Harmful algal toxins of the Florida red tide (Karenia brevis): natural

chemical stressors in South Florida coastal ecosystems

R. H. Pierce and M. S. Henry

Mote Marine Laboratory, 1600 Ken Thompson Parkway, Sarasota, FL 34236, USA

Abstract

The Florida red tide is a descriptive name for high concentrations of the harmful marine alga, Karenia

brevis. Although most prevalent along the south-west Florida coast, periodic blooms have occurred

throughout the entire US and Mexico Gulf coasts and the Atlantic coast to North Carolina. This

dinoflagellate produces a suite of polyether neurotoxins, called brevetoxins, that cause severe impacts

to natural resources, as well as public health. These naturally produced biotoxins may represent one

of the most common chemical stressors impacting South Florida coastal and marine ecosystems.

Impacts include massive fish kills, marine mammal, sea turtle and sea bird mortalities, benthic

community die-off and public health effects from shellfish contamination and inhalation of air-borne

toxins. The primary mode of action is binding to voltage-gated sodium channels causing

depolarization of nerve cells, thus interfering with nerve transmission. Other effects include immune

depression, bronchial constriction and haemolysis. Parent algal toxins are synthesized within the

unicellular organism, others are produced as metabolic products. Recent studies into the composition

of brevetoxins in cells, water, air and organisms have shown PbTx-2 to be the primary intracellular

brevetoxin that is converted over time to PbTx-3 when the cells are ruptured, releasing extracellular

brevetoxins into the environment. Brevetoxins become aerosolized by bubble-mediated transport of

extracellular toxins, the composition of which varies depending on the composition in the source

water. Bivalved molluscs rapidly accumulate brevetoxins as they filter feed on K. brevis cells.

However, the parent algal toxins are rapidly metabolized to other compounds, some of which are

responsible for neurotoxic shellfish poisoning (NSP). These results provide new insight into the

distribution, persistence and impacts of red tide toxins to south-west Florida ecosystems.

Keywords

Brevetoxins; Biotoxins; PbTx; HABs; Florida red tide

Introduction

Toxic red tides (harmful algal blooms, HABs) were reported along the Florida Gulf coast by

Spanish explorers in the 1500s with written documentation in the 1840s (Ingersoll 1882;

Walker 1884; Baden et al. 2005). Environmental impacts include massive fish kills, marine

mammal, sea turtle and sea bird mortalities and impacts on benthic communities including sea

grass and coral community die-offs (Steidinger et al. 1973, 1995; Bossart et al. 1998; Trainer

and Baden 1999; Flewelling et al. 2005). Human health effects include cases of human

intoxication from neurotoxic shellfish poisoning (NSP) and impacts on human respiratory

function (Plakas et al. 2002; Fleming et al. 2005; Pierce et al. 2005).

Correspondence to: R. H. Pierce, rich@mote.org.

NIH Public Access

Author Manuscript

Ecotoxicology. Author manuscript; available in PMC 2009 May 18.

Published in final edited form as:

Ecotoxicology. 2008 October ; 17(7): 623–631. doi:10.1007/s10646-008-0241-x.

NIH-PA Author Manuscript NIH-PA Author Manuscript NIH-PA Author Manuscript
Globally, HABs appear to be increasing in frequency, duration and geographic region (Smayda

1990; Anderson 1994; Van Dolah 2000). The most prevalent HABs along the Florida Gulf

coast are caused by the dinoflagellate, K. brevis (formerly, Gymnodinium breve, Davis)

(Duagbjerg et al. 2001). Although always present in low concentrations throughout the Gulf

with no apparent adverse effects, high concentrations (blooms) of K. brevis produce sufficient

neurotoxins to cause the ecological and human impacts (Roberts 1979; Tester and Steidinger

1997; Landsberg and Steidinger 1998; Poli et al. 2000; Pierce et al. 2004, 2005). Commonly

referred to as the Florida Red Tide, these blooms occur most frequently along the south-west

Florida coast that vary from minor blooms to severe, intensive blooms that persist up to 18

months (Gunter et al. 1948; Rounsefell and Nelson 1966; Landsberg 2002).

Brevetoxins are polycyclic ether ladder compounds that are differentiated into two similar, yet

distinct backbone structures PbTx-1 (type-A) with 10 rings, and PbTx-2 (type-B) with 11 rings

(Fig. 1) (Catterell and Risk 1981;Poli et al. 1986;Shimizu et al. 1986). The suite of brevetoxins

includes at least nine, and as many as 14 compounds (designated as PbTx-1, -2, -3, etc.) ranging

in molecular weight from 868 to 936 (Poli et al. 1986;Baden et al. 1995). The parent algal

toxins (PbTx-1 and -2) undergo metabolic changes producing the suite of PbTx as the bloom

matures. Several additional PbTx compounds and analogue have been observed recently and

are currently undergoing structural verification, including the PbTx antagonist, brevenal, that

competitively inhibits the toxicity of PbTx (Baden et al. 2005;Bourdelais et al. 2005;Abraham

et al. 2006).

The primary mode of action is binding of PbTx to site 5 of voltage-sensitive sodium channels

(VSSC) in neurons (Baden and Mende 1982; Trainer and Baden 1999). This binding results

in persistent activation of cells, interfering with proper nerve transmission. Additional impacts

include bronchial constriction, haemolysis, immune suppression and genetic damage (Baden

et al. 1995, 2005; Bossart et al. 1998). Mammalian toxicity has been determined by oral,

intravenous (iv) and intrapperitoneal (ip) injections to mice. PbTx-3 (T17) exhibited an acute

24 h LC50 of 0.52 mg/kg oral, 0.17 mg/kg ip and 0.09 mg/kg iv. PbTx-2 (T34) exhibited 6.6

mg/kg oral, 0.2 mg/kg iv and 0.2 mg/kg ip, indicating PbTx-3 to be the predominantly orally

toxic PbTx (Baden and Mende 1982). The 24 h acute LD50 for PbTx-1 has been established

as 0.5 mg/kg ip, mouse body weight (Rein et al. 1994).

The most serious intoxication observed in humans is NSP resulting from ingestion of

contaminated shellfish (Steidinger et al. 1973; Baden 1983; Poli et al. 2000). Filter-feeding

shellfish, such as mussels, clams and oysters, accumulate the neurotoxins and toxic metabolites

as they feed on the microscopic algae. Symptoms of NSP include gastrointestinal disorders,

tingling sensation of lips and extremities, reversal of hot and cold sensation, rapid heartbeat,

loss of balance and a lack of motor coordination (Steidinger and Baden 1984; Baden et al.

1995). The State of Florida maintains a public health safety policy for closure of shellfish beds

at K. brevis cell counts of 5,000 cells/l, requiring continued monitoring of shellfish waters for

public health protection. Human toxicity levels have been established as 0.8 mg PbTx-2/kg

shellfish tissue. Utilizing the mouse bioassay as the standard technique for monitoring shellfish

beds, toxicity is indicated at 20 mouse units/100 g of shellfish tissue (American Public Health

Association 1970). New analytical techniques are currently being developed to provide more

rapid and less invasive procedures, including enzyme-linked immunosorbent assay (ELISA)

(Naar et al. 2002).

Another route of exposure is inhalation of air-borne (aerosol) PbTx. The aerosolization process

occurs by bubble-mediated transport of PbTx molecules adsorbed to the surface of entrained

bubbles. Bubbles transport toxins to the sea surface where they are ejected into the air

associated with jet and film drops produced as the bubbles burst (Blanchard 1975; Pierce et al.

1990). Toxin-containing aerosols are blown onshore causing respiratory irritation to humans

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and other mammals (Cheng et al. 2005; Pierce et al. 2005; Baden et al. 2005). Symptoms of

exposure include stinging eyes and nose, dry choking cough and onset of asthmatic attack in

susceptible subjects (Fleming et al. 2005; Kirkpatrick et al. 2006). The first written report

associating respiratory irritation with a Florida red tide was provided by Taylor (1917). A more

thorough correlation with symptoms was provided by Woodcock (1948) who surmised that

the irritation was caused by aerosolized products of the dinoflagellate bloom. More recent

studies have verified Woodcock’s hypothesis showing the composition of aerosolized PbTx

and the size distribution of toxin-containing aerosols (Pierce et al. 1990, 2003, 2005; Cheng

et al. 2005).

Massive fish kills are a common result of the Florida red tide leaving beaches and bays choked

with dead and decaying carcasses. The decomposing biomass adds to the environmental stress

by depleting oxygen from the water. Fish accumulate PbTx by ingestion of viable K. brevis

cells and contaminated prey, and by absorption of toxins across gill membranes (Abbott et al.

1975; Catterell and Risk 1981; Tester et al. 2000). Quick and Henderson (1974) reported a

value of 2.5 × 106 cells/l as the typical concentration causing fish mortality. Mortality from

chronic exposure to much lower concentrations also has been reported indicating accumulation

of toxins to a lethal level over several days (Landsberg 2002; Pierce unpublished data). Fish

have the ability to detoxify PbTx and will recover if removed from red tide contaminated water

in time. Mortality of benthic invertebrates has been related to anoxia as well as neurotoxicity

resulting from a combination of oxygen depletion by decomposition of dead flora and fauna

and night time respiration of high concentrations of K. breve (Simon and Dauer 1972;

Steidinger et al. 1973; Roberts et al. 1979).

Exposure of marine animals to PbTx results from ingestion of contaminated food and from

inhalation of aerosolized PbTx. During two of the largest red tide events to on record, 1946–

1947 and 1953–1955, mass mortalities of marine animals were reported all along the central

and south-west Florida Gulf coast from Tarpon Springs to Key West (Steidinger et al. 1973;

Landsberg 2002). In 1987–1988, more than 740 bottlenose dolphins died along the Atlantic

coast, implicating PbTx-contaminated menhaden as the vector (Geraci 1989). Ingestion of

contaminated fish prey was implicated as the cause in the deaths of 107 bottlenose dolphins

along the Florida Panhandle in 2004 (Flewelling et al. 2005). Manatee deaths have been

reported during numerous red tide events, including 39 deaths in 1982, 149 in 1996, 34 in 2002

and 86 in 2005 (O’Shea et al. 1991; Bossart et al. 1998; FWCC 2007). PbTx and metabolites

were found to persist in seagrass communities long after the bloom had gone, providing a

source for continued intoxication of grazing manatees (Flewelling et al. 2005).

As a result of the extensive areas and variety of natural resources impacted by K. brevis blooms,

PbTx produced by the Florida red tide may represent the most common suite of chemical

stressors impacting South Florida coastal and marine ecosystems. The purpose of this paper is

to provide a comprehensive assessment of PbTx produced during Florida red tides, considering

chemical composition, transport, exposure, concentration and toxicity.

Methods

PbTx composition

The composition and concentration of PbTx were investigated from red tide blooms along the

south-west Florida Gulf coast providing representative results for blooms from Tampa Bay to

the Florida Keys. Water samples were collected in 1 l glass bottles near-shore, and aboard ship

using Niskin® bottles attached to a rosette sampler. A 20 ml sub-sample was fixed with

Utermohls solution (Guillard 1973) for microscopic identification and enumeration of K.

brevis cells. PbTx were extracted from the water by filtration through a C-18 solid-phase

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extraction disc (Ansys Technologies Inc., Lake Forest, CA, USA) and recovered with methanol

for LC–MS analyses according to the procedure of Pierce et al. (2005).

PbTx analyses were performed by LC–MS using a ThermoFinnigan AqA HPLC/MS obtained

from Thermo Electron Corp. (Manchester, UK) using an AqA single quad system scanned

from 204 to 1,216 AMU with a Phenomenex Luna C-18 5Fm 250 mm × 2 mm analytical

column with solvent gradient. The instrument was calibrated with a standard PbTx mix

containing PbTx-2 and PbTx-3 obtained from the Center for Marine Science, UNCW,

Wilmington, NC (Pierce et al. 2005).

The composition of intra and extracellular toxins was studied using a low pressure cell

concentrator (Amicon, Beverly, MA) to separate viable cells from ambient water. The

unarmored nature of K. brevis renders it susceptable to cell lysis releasing PbTx to the ambient

water. Extracellular toxins were recovered from the filtrate by C-18 disc as above. Intracellular

toxins were recovered by lysing the K. brevis cells with distilled water and filtering through a

C-18 disc, followed by methanol extraction for LC–MS analysis as above. One-litre samples

were analysed for total toxins, for comparative mass balance (Pierce et al. 2001).

Aerosol toxins

Marine aerosol samples were collected along Florida beaches with high-volume air samplers

(TE-5000, Tisch Environmental Inc., Village of Cleaves, OH, USA) fitted with 20 cm × 28

cm glass fibre filters (Whatman EPM 2000, Maidstone, England) (Pierce et al. 2003, 2005).

Toxin-containing aerosol particle size was determined with a 5-stage, high-volume cascade

impactor, according to the procedures of Cheng et al. (2005). A portable, solar powered weather

station also was deployed to provide wind speed and direction, temperature and relative

humidity (Complete Weather Station, Davis Instruments, Hayward, CA, USA). PbTx in marine

aerosol were recovered from the glassfibre filters by extraction for 12 h in acetone using a

Soxhlet apparatus and transferred to methanol for LC–MS analysis as above (Pierce et al.

2005).

Shellfish toxins

Clams (Merceneria merceneria-campenchenesis) and oysters (Crassostrea virginica) were

collected from a common site in Sarasota Bay, Florida, before, during and after K. brevis

blooms. Four-litre water samples were collected concurrently with shellfish for K. brevis cell

counts and PbTx analyses. PbTx and metabolites were extracted from 1 g aliquots of shellfish

tissue in acetone with additional separation and clean up by solid-phase extraction in

preparation for LC/MS analysis at the US Food and Drug Administration Gulf Coast Seafood

Lab, Dauphin Isl., AL (Plakas et al. 2002). Toxicity of the shellfish tissue was determined by

mouse bioassay by injecting diethyl ether extracts of 100 g samples of homogenized shellfish

meat into mice (American Public Health Association 1970). This assay was performed by the

Florida Fish and Wildlife Research Institute, St. Petersburg, FL, reported as mouse units/100

g (Pierce et al. 2004). LC–MS analysis on shellfish tissue was performed using Agilent

Technologies (Palo Alto, CA) Model 1100 LC system and Thermo Finnigan (San Jose, CA)

Navigator AQA MS detector with electrospray ion source, on a YMC J’Sphere ODS-L80 S-4,

2.0 × 250 mm column (YMC Inc., Wilmington, NC) under gradient conditions (Plakas et al.

2002). MS Standards of pure PbTx-2 and PbTx-3 were provided by the Center for Marine

Science, UNC, Wilmington.

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Results

PbTx composition

Results of PbTx composition in selected water samples collected along the south-west Florida

coast are given in Table 1, along with corresponding K. brevis cell counts. In all instances, the

total brevetoxin concentrations were sufficient to cause localized fish kills, NSP to exposed

filter-feeding molluscs and respiratory irritation from aerosolized brevetoxins. These data

provide a representation of the composition, concentration and distribution of PbTx that impact

the south-west Florida coast during red tide events. Results of intra and extracellular toxin

studies are shown in Table 2 for PbTx analyses in water samples collected in Sarasota Bay

during a K. brevis bloom from 6 July to 23 November, 2005. These results show the conversion

of PbTx-2 to PbTx-3 after rupture (lysing) of K. brevis cells, and the persistence of PbTx-3 in

the water after the cell count has diminished to below detectable levels.

Aerosol toxins

Results of PbTx monitored in surf water and marine aerosol along a Florida beach during an

on-shore red tide bloom (Table 3) show changes in relative concentrations of the major

brevetoxin compounds during the transition from water to aerosol (Pierce et al. 2005).

Shellfish (NSP) toxins

Results of LC–MS analysis of NSP-contaminated shellfish (clams and oysters) are given along

with the toxicity as mouse units (Table 4). Also provided are the K. brevis cell counts and PbTx

composition in ambient water samples to provide the composition of the PbTx source. The

LC–MS analyses of shellfish tissue were provided to identify the chemical components

primarily responsible for NSP toxicity.

Discussion

PbTx composition

The three most abundant PbTx in south-west Florida red tide blooms (Table 1) were the parent

algal toxins, PbTx-1 and PbTx-2, and PbTx-3, the primary reduction product of PbTx-2. Also

present was the antagonist, brevenal (Bourdelais et al. 2005). The presence of brevenal is

significant because it inhibits the toxicity of PbTx by competitively replacing brevetoxins at

the sodium channel-binding site. The concentration of brevenal required to inhibit toxicity in

fish in the natural environment has not yet been established. The high variability observed for

each toxin and for K. brevis cell counts is a reflection of the variability of red tide phytoplankton

blooms. The amount of K. brevis cells observed were representative of medium to high bloom

conditions as defined by the Florida Fish and Wildlife Research Institute: background 0–1,000;

very low 1,000 < 10,000; low 10,000 < 100,000; medium 100,000 < 1,000,000; high >

1,000,000 cells/l. Therefore, the concentration of PbTx was sufficient to cause fish kills and

respiratory irritation.

Analysis of intracellular and extracellular PbTx (Table 2) provides insight into the most

abundant toxins affecting marine animals according to the route of exposure. These data show

the three most abundant toxins to be PbTx-1, -2 and -3. Most notable is that PbTx-2 was the

primary intracellular PbTx. As toxins were released from the cells, the composition changed

such that the most abundant extracellular toxin was PbTx-3. Extracellular toxins remained in

the water column after detectable levels of K. brevis had gone (Table 2) suggesting the need

for monitoring PbTx concentration as well as K. brevis cell counts for natural resource and

public health protection.

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The average amount of PbTx produced per cell has been observed to be between 8 and 30 pg/

cell (Baden and Tomas 1988; Pierce et al. 2001). Natural background concentrations of 1,000

cells/l or less result in potential PbTx concentrations from 0 to 30 ng/l with no observable

adverse effects. However, a slight increase to 5,000 cells/l (about 100 ng/l PbTx) is sufficient

to cause filter-feeding shellfish to become toxic for human consumption.

Ichthyotoxicity varies according to the route and rate of exposure and the size and species of

fish. The most ichthyotoxic PbTx is PbTx-1 with a 24-h LD-50 of 3.1 nM (2.7 μg/l), followed

by PbTx-2 at 14.3 nM (12.8 μg/l) and PbTx-3 at 15.8 nM (14.2 μg/l) (Baden 1983; Rein et al.

1994). Subacute exposure of PbTx to the Japanese rice fish, medaka (Oryzias latipes), was

found to produce developmental toxicity in embryos at LD-50 of 4 ng/egg (Coleman and

Ramsdell 2003). These concentrations were well within environmentally relevant amounts to

which fish and fish eggs are exposed, indicating the potential for acute as well as subacute

effects resulting from K. brevis blooms.

Aerosol toxins

Results of PbTx-containing aerosol (Table 3) showed PbTx-3 as the most abundant with less

PbTx-2 and no detectable PbTx-1. A comparison with the source water shows that the most

abundant toxin in water was PbTx-2, followed by PbTx-3 and low concentrations of PbTx-1.

The antagonist, brevenal, was present in water with trace amounts detected in aerosol (Cheng

et al. 2005) indicating possible inhibition of aerosolized PbTx toxicity (Abraham et al. 2005).

It is important to note that on 3/30/03, as the K. brevis cell count and PbTx concentration

increased in the water, the amount of PbTx in marine aerosol dropped drastically. This was a

result of a shift in wind direction from on-shore to along-shore showing the importance of wind

direction and velocity for respiratory impact (Pierce et al. 2005;Cheng et al. 2005). Particle

size distribution analyses of PbTx-containing marine aerosol provided insight into the actual

dosages to which study subjects were exposed: upper airway (75–84%) and the lower airways

(2–6%) (Cheng et al. 2005). Most significant was the observation that subjects with asthma

experienced both upper and lower airway symptoms as well as changes in pulmonary function,

even when exposed to low to moderate levels of aerosolized PbTx while healthy subjects did

not exhibit reduced pulmonary function (Fleming et al. 2005;Backer et al. 2005).

Studies of bronchoconstriction caused by inhalation of PbTx-2 and PbTx-3 in the guinea pig,

showed PbTx-3 to be the agent primarily responsible for respiratory irritation during episodes

of Florida red tide (Baden et al. 1982). Increased sensitivity of asthmatics to inhaled PbTx was

confirmed by exposing asthmatic sheep to environmentally relevant concentrations of PbTx-3

(Abraham et al. 2005). The seriousness of public health-related effects from red tides was

brought to light through a review of emergency room admittance records that revealed a 54%

increase in cases of respiratory-related hospital emergency room admissions of coastal

residents during an intensive red tide period as compared to similar periods with no red tide

activity (Kirkpatrick et al. 2006).

Shellfish (NSP) toxins

Analysis of NSP-contaminated shellfish tissue from Sarasota Bay showed that the parent algal

toxins (PbTx-1, -2, -3, etc., defined here as brevetoxins produced in K. brevis cells) were not

detected in shellfish tissue, except for one oyster sample that contained 0.38 μg PbTx-3/g tissue.

The primary compounds observed in shellfish were PbTx-conjugates, identified by LC–MS

(m/z 1,018, 1,034, 990 and 1,006) produced by metabolic action of shellfish on the algal toxins.

These compounds included the cysteine-PbTx-2 conjugate (m/z 1,018) and its sulfoxide

product (m/z 1,034), along with cysteine-PbTx-1 conjugate (m/z 990) and its sulfoxide product

(m/z 1,006) (Poli et al. 2000; Plakas et al. 2002; Wang et al. 2004).

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These results (Table 4), show that the oysters exhibited rapid accumulation and reduction in

the concentration of metabolites, whereas clams exhibited slower rate of accumulation with

longer persistence. Also, oysters exhibited a more rapid onset of toxicity than clams, whereas

clams retained their toxicity longer than oysters after the red tide cells diminished to

background levels. The more rapid rate of accumulation and toxicity in oysters reflects their

higher filtration rate. These results suggest that the two species may be producing different

concentrations (and possibly different compounds) of NSP-toxic components. Results indicate

that shellfish exhibited toxic levels of NSP compounds once the K. brevis cell counts exceeded

5,000 cells/l. Although clams and oysters were toxic by mouse bioassay, little or no parent

PbTx was detected in the tissue, implicating PbTx-metabolites as likely agents contributing to

NSP toxicity (Plakas et al. 2004;Wang et al. 2004). It is important to note that PbTx-neurotoxins

persisted in the water after K. brevis cell counts dropped to undetectable (background) levels

and that shellfish remained toxic, as observed by mouse bioassay (>20 MU/100 g tissue), for

about 4 weeks following the bloom, indicating a persistent risk to public health as well as to

the marine ecosystem (Pierce et al. 2004).

Ecosystem effects

The Florida red tide organism, K. brevis, is part of the natural phytoplankton community along

the south-west Florida coast. However, recent intensive and frequent blooms have raised

speculation that human activities are generating excessive nutrient runoff resulting in bloom

conditions that exceed the natural balance. Whatever the cause, the south-west Florida coastal

ecosystem has, for years, experienced episodes of severe stress from K. brevis red tide blooms.

This stress is manifest as massive fish kills, marine mammal, sea turtle and sea bird mortalities,

invertebrate mortalities and severe respiratory effects.

Although acute effects from red tides are obvious, little is known about long-term exposure to

sublethal concentrations such as survival and development of vertebrate and invertebrate larvae

(Leverone et al. 2006). Trophic transfer and accumulation of PbTx and toxic analogues

produces toxic stress at various trophic levels, also providing reservoirs of neurotoxins for

continuous, long-term exposure of marine animals and humans (Tester et al. 2000; Flewelling

et al. 2005).

In addition to direct impacts from red tide neurotoxins, oxygen depletion creates stress

especially on benthic organisms such as sea grass and patch reef communities, requiring years

for recovery (Simon and Dauer 1972; Steidinger et al. 1973). Other indirect stresses include

pathogenic bacteria that have been documented in HABs (Buck and Pierce 1989; Epstein

1995; Landsberg 1997; Douchette et al. 1998). PbTx suppression of mammalian immune

function has been implicated in mass mortalities of both dolphins and manatees (Geraci

1989; Bossart et al. 1998; Sayer et al. 2005). These hypotheses have been supported by a

significant reduction in proliferation of manatee lymphocytes in cell culture exposed to 400

ng/ml PbTx (Walsh et al. 2005).

The extensive evidence for frequent and severe impacts, both acute and subacute, of PbTx and

PbTx-analogues on marine life and public health along the Florida Gulf coast points to the

need for recognition of these biotoxins as significant chemical stressors within south-west

Florida coastal ecosystems. To address these concerns, an ecosystem-based approach is needed

to investigate the acute and subacute impacts resulting from K. brevis blooms.

Acknowledgements

Studies from which data were presented were funded by the following agencies: PbTx composition along the southwest Florida coast, FWCC, Grant No. 04089; Aerosolized PbTxs, NIEHS, 5PO-1 ES010594-05; Shellfish NSP toxins,

NOAA-ECO-HAB Award No. NA030S4780187.

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Fig. 1.

Structures of the two major types of brevetoxin compounds (Poli et al. 1986)

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Table 1

Brevetoxin composition (

μg/l) and K. brevis cell counts (cells/ml) from water samples collected along the south-west Florida coast during

the January through February 2005 red tide bloom

Location PbTx-1 PbTx-2 PbTx-3 Brevenal Cells/mlI 1.18 ± 0.89 17.80 ± 10.97 2.24 ± 0.60 0.57 ± 0.45 813 ± 519II 0.98 ± 1.50 11.31 ± 11.46 0.46 ± 0.70 0.70 ± 0.75 736 ± 682III 1.09 ± 0.67 15.05 ± 8.31 3.98 ± 3.01 0.91 ± 0.56 1,184 ± 730IV 0.65 ± 0.93 8.84 ± 10.72 3.96 ± 3.36 0.74 ± 1.10 1,045 ± 1,651V 1.15 ± 1.41 13.22 ± 8.04 0.49 ± 0.34 1.38 ± 1.50 340 ± 312

I Sarasota Bay; II Tampa to Venice; III Venice to Ft. Myers; IV Ft. Myers to Naples; FL Keys. Mean ± SD

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Table 2

Intracellular and extracellular PbTx (

μg/l) recovered from Karenia brevis blooms in Sarasota Bay, 7/6/05 through 11/3/05

Date Cells/l Karenia brevis

Pbtx-1 Pbtx-2 Pbtx-3Incel Excel Incel Excel Incel Excel

7/6/05 357,333 0.12 0.08 1.70 2.49 0.00 1.837/11/05 1,404,333 0.24 0.49 3.33 7.76 0.65 0.897/18/05 419,333 0.16 0.10 3.46 3.29 0.27 6.237/25/05 105,333 0.12 0.00 1.22 0.48 0.00 1.308/2/05 8,000 0.00 0.00 0.00 0.31 0.00 1.088/18/05 588,000 0.21 0.23 2.98 3.19 0.11 2.269/6/05 661,333 0.38 0.10 5.06 1.62 0.12 2.439/19/05 545,000 0.24 0.14 4.42 2.42 0.30 3.3210/4/05 33,333 0.00 0.00 0.08 0.39 0.02 1.9710/17/05 1,333 0.00 0.00 0.00 0.00 0.00 0.2411/3/05 0 0.00 0.00 0.00 0.00 0.00 0.23

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Table 3

Brevetoxin composition and Karenia brevis cells/l in near shore water (

μg/l) and marine aerosol (air)(ng/m3) samples collected along

Siesta Beach, Florida, 3/29 and 3/30/03

Date Cells/l Karenia brevis

Pbtx-1 Pbtx-2 Pbtx-3Water Air Water Air Water Air

3/29 am 225,000 0.05 0.15 3.02 9.16 1.18 23.943/29 pm 152,000 0.00 0.00 1.69 5.16 1.12 20.213/30 am 591,800 0.32 0.00 10.17 1.65 1.40 3.483/30 pm 903,170 0.42 0.00 11.04 0.01 2.62 0.54

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Table 4

Changes in PbTx-conjugate composition of NSP-contaminated oyster and clam tissue, toxicity by mouse units and Karenia brevis cell

counts and PbTxμg/l in ambient water samples, collected before, during and following a red tide bloom in Sarasota Bay, Florida, 1/22/04–4/14/04

Date Sample m/z 1,018 m/z 1,034 m/z 990 m/z 1,006 MU/100 g Cells/l PbTx-μg/l1/22 Oyst 3.44 0.75 0.54 0.37 <20 5,000 0.20

Clam 1.87 0.64 0.60 0.40 <20

2/4 Oyst 12.65 1.31 0.71 nd 32.1 73,000 3.60

Clam 2.12 0.68 0.64 0.41 <20

2/18 Oyst 25.78 2.02 1.44 nd 97.7 131,000 3.30

Clam 4.63 1.48 1.08 0.47 78.2

3/4 Oyst 12.44 1.36 0.89 nd 35.6 3,000 3.30

Clam 4.26 1.08 1.01 0.53 66.7

3/17 Oyst 10.73 1.52 0.97 0.45 22.1 0 0.50

Clam 3.22 1.51 0.93 0.52 41.7

3/31 Oyst 4.12 0.90 0.59 nd <20 0 0.00

Clam 7.42 1.29 1.15 0.43 <20

4/14 Oyst 2.75 0.64 0.46 tr <20 0 0.00

Clam 2.25 1.21 0.68 0.42 <20

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