 5 × 10 3 cells L −1 requires weekly monitoring until the cell concentration has dropped to below the 5 × 10 3 cells L −1 threshold. When cell concentrations fall below 5 × 10 3 cells L −1 FDACS collects shellfish for brevetoxin testing by FWC. Shellfish are collected and tested weekly using the mouse bioassay (MBA) until brevetoxin detection levels fall below the regulatory limit of 20 mouse units. At all times the threat of human illness is minimized through the use of FDACS’ website where SHA Information and Daily Status notices are posted at seas/seas_statusmap.htm . This information is also linked through FWC’s Red Tide Status page at . These websites are updated at a minimum of 2 times per week. In addition to these two websites, FDACS relays information regarding the status of SHAs directly to the members of the shellfish industry via phone calls and emails.
- Sample collection
On September 21, 2007, multi-species fish kills and respiratory irritation from Jacksonville area beaches were reported to FWC via the FWC Fish Kill Hotline, a service that allows citizens and other agencies to notify FWC about fish and animal mortality events and other unusual occurrences that pertain to wildlife. Water samples collected on September 25 from Fernandina Beach and Amelia Island (Nassau County, FL, USA) confirmed a bloom of Karenia brevis . Subsequently, the FWC Marine Mammal Group observed discolored water along 65 km of coastline from Mayport to St. Augustine Beach on September 28 while conducting a routine right whale survey. The confirmation of a K. brevis bloom in the northernmost east coast counties initiated weekly sampling in SHAs ( Fig. 1 ) by FDACS staff. Weekly sampling for water, shellfish and water quality parameters by FDACS occurred between September 25, 2007 and January 15, 2008. Additional samples were collected by FWC staff as part of existing research projects and by FWC volunteers opportunistically. Between September 2007 and January 2008, FDACS and FWC staff and volunteers collected 800 water samples over a 400 km area throughout 10 eastern Florida counties for the analysis of K. brevis cell concentrations. Water samples were collected as surface water grabs from a depth of 0.5 m. Live water samples were placed in 125-mL clear bottles (Nalgene #2007-0004; Thermo Scientific, Waltham, MA, USA), wrapped in wet newspaper and shipped at ambient temperature via overnight delivery to FWC. Live water samples were examined within 24 hours of collection. Fixed water samples were placed in 125-mL amber bottles (Nalgene #2009-0004; Thermo Scientific) containing 1-mL of Lugol’s iodine fixative and shipped to FWC where they were examined upon receipt.
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Florida’s east coast shellfish harvesting areas.
- Analysis forKareniaspecies
Karenia spp. were morphologically identified by screening the live material and then enumerated from Lugol’s iodine preserved aliquots. Samples were mixed by inversion and 3 mL were placed in a Lab-Tek Chamber Slide (Nalge Nunc #155379; Thermo Fischer Scientific, Rochester, NY, USA). All samples were allowed to settle for at least 1 hour prior to examination. Karenia spp. were identified and enumerated at 100× and 400× magnification using inverted microscopes. Identifications of Karenia spp. were based on Haywood et al. (2004) and Steidinger et al. (2008) .
- Shellfish analysis for brevetoxins
When microscopy analyses indicated that K. brevis cell concentrations were below 5 × 10 3 cells L −1 in impacted SHAs, clams ( Mercenaria sp.) or oysters ( Crassostrea virginica ) were collected weekly by FDACS and tested by FWC for NSP toxicity using MBA following the guidelines of the American Public Health Association (1970) . For MBAs, a minimum of 12 shellfish were shucked to obtain a 100 g meat sample for testing. Each meat sample was tested using a five-mouse set. Mice used were Swiss-Webster out-bred male mice, weighing 19 to 23 g, obtained from a regulated stock colony (Charles River, Wilmington, MA, USA). Mice were allowed to acclimate and rehydrate for at least 24 hours following shipping before being used in a MBA.
- Visualizing the data
The data was visualized in ArcGIS v.10.2.1 both as site specific, ground-truthed data points and interpolated as a surface model using kernel density estimation (KDE). The site specific data, given as geographic coordinates, was analyzed using a temporal data tool to show the event’s development over time and the geographic trajectory. This analysis allowed for the understanding of when the event became established and moved to the Intracoastal Waterway. To show the geographic extent of the bloom a surface model was created using point data (as recommended by Wang and Wu 2009 ) in the ArcGIS KDE function. The default bandwidth (point expansion radius) was selected so that calculations were based on spatial configuration and number data inputs and spatial outliers were autocorrected. Following the methods proposed by Xie and Yan (2008) in which cell per liter concentrations were converted to density using a Quartic curve, the K. brevis bloom was mapped using a standard planar KDE with a 5 km 2 radius from each data point and cell output size of 50 m.
- Analysis forKareniaspecies
Water samples collected on September 25 from Fernandina Beach and Amelia Island (Nassau County, FL, USA) indicated a bloom of K. brevis up to 3 × 10 5 cells L −1 . By October 3, K. brevis was detected along the coastlines of the five northeast counties of Florida and within the Intracoastal Waterways of St. Johns County ( Fig. 2A ) closing the SHAs located here. On October 16, K. brevis cell concentrations peaked at 6 × 10 6 cells L −1 in the Intracoastal Waterway of St. Johns County. During November the bloom persisted alongshore and in the Intracoastal Waterway of Volusia County. In late November the bloom was situated in the coastal and Intracoastal areas south of Cape Canaveral ( Fig. 2B ). By December 3, four of the seven SHAs in Brevard County were closed. On December 9, K. brevis was detected in the Intracoastal Waterways of Indian River and St. Lucie counties and SHAs were closed. On December 27, K. brevis was detected along the coast of Martin County. Throughout this bloom water temperatures ranged from 12.2-29.2℃ in the Intracoastal Waterway and 20.0-29.1℃ in the coastal waters; salinity ranged from 19.6-37.6 in the Intracoastal Waterway and 27.1-37.0 in the coastal waters.
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Progression of the Karenia brevis red tide along the east coast of Florida from September 25, 2007 through January 15, 2008. (A) Cell concentrations of K. brevis for September 25 through November 3, 2007. (B) Cell concentrations of K. brevis for November 16, 2007 through January 15, 2008. Data points represent analysis of 800 individual water samples.
While monitoring for K. brevis during the 2007-2008 red tide event, four other species of Karenia were detected. Concentrations of Karenia papilionacea, K. mikimotoi, K. selliformis , and Karenia sp. #3 [described in Steidinger et al. (2008) as morphologically similar to K. umbella ] were at very low levels (0.3−7 × 10 3 cells L −1 ) and always co-occurred with K. brevis .
- Shellfish analysis for brevetoxins
When K. brevis cell concentrations dropped below the regulatory limit of 5 × 10 3 cells L −1 MBAs were conducted on shellfish (oysters, clams, or both, depending on the SHA) collected weekly from impacted SHAs. When MBA results indicated NSP concentrations were below the regulatory action limit of <20 mouse units 100 g shellfish FDACS −1 reopened SHAs to commercial and recreational harvesting. Based on MBA results, SHAs in St. Johns County were reopened on December 13. SHAs in Indian River County were reopened on January 12, 2008 and on January 25 in Brevard, St. Lucie, and Volusia counties. Ten SHAs on the east coast of Florida were closed for an average of 53 days due to this K. brevis red tide ( Table 1 ).
Shellfish harvesting area (SHA) closures due to neurotoxic shellfish poisoning (NSP) during the 2007-2008Karenia brevisred tide event along Florida’s east coast
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Action limit for SHA closure is 5,000 cells L−1 of K. brevis. Shellfish resources tested for NSP must be below 20 MU for SHAs to be reopened. aK. selliformis only. NA, not acquired.
- Visualizing the data
The data presented in Fig. 2 were used by resources managers and posted to FWC’s Red Tide Current Status webpage. The data presented as a KDE map ( Fig. 3 ) provides a more probable image of what Florida’s east coast looked like during the red tide. Given the limited distribution of samples within any one map quadrate a conservative estimate of 5 km 2 was used to expand the density radius of each data point.
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Karenia brevis cell concentrations visualized using a kernel density estimation over a 5 km2 radius for the duration of the 2007-2008 Florida east coast bloom.
K. brevis red tides on the east coast of Florida are not uncommon but they are not the nearly annual events that they are on the West Florida shelf. The four month long 2007-2008 event represents the longest east coast K. brevis red tide recorded to date and affected approximately 400 km of coastline. Using a Regional Oceanographic Modeling System (ROMS) and Hybrid Coordinate Ocean Model (HYCOM) derived circulation model for surface drifters and diagnostic color and backscatter algorithms for satellite imagery (both calibrated for Karenia on the West Florida shelf). Walsh et al. (2009) showed that the 2007-2008 east coast red tide was transported to the Jacksonville area via the Loop Current and the Gulf Stream from a K. brevis population detected offshore of Fort Myers, Florida. Winds and currents moved the bloom from coastal waters of Jacksonville southwards into the Intracoastal waterways. During this event, 10 SHAs on Florida’s east coast were closed for an average of 53 days. The duration of this event across 14 different SHAs allowed for a thorough testing of the National Shellfish Sanitation Program Model Ordinance’s Marine Biotoxin Monitoring for NSP by FDACS and FWC.
Notification of a potential K. brevis bloom / NSP event was received by FWC on September 21, 2007 via the FWC Fish Kill Hotline. Opportunistic aerial surveys conducted by the FWC Marine Mammal Group during the last week of September 2007 allowed for first hand observation of the discolored water in the Jacksonville area. This information was passed along to FDACS staff to initiate an increase in the frequency and geographical distribution of sampling within SHAs and to FWC staff and volunteers to provide ancillary samples and data.
Within one week of the initial sampling confirming the presence of K. brevis , FDACS and FWC had determined that the K. brevis was present along the coastlines and Intracoastal waterways of the five northern-most east Florida counties. The severity of the K. brevis bloom ( Fig. 3 ) was sufficient enough to warrant the closing of commercial and recreational SHAs to prevent human illness from NSP as brevetoxins are rapidly accumulated by oysters ( Crassostrea virginica ) and clams ( Mercenaria sp.) through ingestion of K. brevis cells and through exposure to brevetoxin in the water column ( Plakas et al. 2008 , Griffith et al. 2013 ). From September 25, 2007 to January 25, 2008, SHAs were monitored weekly for K. brevis cell concentrations from water samples. Once K. brevis cell concentrations dropped below 5 × 10 3 cells L −1 , MBAs were performed on the meats of clams and oysters to test for the presence or absence of brevetoxin. After brevetoxin levels in tested shellfish dropped below the regulatory action limits of 20 mouse unit 100 g SHAs −1 were reopened.
Plakas et al. (2008) reported that oysters could take up to two weeks after the dissipation of a K. brevis bloom to depurate enough brevetoxin so that is was not detectable using MBA. However, brevetoxin metabolite products can be detected in oysters for 2-8 months after bloom dissipation using in vitro assays or instrumental methods ( Plakas et al. 2004 ). Griffith et al. (2013) reported similar findings for the clam Mercenaria mercenaria but their experimental method did not allow for a differentiation between the brevetoxin parent congeners and metabolite products. During the 2007-2008 bloom event it took an average of 8 days for clams to depurate brevetoxin and for SHAs to be reopened after K. brevis cell concentrations dropped below regulatory levels. Alternatively, it took an average of 30 days for oysters to depurate brevetoxin and for SHAs to be reopened after K. brevis cell concentrations dropped below regulatory limits. The current guidelines in the National Shellfish Sanitation Program Model Ordinance’s Marine Biotoxin Monitoring for NSP do not specify which species of shellfish should be examined for SHA regulations. However, our findings show there is a different rate of brevetoxin depuration between oyster and clam species and this should be considered when monitoring SHAs with mixed shellfish.
No reports of human NSP illness were received during this event despite that fact that shellfish from seven SHA were at levels considered toxic for more than one month. This highlights the success of the standard operating procedure of the National Shellfish Sanitation Program Model Ordinance’s Marine Biotoxin Monitoring for NSP. It should be noted that at the onset of this event (September 25-29) construction workers dredging near Amelia Island reported experiencing respiratory and eye irritation, symptoms consistent with exposure to K. brevis blooms, to the Nassau County Health Department ( Reich et al. 2008 ). Interagency cooperation between FDACS and FWC was instrumental in monitoring the 2007-2008 east coast K. brevis red tide event and preventing human illness due to NSP.
During the 2007-2008 K. brevis red tide event, four other species of Karenia were detected. Throughout the event, concentrations of Karenia mikimotoi, K. papilionacea, K. selliformis , and Karenia sp. #3 (morphologically similar to K. umbella ) were at very low levels (0.3−7 × 10 3 cells L −1 ) and co-occurred with K. brevis , except in Body E (Brevard County) where only K. selliformis was detected. This represents the first time these four Karenia species have been recorded on Florida’s east coast although they have been reported to occur in the Gulf of Mexico ( Steidinger et al. 2008 ) and are found routinely during K. brevis red tides along the west Florida coast (J. Wolny unpublished data).
Karenia mikimotoi, K. papilionacea , and K. selliformis occurred September through December in mainly coastal samples (<70% of occurrences). This may indicate a coastal origin and / or movement of these species within the existing K. brevis bloom. Karenia sp. #3 was recorded in 78 samples, of which 55.2% were collected in the Intracoastal Waterway from October through January. This, along with previous records of Karenia sp. #3 made in the Indian River Lagoon during times when K. brevis was absent (J. Wolny unpublished data), may indicate a lagoonal origin or habitat preference for this species.
The National Shellfish Sanitation Program Model Ordinance’s Marine Biotoxin Monitoring for NSP guidelines for Florida’s commercial and recreational SHAs are based only on the presence of K. brevis and the toxicity of shellfish due to brevetoxin. To date, toxic compounds have not been found associated with K. papilionacea ( Mooney et al. 2007 ) or K. umbella ( de Salas et al. 2004 ). However, K. selliformis produces gymnodimines and spirolides, both types of neurotoxins ( Dragunow et al. 2005 ), that have not been linked to any negative human health impacts but can produce false positives in toxin detection ( Fonfría et al. 2010 ). The environmental triggers that may enhance the toxicity of polyunsaturated fatty acids and other bioactive compounds produced by K. mikimotoi are still being investigated ( Mooney et al. 2007 , Chen et al. 2011 ). The management implications for the presence of multi-species Karenia blooms in Florida waters have not been addressed and are an avenue for future research and policy reviews.
One of the main limiting factors for using satellite remote sensing to detect HABs is the optical complexity of shallow inshore waters ( Hu et al. 2005 ), like those of Florida’s Intracoastal Waterway. KDE mapping is useful for representing spatial data points over 2-D geographical space ( Xie and Yan 2008 ) and Wang and Wu (2009) used KDE mapping to identify ‘hot spots’ of HAB activity in the East China Sea. While the use of ocean optics and satellite imagery for detecting and monitoring algal blooms has been well documented and tested on Florida’s west coast ( Hu et al. 2005 , Cannizzaro et al. 2008 , Tomlinson et al. 2009 ), the same is not true for Florida’s east coast. Until such a time when satellite imagery and ocean optics can be relied on for imaging algal blooms on Florida’s east coast it may be beneficial to use KDE mapping to create a more accurate picture of how an area is being impacted, since blooms are known to occur over a geographic expanse and not just where a sample is taken. This paper reports on the first time this technique has been used to visualize a Florida HAB. The map presented in Fig. 3 gives a more realistic image of what the geographical extent of the Karenia bloom looked like along Florida’s east coast. Like the KDE model developed by Wang and Wu (2009) our approach did not take into account meteorological factors, such as tides and currents, which obviously play a role in bloom distribution. Before KDE mapping can be used by FWC, FDACS, or other agencies for management and mitigation strategies, the appropriate bandwidth should be tested with concentrated, fixed-point discrete sampling and flow-rate measurements along Florida’s east coast and within the Intercoastal Waterway.
Dr. Earnest Truby is gratefully acknowledged for his contribution to monitoring Florida’s waters forKarenia. Doug Adams and Rich Paperno (FWC) and Howard Beadle and Bill Browning (FDACS) are thanked for assisting with sample collections.
1970 Recommended procedures for the examination of sea water and shellfish 4th ed American Public Health Association New York 105 -
Cannizzaro J. P. , Carder K. L. , Chen F. R. , Heil C. A. , Vargo G. A. 2008 A novel technique for detection of the toxic dinoflagellate, Karenia brevis, in the Gulf of Mexico from remotely sensed ocean color data Cont. Shelf Res. 28 137 - 158
Chen Y. , Yan T. , Yu R. , Zhou M. 2011 Toxic effects of Karenia mikimotoi extracts on mammalian cells Chinese J. Oceanol. Limnol. 29 860 - 868
Davis C. C. 1948 Gymnodinium brevis sp. nov., a cause of discolored water and animal mortality in the Gulf of Mexico Bot. Gaz. 109 358 - 360
de Salas M. F. , Bolch C. J. S. , Hallegraeff G. M. 2004 Karenia umbella sp. nov. (Gymnodiniales, Dinophyceae), a new potentially ichthyotoxic dinoflagellate species from Tasmania, Australia Phycologia 43 166 - 175
Dragunow M. , Trzoss M. , Brimble M. A. , Cameron R. , Beuzenberg V. , Holland P. , Mountfort D. 2005 Investigations into the cellular actions of the shellfish toxin gymnodimine and analogues Environ. Toxicol. Pharm. 20 305 - 312
Fonría E. S. , Vilariño N. , Espiña B. , Louzao M. C. , Álverez M. , Molgó J. , Aráoz R. , Botana L. M. 2010 Feasibility of gymnodimine and 13-desmethyl C spirolide detection by fluorescence polarization using a receptor-based assay in shellfish matrixes Anal. Chim. Acta. 657 75 - 82
Griffith A. W. , Shumway S. E. , Volety A. K. 2013 Bioaccumulation and depuration of brevetoxins in the eastern oyster (Crassostrea virginica) and the northern quahog (= hard clam, Mercenaria mercenaria) Toxicon 66 75 - 81
Haverkamp D. , Steidinger K. A. , Heil C. A. , Hall S. , Etheridge S. , Anderson D. , Kleindinst J. , Zhu M. , Zou Y. 2004 Harmful Algae Management and Mitigation. APEC Publication #204-MR-04.2 Asia Pacific Economic Cooperation Singapore 102 - 109
Haywood A. J. , Steidinger K. A. , Truby E. W. , Berquist P. R. , Berquist P. L. , Adamson J. , MacKenzie L. 2004 Comparative morphology and molecular phylogenetic analysis of three new species of the genus Karenia (Dinophyceae) from New Zealand J. Phycol. 40 165 - 179
Heil C. A. , Bronk D. A. , Dixon L. K. , Hitchcock G. L. , Kirkpatrick G. J. , Mulholland M. R. , O’Neil J. M. , Walsh J. J. , Weisberg R. , Garrett M. 2014 The Gulf of Mexico ECOHAB: Karenia Program 2006-2012 Harmful Algae 38 3 - 7
Heil D. C. 2009 Karenia brevis monitoring, management, and mitigation for Florida molluscan shellfish harvesting areas Harmful Algae 8 608 - 610
Hu C. , Muller-Karger F. E. , Taylor C. , Carder K. L. , Kelble C. , Johns E. , Heil C. A. 2005 Red tide detection and tracing using MODIS fluorescence data: a regional example in SW Florida coastal waters Remote Sens. Environ. 97 311 - 321
Kirkpatrick B. , Fleming L. E. , Squicciarini D. , Backer L. C. , Clark R. , Abraham W. , Benson J. , Cheng Y. S. , Johnson D. , Pierce R. , Zaias J. , Bossart G. D. , Baden D. G. 2004 Literature review of Florida red tide: implications for human health effects Harmful Algae 3 99 - 115
Landsberg J. H. , Hall S. , Johannessen J. N. , White K. D. , Conrad S. M. , Abbott J. P. , Flewelling L. J. , Richardson R. W. , Dickey R. W. , Jester E. L. E. , Etheridge S. M. , Deeds J. R. , van Dolah F. M. , Leighfield T. A. , Zou Y. , Beaudry C. G. , Benner R. A. , Rogers P. L. , Scott P. S. , Kawabata K. , Wolny J. L. , Steidinger K. A. 2006 Saxitoxin puffer fish poisoning in the United States, with the first report of Pyrodinium bahamense as the putative toxin source Enivron. Health Perspect. 114 1502 - 1507
Mooney B. D. , Nichols P. D. , de Salas M. F. , Hallegraeff G. M. 2007 Lipid, fatty acid, and sterol composition of eight species of Kareniaceae (Dinophyta): chemotaxonomy and putative lipid phycotoxins J. Phycol. 43 101 - 111
Murphy E. B. , Steidinger K. A. , Roberts B. S. , Williams J. , Jolley J. W. 1975 An explanation for the Florida East Coast Gymnodinium breve red tide of November 1972 Limnol. Oceangr. 20 481 - 486
Paluszkiewicz T. , Atkinson L. P. , Posmentier E. S. , McClain C. R. 1983 Observations of a loop current frontal eddy intrusion onto the West Florida Shelf J. Geophys. Res. 88 9639 - 9651
Phlips E. J. , Badylak S. , Christman M. , Wolny J. , Brame J. , Garland J. , Hall L. , Hart J. , Landsberg J. , Lasi M. , Lockwood J. , Paperno R. , Scheidt D. , Staples A. , Steidinger K. 2011 Scales of temporal and spatial variability in the distribution of harmful algae species in the Indian River Lagoon, Florida, USA Harmful Algae 10 277 - 290
Plakas S. M. , Jester E. L. E. , El Said K. R. , Granade H. R. , Abraham A. , Dickey R. W. , Scott P. S. , Flewelling L. J. , Henry M. , Blum P. , Pierce R. 2008 Monitoring of brevetoxins in the Karenia brevis bloom-exposed Eastern oyster (Crassostrea virginica) Toxicon 52 32 - 38
Plakas S. M. , Wang Z. , El Said K. R. , Jester E. L. E. , Granade H. R. , Flewelling L. , Scott P. , Dickey R. W. 2004 Brevetoxin metabolism and elimination in the Eastern oyster (Crassostrea virginica) after controlled exposures to Karenia brevis Toxicon 44 667 - 685
Reich A. , Blackmore C. , Hopkins R. , Lazensky R. , Geib K. , Ngo-Seidel E. 2008 Illness associated with red tide - Nassau County, Florida, 2007 Morb. Mortal. Wkly. Rep. 57 717 - 720
Roberts B. S. , Taylor D. L. , Seliger H. H. 1979 Toxic Dinoflagellate Blooms Elsevier New York Occurrence of Gymnodinium breve red tides along the west and east coasts of Florida during 1976 and 1977 199 - 202
Steidinger K. A. , Falconer I. R. 1993 Algal Toxins in Seafood and Drinking Water Academic Press London Some taxonomic and biologic aspects of toxic dinoflagellates 1 - 28
Steidinger K. A. , Baden D. G. , Spector D. L. 1984 Dinoflagellates Academic Press Orlando, FL Toxic marine dinoflagellates 201 - 261
Steidinger K. A. , Wolny J. L. , Haywood A. J. 2008 Identification of Kareniaceae (Dinophyceae) in the Gulf of Mexico Nova Hedwigia Beih. 133 269 - 284
Tester P. A. , Steidinger K. A. 1997 Gymnodinium breve red tide blooms: initiation, transport, and consequences of surface circulation Limnol. Oceanogr. 42 1039 - 1051
Tester P. A. , Stumpf R. P. , Vukovich F. M. , Fowler P. K. , Turner J. T. 1991 An expatriate red tide bloom: transport, distribution, and persistence Limnol. Oceanogr. 36 1053 - 1061
Tomlinson M. C. , Wynne T. T. , Stumpf R. P. 2009 An evaluation of remote sensing techniques for enhanced detection of the toxic dinoflagellate, Karenia brevis Remote Sens. Environ. 113 598 - 609
Walsh J. J. , Weisberg R. H. , Lenes J. M. , Chen F. R. , Dieterle D. A. , Zheng L. , Carder K. L. , Vargo G. A. , Havens J. A. , Peebles E. , Hollander D. J. , He R. , Heil C. A. , Mahmoudi B. , Landsberg J. H. 2009 Isotopic evidence for dead fish maintenance of Florida red tides, with implications for coastal fisheries over both source regions of the West Florida shelf and within downstream waters of the South Atlantic Bight Prog. Oceanogr. 80 51 - 73
Wang J. , Wu J. 2009 Occurrence and potential risk of harmful algal blooms in the East China Sea Sci. Total Environ. 407 4012 - 4021
Xie Z. , Yan J. 2008 Kernel density estimation of traffic accidents in a network space Comput. Environ. Urban Syst. 32 396 - 406