In the last two decades, the health risk associated with the presence of cyanobacteria in lakes, rivers, reservoirs, and ponds has been widely recognized. At least 46 toxin-producing cyanobacterial species were identified (Apeldoorn et al. 2007). Moreover, both toxic and non-toxic strains were identified within a given species in the same habitat (Osswald et al. 2007). Simultaneous production of several variants of hepatotoxic microcystins, the most common group of cyanotoxins, and less common neurotoxic anatoxin-a was also reported (Rantala et al. 2006).
Microcystins are persistent compounds and they accumulate in different compartments of aquatic environments, including fish, mussels and sediment. These compounds are highly toxic and different exposure routes are possible (Chorus 2012). The World Health Organization established a guideline value for the daily intake of microcystin-LR (MC-LR), i.e. the most common and most toxic MC congener (WHO, 2011). In many countries, contact with cyanobacteria at bathing sites is the most probable route of exposure to cyanotoxins and can result in health problems, particularly in children. According to the European Bathing Water Directive 2006/7/EC, when the bathing water profile indicates a potential for cyanobacterial proliferation, an appropriate monitoring program should be implemented (Directive 2006/7/EC).
In Russia, there are over 2.7 million lakes with a total water surface area of about 409 000 km2. The lake area covers about 4% of the territory of the Russian Federation. Most lakes (98%) are small (with the surface area below 1 km2) and shallow (average depth 1.0-1.5 m). Many lakes (14%) are situated in Northwestern Russia. According to hydrobiological data, green algae, diatoms and cyanobacteria dominate in the lakes (Trifonova & Pavlova 2008).
Reports on the occurrence of cyanobacteria and cyanotoxins in Russia are scarce and limited to several presentations at international conferences. Occasional studies on cyanotoxins were conducted in Central Russia, in particular in Volga Reservoirs (Korneva et al. 2014; Sidelev et al. 2015) and Lake Nero (Babanazarova et al. 2011), in lakes of Northwestern Russia, including Lake Ladoga (Gromov et al. 1996) and Karelian Isthmus lakes (Voloshko et al. 2008), and Lake Baikal in East Siberia (Belykh et al. 2015). Different analytical methods (PCR, ELISA, LC-MS) were used in the above-mentioned works to detect and quantify the microcystins. The obtained results showed the presence of toxigenic species and cyanotoxins in the studied water bodies.
Cyanobacterial blooms have also been reported from water bodies located in Saint Petersburg region. Limnologic studies conducted in these lakes during the last 50 years showed a shift in the dominant species from diatoms to cyanobacteria (Trifonova & Pavlova 2008). In addition, an increase in the range and intensity of phytoplankton blooms was observed and attributed to anthropogenic impact and increasing eutrophication. It was shown that phytoplankton biomass in Sestroretskij Razliv Lake increased six to seven times for the last two decades (Trifonova & Pavlova 2008).
Our preliminary studies conducted in two eutrophic lakes located in the territory of Saint Petersburg and Leningrad Region, Razliv and Suzdal, documented the dominance of
This paper presents the results of the regular research performed for the first time on the toxin production by cyanobacteria occurring in freshwater reservoirs located in Northwestern Russia, Razliv and Suzdal. The research covered a 3-year period (2010-2012), from May to October. Data on phytoplankton composition, as well as on intra- and extracellular concentration of cyanotoxins were collected. The aim of the study was to assess the potential threat to water users related to the occurrence of toxic cyanobacteria at the examined bathing sites.
The present study was conducted in two shallow, humic, eutrophic lakes with a different nutrient status – Lake Sestroretskij Razliv (Razliv) and Lower Suzdal Lake (Suzdal) – located in Saint Petersburg region, Russia, and used for recreational purposes. Razliv is a large artificial reservoir with a surface area of 1100 ha and average depth of 1.6 m. The surface area of Suzdal is 97 ha and the mean depth is 3.0 m.
Surface water samples (1 l) were collected from these lakes with plastic bottles and phytoplankton biomass was collected with a net (mesh size of 85 μm). Sampling was performed every 2 weeks from May to October in 2010-2012. Altogether, 45 water samples and 40 phytoplankton samples were collected from the two lakes. The water samples in 1 l bottles were fixed with a Lugol-formalin solution. Cyanobacterial material from net samples was transported to a laboratory in screw-cap tubes (Axigen, California, USA) and immediately frozen at –20°C until freeze-drying.
Qualitative and quantitative analyses of phytoplankton were carried out under a light microscope (Mikromed-3, LOMO, Saint Petersburg, Russia). The volume of the counting chamber Uchinskaya was 0.1 ml. The biovolume of algae and cyanobacteria was calculated using species-specific geometric formulas (Olenina et al. 2006). The phytoplankton biomass was determined from the total volume of algae according to the counted cell density and the measured average cell density.
Microcystin standards (MC-LR, MC-RR, and MC-YR) were purchased from Sigma-Aldrich (St. Louis, MO, USA) and (+/-) anatoxin-a fumarate was obtained from Tocris Bioscience (Bristol, UK). Acetonitrile (HPLC-grade) and methanol (LiChrosolv hypergrade for LC-MS) were purchased from Merck (Darmstadt, Germany). Water was purified to 18.2 MΩ cm−1 in a Millipore Direct-Q water purification system (Bedford, MA, USA). Formic acid was obtained from Fluka Chemika (Buchs, Switzerland). Membrane filter discs (nylon 66, 47-mm diameter) were obtained from Supelco (Bellefonte, PA).
Water samples (1 l) for the analysis of extracellular cyanotoxins (AN and MCs) were filtered on a Supelco mobile-phase filtration apparatus (nylon-66 membrane filter discs, 47-mm diameter, Supelco, Bellefonte, PA). Solid phase extraction (SPE) with Oasis HLB cartridges (60 or 200 mg, Waters, Milford, Massachusetts, USA) was used. The toxins were eluted from the cartridges with 10 ml methanol. The collected extracts were dried using a rotary evaporator and stored at –20°C until further analysis. The dried extracts were reconstituted in 1 ml of 80% aqueous methanol and centrifuged (CM-50 centrifuge, ELMI, Riga, Latvia) at 14 000 rpm for 10 min prior to analysis by high-performance liquid chromatography/high-resolution tandem mass spectrometry (LC-HR-MS/MS).
For the extraction of biomass-bound (intracellular) MCs and anatoxin-a, the dry lyophilized cells (10-30 mg) were treated twice with 1 ml of 75% aqueous methanol by sonication in an ultrasound bath (US) for 15 min, and then centrifuged at 14 000 rpm for 15 min. The obtained extracts were combined.
The LC-MS experiments were carried out in the Accela HPLC system (Thermo Finnigan, San Jose, CA, USA) coupled with a Hybrid Ion Trap-Orbitrap Mass Spectrometer – LTQ Orbitrap XL (Thermo Fisher Scientific, San Jose, USA) with the electrospray interface. Separation of the toxins was performed on a Thermo Hypersil Gold RP C18 column (100 × 3 mm, 3 μm) with a Hypersil Gold drop-in guard column (Thermo Fisher Scientific). The mobile phase consisted of water (solvent A) and acetonitrile (solvent B), both containing 0.05% formic acid. The gradient program started at 5% B (held for 10 min), then the content of phase B increased to 75% over 18 min (held for 3 min), and then increased to 95% B over 1 min (held for 5 min). The flow rate was 0.2 ml min−1. The column temperature was 40°C and the injection volume was 25 μl for water sample extracts and 10 μl for biomass sample extracts.
The MS conditions using electrospray ionization were as follows: Ion Spray voltage 3.2 kV, capillary Voltage 20 V, ion-transfer capillary temperature 320°C, tube lens 130 V. The mass spectrometer operated in the positive ion mode at a resolving power of 30 000. A scan function (
For quantitative analysis of cyanotoxins, the calibration curves for standards solutions of AN and MC-LR, -RR, and -YR were determined (
Measurements of the concentrations of the singly charged MC variants, whose standards were not available, were based on the standard curve for MC-LR. As there were large variations in the MS response of the singly charged MCs and the doubly charged ions of different MC-RR congeners, the concentrations of their desmethylated (dm) and methylated counterparts were determined on the basis of the curve drawn for
Major hydrochemical parameters for both lakes were similar. The maximum gradients for ammonia nitrogen (0.6-2.0 mg N l−1) and phosphates (0.002-0.600 mg P l−1) were typical of eutrophic lakes of Northwestern Russia. During the study period, the pH values in the lakes changed within the range of 6.2-8.5 in Razliv, and within the range of 7.6-9.0 in Suzdal.
The seasonal cyanobacterial dynamics in Razliv and Suzdal was determined based on the analysis of 41 phytoplankton samples. The total number of phytoplankton taxa identified in the collected samples was 138. The identified species belonged to nine taxonomic groups of algae, with the dominance of green algae (41% of the total number of species), cyanobacteria (18%), euglenoids (13%), and diatoms (11%). Among green algae, the family Chlorococcoaceae was represented by the largest number of species. The data on the abundance and biomass of the observed taxonomic groups are presented in supplementary tables (Supplementary tables S1A-S1F).
Abundance and biomass of the observed taxonomic groups in the studied lakes in the period of 2010-2012
Sestroretskij Razliv Lake, 2010 | |||||
---|---|---|---|---|---|
Date | Groups | Abundance (×10 cell l ) | Abundance (%) | Biomass (mg l ) | Biomass (%) |
16-Jun-2010 | Cyanoprokaryota | 60.8 | 96 | 4.47 | 42 |
Cryptophyceae | 1.1 | 2 | 2.70 | 26 | |
All groups | 63.3 | 100 | 10.55 | 100 | |
1-Jul-2010 | Cyanoprokaryota | 6.4 | 41 | 0.73 | 2 |
Cryptophyceae | 1.8 | 12 | 3.73 | 11 | |
Diatomophyceae | 5.0 | 32 | 9.80 | 29 | |
Chlorophyta | 2.3 | 15 | 19.47 | 57 | |
All groups | 15.5 | 100 | 34.13 | 100 | |
23-Jul-2010 | Cyanoprokaryota | 8.3 | 43 | 3.19 | 9 |
Chlorophyta | 10.9 | 56 | 30.89 | 88 | |
All groups | 19.4 | 100 | 35.09 | 100 | |
05-Aug-2010 | Cyanoprokaryota | 72.2 | 86 | 13.96 | 19 |
Chlorophyta | 10.0 | 12 | 56.71 | 75 | |
All groups | 83.5 | 100 | 75.26 | 100 | |
16-Aug-2010 | Cyanoprokaryota | 62.5 | 67 | 5.44 | 12 |
Chlorophyta | 12.0 | 13 | 32.28 | 70 | |
All groups | 93.7 | 100 | 46.36 | 100 | |
21-Sep-2010 | Cyanoprokaryota | 15.0 | 89 | 1.05 | 19 |
Cryptophyceae | 1.5 | 3 | 9.05 | 63 | |
All groups | 16.9 | 100 | 5.47 | 100 | |
7-Oct-2010 | Cyanoprokaryota | 0.2 | 5 | 0.02 | 0.4 |
Cryptophyceae | 0.8 | 30 | 1.57 | 29 | |
Diatomophyceae | 2.1 | 65 | 2.98 | 56 | |
All groups | 3.2 | 100 | 5.34 | 100 |
Sestroretskij Razliv Lake, 2011 | |||||
---|---|---|---|---|---|
Date | Groups | Abundance (×10 cell l ) | Abundance (%) | Biomass (mg l ) | Biomass (%) |
2-Jun-2011 | Cyanoprokaryota | 16.4 | 56 | 2.54 | 33 |
Cryptophyceae | 10.7 | 37 | 2.14 | 28 | |
Diatomophyceae | 1.0 | 4 | 1.51 | 20 | |
All groups | 29.2 | 100 | 7.61 | 100 | |
27-Jun-2011 | Cyanoprokaryota | 15.7 | 84 | 2.55 | 29 |
Cryptophyceae | 1.6 | 9 | 2.93 | 33 | |
Chlorophyta | 0.8 | 4 | 2.13 | 24 | |
All groups | 18.8 | 100 | 8.91 | 100 | |
18-Jul-2011 | Cyanoprokaryota | 793.9 | 99.9 | 61.94 | 99 |
All groups | 794.2 | 100 | 62.86 | 100 | |
01-Aug-2011 | Cyanoprokaryota | 98.0 | 99 | 15.22 | 82 |
All groups | 99.2 | 100 | 18.54 | 100 | |
22-Aug-2011 | Cyanoprokaryota | 33.2 | 89 | 2.19 | 42 |
Cryptophyceae | 0.2 | 0.6 | 0.66 | 12 | |
Chlorophyta | 3.5 | 9 | 0.90 | 17 | |
All groups | 37.5 | 100 | 5.27 | 100 | |
19-Sep-2011 | Cyanoprokaryota | 74.4 | 99.6 | 5.83 | 88 |
All groups | 74.7 | 100 | 6.61 | 100 |
Sestroretskij Razliv Lake, 2012 | |||||
---|---|---|---|---|---|
Date | Groups | Abundance, (×106 cell l–1) | Abundance, (%) | Biomass, (mg l–1 | Biomass, % |
28-May-2012 | Cyanoprokaryota | 19.3 | 66 | 2.33 | 9 |
Cryptophyceae | 1.9 | 7 | 5.92 | 23 | |
Diatomophyceae | 6.8 | 23 | 17.14 | 65 | |
All groups | 29.5 | 100 | 26.29 | 100 | |
14-Jun-2012 | Cyanoprokaryota | 103.3 | 87 | 7.11 | 27 |
Diatomophyceae | 14.0 | 12 | 16.04 | 62 | |
All groups | 117.9 | 100 | 25.99 | 100 | |
24-Jun-2012 | Cyanoprokaryota | 4.8 | 65 | 0.45 | 9 |
Cryptophyceae | 0.2 | 3 | 0.63 | 12 | |
Diatomophyceae | 2.2 | 30 | 2.86 | 56 | |
Chlorophyta | 0.2 | 2 | 1.06 | 21 | |
All groups | 7.5 | 100 | 5.15 | 100 | |
05-Jul-2012 | Cyanoprokaryota | 16.5 | 97 | 2.10 | 56 |
Cryptophyceae | 0.3 | 2 | 0.92 | 25 | |
All groups | 17.0 | 100 | 3.72 | 100 | |
20-Jul-2012 | Cyanoprokaryota | 58.7 | 99 | 4.84 | 77 |
All groups | 58.9 | 100 | 6.29 | 100 | |
02-Aug-2012 | Cyanoprokaryota | 20.8 | 98 | 1.43 | 56 |
Diatomophyceae | 0.4 | 2 | 0.71 | 28 | |
All groups | 21.3 | 100 | 2.55 | 100 | |
13-Aug-2012 | Cyanoprokaryota | 19.0 | 95 | 1.44 | 35 |
Cryptophyceae | 0.3 | 1 | 0.93 | 23 | |
Diatomophyceae | 0.6 | 3 | 0.91 | 22 | |
All groups | 20.0 | 100 | 4.08 | 100 | |
Cyanoprokaryota | 173.3 | 97 | 11.34 | 54 | |
03-Sep-2012 | Cryptophyceae | 1.6 | 1 | 2.75 | 13 |
Diatomophyceae | 2.5 | 1 | 5.58 | 27 | |
All groups | 178.1 | 100 | 20.85 | 100 | |
Cyanoprokaryota | 68.2 | 93 | 4.62 | 29 | |
13-Sep-2012 | Diatomophyceae | 4.5 | 6 | 9.60 | 60 |
All groups | 73.0 | 16.09 | 100 | 100 | |
Cyanoprokaryota | 29.6 | 98 | 1.97 | 61 | |
24-Sep-2012 | Diatomophyceae | 0.7 | 2 | 0.88 | 27 |
All groups | 30.4 | 100 | 3.24 | 100 |
Lower Suzdal Lake, 2010 | |||||
---|---|---|---|---|---|
Date | Groups | Abundance (×10 cell l ) | Abundance (%) | Biomass (mg l ) | Biomass (%) |
11-Jun-2010 | Cyanoprokaryota | 0.0 | 0.5 | 0.007 | 0.1 |
Diatomophyceae | 5.6 | 98 | 11.0 | 96 | |
All groups | 5.8 | 100 | 11.43 | 100 | |
28-Jun-2010 | Cyanoprokaryota | 171.5 | 99 | 13.57 | 72 |
All groups | 174.1 | 100 | 18.80 | 100 | |
15-Jul-2010 | Cyanoprokaryota | 103.3 | 98 | 6.87 | 35 |
Dinophyta | 0.2 | 0.1 | 4.39 | 22 | |
Euglenophyta | 1.6 | 2 | 6.90 | 35 | |
All groups | 105.8 | 100 | 19.52 | 100 | |
02-Aug-2010 | Cyanoprokaryota | 4.6 | 85 | 0.30 | 16 |
Dinophyta | 0.0 | 0.2 | 0.59 | 31 | |
Euglenophyta | 0.1 | 2 | 0.50 | 26 | |
Chlorophyta | 0.7 | 13 | 0.50 | 26 | |
All groups | 5.4 | 100 | 1.95 | 100 | |
09-Sep-2010 | Cyanoprokaryota | 1.9 | 71 | 0.13 | 2 |
Dinophyta | 0.0 | 2 | 3.01 | 51 | |
Euglenophyta | 0.5 | 19 | 1.65 | 28 | |
Chlorophyta | 0.2 | 7 | 1.05 | 18 | |
All groups | 2.6 | 100 | 5.90 | 100 | |
27-Sep-2010 | Cyanoprokaryota | 0.5 | 8 | 0.03 | 0.3 |
Euglenophyta | 1.8 | 31 | 5.48 | 50 | |
Diatomophyceae | 0.5 | 8 | 1.15 | 10 | |
Chlorophyta | 2.9 | 50 | 4.07 | 37 | |
All groups | 5.8 | 100 | 11.01 | 100 |
Lower Suzdal Lake, 2011 | |||||
---|---|---|---|---|---|
Date | Groups | Abundance (×10 cell l ) | Abundance (%) | Biomass (mg l ) | Biomass (%) |
06-Jun-2011 | Cyanoprokaryota | 6.8 | 81 | 0.43 | 7 |
Euglenophyta | 0.7 | 8 | 1.96 | 31 | |
Diatomophyceae | 0.5 | 7 | 1.13 | 18 | |
Chlorophyta | 0.4 | 4 | 2.06 | 33 | |
All groups | 8.4 | 100 | 6.24 | 100 | |
04-Jul-2011 | Cyanoprokaryota | 127.1 | 99 | 7.45 | 76 |
All groups | 128.9 | 100 | 9.76 | 100 | |
11-Jul-2011 | Cyanoprokaryota | 50.5 | 97 | 1.78 | 30 |
Dinophyta | 0.01 | 0.1 | 1.15 | 19 | |
Cryptophyceae | 0.5 | 1 | 0.90 | 15 | |
Chlorophyta | 0.7 | 1.4 | 1.54 | 26 | |
All groups | 51.9 | 100 | 5.87 | 100 | |
21-Jul-2011 | Cyanoprokaryota | 211.7 | 99 | 16.72 | 80 |
All groups | 212.9 | 100 | 20.92 | 100 | |
05-Sep-2011 | Cyanoprokaryota | 436.9 | 99 | 7.38 | 58 |
Dinophyta | 0.0 | 0.01 | 2.37 | 19 | |
All groups | 438.6 | 100 | 12.68 | 100 | |
25-Sep-2011 | Cyanoprokaryota | 346.6 | 99 | 8.78 | 82 |
All groups | 347.1 | 100 | 10.65 | 100 |
Lower Suzdal Lake, 2012 | |||||
---|---|---|---|---|---|
Date | Groups | Abundance (×10 cell l ) | Abundance (%) | Biomass (mg l ) | Biomass (%) |
05-Jun-2012 | Cyanoprokaryota | 41.6 | 97 | 2.75 | 40 |
Euglenophyta | 0.3 | 1 | 1.20 | 17 | |
Diatomophyceae | 1.0 | 2 | 1.66 | 24 | |
Chlorophyta | 0.1 | 0.2 | 1.26 | 18 | |
All groups | 43.1 | 100 | 6.89 | 100 | |
18-Jun-2012 | Cyanoprokaryota | 309.7 | 98 | 21.02 | 65 |
Diatomophyceae | 6.5 | 2 | 6.92 | 22 | |
All groups | 317.6 | 100 | 32.16 | 100 | |
06-Jul-2012 | Cyanoprokaryota | 105.9 | 97 | 7.55 | 58 |
Diatomophyceae | 2.8 | 2.5 | 2.52 | 26 | |
All groups | 109.5 | 100 | 13.01 | 100 | |
23-Jul-2012 | Cyanoprokaryota | 396.6 | 97 | 26.03 | 41 |
Dinophyta | 0.1 | 0.03 | 13.14 | 21 | |
Cryptophyceae | 3.4 | 1 | 9.75 | 15 | |
Diatomophyceae | 5.6 | 1 | 10.93 | 17 | |
All groups | 407.5 | 100 | 64.17 | 100 | |
30-Jul-2012 | Cyanoprokaryota | 284.9 | 96 | 18.64 | 27 |
Dinophyta | 0.3 | 0.1 | 26.89 | 39 | |
Diatomophyceae | 9.4 | 3 | 18.38 | 26 | |
All groups | 297.4 | 100 | 69.47 | 100 | |
16-Aug-2012 | Cyanoprokaryota | 6.8 | 42 | 0.44 | 1 |
Dinophyta | 0.3 | 2 | 27.74 | 51 | |
Cryptophyceae | 7.4 | 45 | 21.99 | 41 | |
All groups | 16.2 | 100 | 54.04 | 100 | |
Cyanoprokaryota | 5.5 | 92 | 0.36 | 4 | |
06-Sep-2012 | Dinophyta | 0.1 | 1 | 8.46 | 88 |
All groups | 5.9 | 100 | 9.56 | 100 |
Both lakes were described as β-mezosaprobic. During the study period, the phytoplankton biomass varied significantly within and between the seasons and lakes (Fig. 1). Among the identified species, the following were most numerous:
The highest mean seasonal cyanobacterial biomass was recorded in 2012 in Suzdal (10.97 mg l−1) and in 2011 in Razliv (15.05 mg l−1). The contribution of cyanobacteria to the total phytoplankton biomass varied from 0.4% (0.02 mg l−1) to 99% (61.94 mg l−1) in Razliv and from 0.1% (0.01 mg l−1) to 41% (26.03 mg l−1) in Suzdal (Fig. 1, Supplementary tables S1A-S1F).
In 2010 and 2012,
The studies carried out in 2010-2012 showed the occurrence of cyanotoxins both in Razliv and in Suzdal. The concentrations of microcystins exceeding the value of ≥ 0.1 μg l−1 for the extracellular fraction, or 0.1 mg g−1 on a dry-weight (DW) basis for the intracellular fraction, were determined in 54 water and biomass samples (59% of all the collected samples). Extracellular microcystins were detected in 25 of 46 water samples (54% of the water samples) (Tables 1, 2, Supplementary tables S2-S7). AN was present only in 5 water samples from Suzdal (Table 2, Supplementary tables S5, S6).
Concentration of extracellular and intracellular cyanotoxins, three main toxin variants, and biomass of dominant species in samples from Lake Sestroretskij Razliv. MC = microcystin, dm = desmethyl, didm = double desmethyl, *denotes trace concentration (below 50 pg per injection), nd = values below LOD, DW = on a dry-weight basis
Sampling period (number of events) | Concentration of extracellular cyanotoxins in water (µg l ) | Concentration of intracellular cyanotoxins in biomass (µg g DW) | Dominant species according to the number of cells | Cyanobacterial biomass (mg l ) | ||
---|---|---|---|---|---|---|
Total | Three main toxin variants | Total | Three main toxin variants | |||
2010 | seasonal median 1.61 (min. 0.11, max 41.37, N=8) | seasonal median 132 (min. 8, max 380, N=8) | ||||
June-July (2) | 0.10-0.19 | dmMC-LR (0.01-0.06), MC-LR (0.03-0.15), MC-YR * | 8-51 | MC-RR (4-20), MC-LR (2-20) | 0.73-4.47 | |
July-Aug. (2) | 0.16-2.60 | dmMC-RR (0.01-1.03), MC-LR (0.08-0.87), MC-YR (nd-0.24) | 11-23 | MC-RR (6), didmMC-RR (nd-6) | 3.19-13.96 | |
Aug.-Sept. (3) | 0.61-41.37 | dmMC-RR (0.46-38.54), dmMC-LR (0.05-1.65), MC-LR (0.03-1.41) | 213-380 | MC-RR (51-100), MC-LR (34-80), didmMC-RR (14-104) | 1.00-5.44 | |
Oct. (1) | 13.38 | dmMC-RR (6.54), MC-LR (2.80), MC-RR (2.16) | 255 | dmMC-LR (133), MC-LR (74), dmMC-YR (15) | 0.02 | |
2011 | seasonal median 0.08 (min.< 0.003, max 0.70, N=7) | seasonal median 463 (min. < 0.08, max 2095, N=7) | ||||
June-Sept. (7) | < 0.10-0.70 | MC-RR (nd-0.26), MC-LR (nd-0.21), dmMC-RR (nd-0.28) | < 0.08-2095 | MC-LR (nd-306), MC-YR (nd-345), dmMC-RR (nd-1245) | 2.19-61.94 | |
2012 | seasonal median 0.06 (min.< 0.003, max 1.24, N=9) | seasonal median 490 (min. 45, max 2294, N=8) | ||||
May (1) | 0.06 | MC-LR (0.02), MC-RR (0.04) | 1377 | MC-RR (578), dmMC-RR (349), MC-LR (244) | 2.33 | |
mid-June (1) | 1.24 | MC-RR (0.74), MC-LR (0.50) | 1859 | MC-LR (734), MC-RR (807), MC-LF (112) | 7.11 | |
end of June (1) | 0.12 | MC-LR (0.07), MC-RR (0.05) | 298 | MC-RR (215), MC-LR (78) | 0.45 | |
July (2) | <0.10-0.87 | MC-LR (0.01-0.31), MC-RR (0.03-0.44), MC-YR (0.01-0.06) | 260-489 | MC-LR (51-116), MC-RR (186-334), MC-YR (20-36) | 2.10-4.84 | |
Aug.-Sept. (4) | <0.10-0.92 | MC-LR (nd-0.40), MC-RR (nd-0.29), MC-YR (0.06-0.23) | 45-2294 | MC-RR (6-995), [L-Ser ]MC-RR (nd-973), MC-LR (8-344) | 1.43-11.34 |
Concentration of extracellular and intracellular cyanotoxins, three main toxin variants, and biomass of dominant species in samples from Lower Suzdal Lake. MC = microcystin, AN = anatoxin-a, dm = desmethyl, *denotes trace concentration (below 50 pg per injection), nd = values below LOD, DW = on a dry-weight basis.
Sampling period (number of events) | Concentration of extracellular cyanotoxins in water (µg l ) | Concentration of intracellular cyanotoxins in biomass (µg g DW) | Dominant species according to the number of cells | Cyanobacterial biomass (mg l ) | ||
---|---|---|---|---|---|---|
Total | Three main toxin variants | Total | Three main toxin variants | |||
2010 | seasonal median 0.44 (min. 0.01, max 2.89, N=7) | seasonal median 18 (min. 1, max 234, N=7) | ||||
mid-June (1) | 0.39 | [L-Ser ]-MC-RR (0.18), MC-LR (0,14), dmMC-LR (0.05) | 7 | MC-LR (5), MC-RR (2) | 0.01 | |
end of June-Aug. (4) | <0.10-1.68 | dmMC-RR (0.01-0.36), [L-Ser ]-MC-RR (0.01-0.32), AN (nd-0.54) | 4-234 | MC-RR (2-98), MC-LR (2-7), MC-WR (2-8) | 0.30-13.57 | |
Sept. (2) | 0.56-2.89 | [L-Ser ]MC-RR (0.13-0.87), dmMC-RR (0.26-0.95), dmMC-LR (0.12-0.45) | 1-18 | dmMC-RR (nd-12), dmMC-YR (nd-6) | 0.03-0.13 | |
2011 | seasonal median 0.02 (min. 0.01, max 0.40, N=7) | seasonal median 120 (min.< 0.08, max 700, N=7) | ||||
June-July (4) | <0.10-0.40 | AN (nd-0.27), MC-RR (0.01-0.20), dmMC-RR (nd-0.14) | < 0.08-698 | MC-LR (nd-225), MC-YR (nd-351), MC-LW (4-7), AN (nd-30) | 0.43-16.72 | |
Aug.-Sept. (3) | <0.10-0.24 | AN (nd-0.24), MC-RR*, dmMC-RR* | 121-142 | MC-LR (28-41), MC-RR (31-32), dmMC-RR (34-35) | 7.38-8.78 | |
2012 | seasonal median 0.05 (min.< 0.003, max 0.71, N=8) | seasonal median 250 (min. 50, max 1800, N=8) | ||||
June-July (5) | <0.10-0.70 | dmMC-RR (0.05-0.60), MC-RR (nd-0.22), MC-LR (nd-0.21) | 51-470 | MC-RR (33-318), MC-LR (8-121), dmMC-RR (1-97) | 2.75-26.03 | |
Aug.-Sept. (3) | <0.10 | MC-RR*, MC-LR* | 50-1796 | MC-RR (15-1345), MC-LR (26-353), MC-YR (9-116) | 0.36-0.44 |
Detected concentrations of extracellular MCs in wat er and intracellular MCs in biomass samples, cell number and biomass of obse rved cyanobacterial species in Sestroretskij Razliv Lake in 2010.
Sestroretskij Razliv Lake, 2010 | MC-LR | dmMC-LR | didmMC-LR | [L-Ser7]MC-LR | [L-MeSer][-MC-LR] | MC-RR | dmMC-RR | didm-MC-RR | [L-Ser]-MC-RR | MC-YR | dmMC-YR | MC-LF | MC-HtyR | MC-YA | Total MCs | Cell number of cyanobacterial species, × 106 cells l–1, (N,%) | Biomass of cyanobacterial species, mg l–1, (B,%) | |
---|---|---|---|---|---|---|---|---|---|---|---|---|---|---|---|---|---|---|
16 Jun | Water, µg l–1 | 0.153 | 0.009 | 0.006 | 0.014 | 0.007 | 0.189 | |||||||||||
Bio, µg g–1 dw | 20 | 3 | 3 | 20 | 1 | 1 | 1 | 51 | ||||||||||
01 Jul | Water, µg l–1 | 0.028 | 0.055 | 0.003 | 0.025 | 0.111 | ||||||||||||
Bio, µg g–1 dw | 2 | 2 | 4 | 8 | ||||||||||||||
23 Jul | Water, µg l–1 | 0.054 | 0.028 | 0.012 | 0.094 | |||||||||||||
Bio, µg g–1 dw | 3 | 2 | 6 | 1 | 11 | |||||||||||||
05 Aug | Water, µg l–1 | 0.874 | 0.238 | 0.053 | 0.158 | 1.032 | 0.241 | 0.003 | 2.599 | |||||||||
Bio, µg g–1 dw | 3 | 2 | 1 | 23 | ||||||||||||||
16 Aug | Water, µg l–1 | 0.830 | 0.945 | 0.042 | 0.840 | 38.542 | 0.165 | 0.006 | 41.370 | |||||||||
Bio, µg g–1 dw | 80 | 0 | 100 | 49 | 8 | 19 | 3 | 256 | ||||||||||
06 Sep | Water, µg l–1 | 1.410 | 1.650 | 0.020 | 0.451 | 12.490 | 0.036 | 16.057 | ||||||||||
Bio, µg g–1 dw | 34 | 53 | 1 | 51 | 14 | 10 | 14 | 36 | 213 | |||||||||
21 Sep | Water, µg l–1 | 0.030 | 0.050 | 0.055 | 0.017 | 0.459 | 0.611 | |||||||||||
Bio, µg g–1 dw | 47 | 27 | 90 | 104 | 33 | 13 | 65 | 380 | ||||||||||
07 Oct | Water, µg l–1 | 2.802 | 1.425 | 2.160 | 6.543 | 0.248 | 0.200 | 13.378 | ||||||||||
Bio, µg g–1 dw | 74 | 133 | 3 | 14 | 3 | 14 | 15 | 255 |
Detected concentrations of extracellular MCs in water and intracellular MCs in biomass samples, cell number and biomass of observed cyanobacterial species in Sestroretskij Razliv Lake in 2011. * denotes to cell number or biomass <1%. Aph. =
Sestroretskij Razliv Lake, 2011 | MC-LR | dmMC-LR | [D-Glu-OCH MC-LR] | MC-RR | dmMC-RR | MC-YR | MC-WR | MC-LW | Total MCs | Cell number of cyanobacterial species, x 10 cells l , (N,%) | Biomass of observed cyanobacterial species, mg l , (B,%) | |
---|---|---|---|---|---|---|---|---|---|---|---|---|
02 Jun | Water, µg l | 0.004 | 0.003 | 0.070 | 0.077 | |||||||
Bio,µg g dw | ||||||||||||
27 Jun | Water, µg l | |||||||||||
Bio,µg g dw | ||||||||||||
18 Jul | Water, µg l | 0.211 | 0.086 | 0.044 | 0.341 | |||||||
Bio,µg g dw | 264 | 20 | 8 | 188 | 20 | 62 | 17 | 10 | 593 | |||
01 Aug | Water, µg l | 0.008 | 0.022 | 0.018 | 0.048 | |||||||
Bio,µg g dw | 119 | 7 | 5 | 84 | 7 | 29 | 9 | 2 | 266 | |||
22 Aug | Water, µg l | 0.024 | 0.025 | 0.049 | ||||||||
Bio,µg g dw | 196 | 5 | 5 | 175 | 1 | 62 | 19 | 463 | ||||
19 Sep | Water, µg l | 0.066 | 0.017 | 0.071 | 0.004 | 0.014 | 0.172 | |||||
Bio,µg g dw | 159 | 11 | 335 | 1245 | 345 | 2095 | ||||||
22 Sep | Water, µg l | 0.046 | 0.012 | 0.263 | 0.278 | 0.097 | 0.696 | |||||
Bio,µg g dw | 306 | 21 | 142 | 43 | 29 | 541 |
Detected concentrations of extracellular MCs in water and intracellular MCs in biomass samples, cell number and biomass of observed cyanobacterial species in Sestroretskij Razliv Lake in 2012. * denotes to cell number or biomass <1%. Aph. =
Sestroretskij Razliv Lake, 2012 | MC-LR | dmMC-LR | MC-RR | didmMC-RR | dmMC-RR | ]MC-RR [L-Ser | MC -YR | dmMC-YR | MC-LF | Total MCs | Cell number of cyanobacterial species, x 10 cells l , (N,%) | Biomass of cyanobacterial species, mg l , (B,%) | |
---|---|---|---|---|---|---|---|---|---|---|---|---|---|
28 May | Water, µg l | 0.015 | 0.035 | 0.050 | |||||||||
Bio, µg g dw | 244 | 71 | 578 | 16 | 349 | 81 | 37 | 1 | 1377 | ||||
14 Jun | Water, µg l | 0.495 | 0.735 | 0.005 | 0.008 | 1.243 | |||||||
Bio, µg g dw | 743 | 78 | 807 | 12 | 89 | 6 | 22 | 112 | 1859 | ||||
24 Jun | Water, µg l | 0.067 | 0.054 | 0.121 | |||||||||
Bio, µg g dw | 78 | 215 | 5 | 298 | |||||||||
5 Jul | Water, µg l | 0.014 | 0.030 | 0.009 | 0.053 | ||||||||
Bio, µg g dw | 116 | 334 | 3 | 36 | 489 | ||||||||
20 Jul | Water, µg l | 0.315 | 0.438 | 0.053 | 0.061 | 0.867 | |||||||
Bio, µg g dw | 51 | 186 | 3 | 20 | 260 | ||||||||
2 Aug | Water, µg l | 0.399 | 0.289 | 0.228 | 0.916 | ||||||||
Bio, µg g dw | 308 | 880 | 2 | 973 | 131 | 2294 | |||||||
13 Aug | Water, µg l | ||||||||||||
Bio, µg g dw | 344 | 995 | 2 | 1 | 124 | 1466 | |||||||
3 Sep | Water, µg l | 0.058 | 0.058 | ||||||||||
Bio, µg g dw | 14 | 2 | 35 | 11 | 7 | 1 | 70 | ||||||
13 Sep | Water, µg l | ||||||||||||
Bio, µg g dw | 8 | 7 | 6 | 1 | 14 | 3 | 6 | 45 |
Detected concentrations of extracellular MCs in water and intracellular MCs in biomass samples, cell number and biomass of observed cyanobacterial species in Lower Suzdal Lake in 2010. * denotes to cell number or biomass <1%. Aph. =
Lower Suzdal Lake, 2010 | MC- LR | dmMC-LR | ]MC-LR [L-Ser | MC-RR | dmMC-RR | ]MC-RR [L-Ser | MC-YR | dmMC-YR | MC-WR | Total MCs | Anatoxin-a | Cell number of cyanobacterial species, x 10 cells l , (N,%) | Biomass of cyanobacterial species, mg l , (B,%) | |
---|---|---|---|---|---|---|---|---|---|---|---|---|---|---|
11 Jun | Water, µg l | 0.135 | 0.047 | 0.022 | 0.006 | 0.176 | 0.386 | |||||||
Bio, µg g dw | 5 | 2 | 7 | |||||||||||
28 Jun | Water, µg l | 0.007 | 0.007 | 0.014 | 0.160 | |||||||||
Bio, µg g dw | 2 | 2 | 4 | |||||||||||
15 Jul | Water, µg l | 0.089 | 0.079 | 0.255 | 0.021 | 0.357 | 0.315 | 0.564 | 1.680 | 0.540 | ||||
Bio, µg g dw | 5 | 3 | 2 | 11 | 7 | 2 | 30 | |||||||
02 Aug | Water, µg l | 0.010 | 0.036 | 0.023 | 0.005 | 0.230 | 0.304 | |||||||
Bio, µg g dw | 3 | 3 | 6 | 6 | 1 | 2 | 8 | 29 | ||||||
16 Aug | Water, µg l | 0.035 | 0.078 | 0.047 | 0.018 | 0.081 | 0.079 | 0.098 | 0.436 | |||||
Bio, µg g dw | 67 | 10 | 98 | 1 | 22 | 31 | 5 | 234 | ||||||
09 Sep | Water, µg l | 0.031 | 0.115 | 0.025 | 0.262 | 0.131 | 0.564 | |||||||
Bio, µg g dw | 1 | 1 | ||||||||||||
27 Sep | Water, µg l | 0.049 | 0.454 | 0.123 | 0.199 | 0.954 | 0.874 | 0.089 | 0.143 | 2.885 | ||||
Bio, µg g dw | 12 | 6 | 18 |
Detected concentrations of extracellular MCs in water and intracellular MCs in biomass samples, cell number and biomass of observed cyanobacterial species in Lower Suzdal Lake in 2011. * denotes to cell number or biomass <1%. Aph. =
Lower Suzdal Lake, 2011 | MC-LR | dmMC-LR | MC-RR | dmMC-RR | MC-YR | dmMC-YR | MC-LW | Total ??s | Anatoxin-a | Cell number of cyanobacterial species, x 10 cells l , (N,%) | Biomass of cyanobacterial species, mg l , (B,%) | |
---|---|---|---|---|---|---|---|---|---|---|---|---|
6 Jun | Water, µg l | 0.006 | 0.008 | 0.002 | 0.016 | |||||||
Bio, µg g dw | ||||||||||||
4 Jul | Water, µg l | 0.007 | 0.007 | 0.139 | ||||||||
Bio, µg g dw | 1 | 3 | 4 | 30 | ||||||||
11 Jul | Water, µg l | 0.008 | 0.008 | 0.266 | ||||||||
Bio, µg g dw | 4 | 4 | ||||||||||
21 Jul | Water, µg l | 0.054 | 0.009 | 0.203 | 0.138 | 0.404 | ||||||
Bio, µg g dw | 225 | 17 | 71 | 24 | 351 | 3 | 7 | 698 | ||||
5 Aug | Water, µg l | 0.006 | 0.006 | 0.012 | 0.240 | |||||||
Bio, µg g dw | 33 | 15 | 28 | 23 | 16 | 5 | 121 | |||||
5 Sep | Water, µg l | 0.0011 | 0.007 | 0.018 | 0.029 | 0.065 | ||||||
Bio, µg g dw | 41 | 13 | 32 | 35 | 19 | 142 | ||||||
29 Sep | Water, µg l | 0.070 | 0.007 | |||||||||
Bio, µg g dw | 28 | 26 | 31 | 34 | 2 | 121 |
Detected concentrations of extracellular MCs in water and intracellular MCs in biomass samples, cell number and biomass of observed cyanobacterial species in Lower Suzdal Lake in 2012. * denotes to cell number or biomass <1%. Aph. =
Lower Suzdal Lake, 2012 | MC- LR | MC -RR | dmMC-RR | MC- YR | Total ??s | Cell number of cyanobacterial species, x10 cells l , (N,%) | Biomass of cyanobacterial species, mg l , (B,%) | |
---|---|---|---|---|---|---|---|---|
05 Jun | Water, µg l | 0.002 | 0.045 | 0.047 | ||||
Bio, µg g dw | 21 | 33 | 97 | 10 | 161 | |||
21 Jun | Water, µg l | 0.010 | 0.618 | 0.628 | ||||
Bio, µg g dw | 8 | 33 | 5 | 5 | 51 | |||
06 Jul | Water, µg l | 0.031 | 0.124 | 0.528 | 0.022 | 0.705 | ||
Bio, µg g dw | 69 | 221 | 11 | 13 | 315 | |||
23 Jul | Water, µg l | 0.010 | 0.048 | 0.058 | ||||
Bio, µg g dw | 121 | 318 | 1 | 30 | 470 | |||
30 Jul | Water, µg l | 0.208 | 0.218 | 0.099 | 0.020 | 0.545 | ||
Bio, µg g dw | 46 | 131 | 2 | 12 | 191 | |||
16 Aug | Water, µg l | 0.002 | 0.002 | |||||
Bio, µg g dw | 26 | 15 | 9 | 50 | ||||
06 Sep | Water, µg l | 0.003 | 0.003 | 0.006 | ||||
Bio, µg g dw | 353 | 1345 | 2 | 96 | 1796 | |||
12 Sep | Water, µg l | 0.004 | 0.004 | |||||
Bio, µg g dw | 262 | 695 | 2 | 116 | 1075 |
The median seasonal and maximum concentrations of the total MCs, extracellular and intracellular MCs concentrations, and the concentrations of the three main toxins identified in the two water bodies by LC-MS/MS in each sampling period are shown in Tables 1 and 2. The sampling periods are highlighted in the tables according to the change in the dominant species. The total number of detected MCs variants during our three-year study was 14 in Razliv, and 9 in Suzdal. The number and structures of microcystin congeners identified in the lakes are presented in Table 3.
The number and structure of microcystin (MC) variants identified in Sestroretskij Razliv and in Lower Suzdal Lake in 2010–2012
Year | MCs in Razliv (total variants 14) | MCs in Suzdal (total variants 9) |
---|---|---|
2010 | dmMC-LR |
dmMC-LR |
2011 | dm-MC-LR |
dm-MC-LR |
2012 | dmMC-LR |
MC-LR |
Although cyanobacterial biomass was not high in 2010 (Fig. 1A, 1D), the median values for total extracellular toxins reached their maxima in Razliv (1.61 μg l−1) and Suzdal (0.44 μg l−1) (Tables 1, 2). The maximum extracellular MCs concentrations in each water body for the whole study period were recorded in the same season. In Razliv, the maximum extracellular MCs concentration (41.37 μg l−1 mainly due to 38.54 μg l−1 of desmethyl-MC-RR) was determined in August 2010 (Table 1, Supplementary tables S2). The maximum concentration of extracellular MCs in Suzdal was noted in September 2010 and it amounted to 2.89 μg l−1 (Table 2, Supplementary tables S5). Concentrations of intracellular MCs were low during this sampling season in both lakes, their median values were 132 μg g−1 DW in Razliv and 18 μg g−1 DW in Suzdal (Tables 1, 2).
In 2011, in spite of higher cyanobacterial biomass and higher contribution of cyanobacteria to the phytoplankton community than in 2010 (Fig. 1 B, E), the values of median concentration of extracellular MC were low in both lakes (Tables 1 and 2). The maximum dissolved MCs concentrations recorded this season were also low in both lakes and amounted to 0.70 μg l−1 in Razliv (Table 1, Fig. 1B, and Supplementary Table S3) and 0.40 μg l−1 in Suzdal (Table 2, Fig. 1F, and Supplementary table S6). On the other hand, the intracellular MC content was high and reached 2095 μg g-1 in Razliv and 698 μg g−1 in Suzdal.
The highest median concentrations of intracellular MCs in both lakes were recorded in 2012. At the beginning of August 2012, the maximum concentration of intracellular MCs for the entire study period (2294 μg g−1 DW) was recorded in Razliv. In Suzdal, peak values of intracellular MCs concentrations (1075-1796 μg g−1 DW) were recorded in September (Table 2, Supplementary table S7).
Neurotoxic AN was detected only in Suzdal. It was found in water samples collected from late June to early August 2010 and 2011 (Table 2, Supplementary tables S5, S6). Extracellular concentration of AN in filtered water samples was in the range of 0.16-0.54 μg l-1 (2 samples) in 2010 and 0.14-0.27 μg l−1 (3 samples: two samples in the sampling period June-July and one in August) in 2011 (Table 2, Supplementary table S5). Intracellular AN (30 μg g−1 DW) was recorded only in one biomass sample at the beginning of July. The presence of
The occurrence and distribution of cyanobacterial toxins were studied in two lakes typical for Saint Petersburg region: Sestroretskij Razliv Lake and Lower Suzdal Lake. The obtained data showed the constant presence of species able to produce cyanotoxins in both water bodies. However, the phytoplankton structure and dynamics were different between the studied lakes and seasons. In Suzdal, a higher variability of different taxonomic groups of phytoplankton was observed (Supplementary Table S1), whereas in Razliv – mainly Cyanobacteria were present.
The mass occurrence of cyanobacteria, cyanobacterial biomass values and the pattern of changes in their structure were typical for other hypertrophic or eutrophic water bodies and dam reservoirs across Europe (Teubner et al. 1999; Nixdorf et al. 2003; Pawlik-Skowrońska et al. 2004; Stefaniak et al. 2005; Dittmann & Wiegand 2006; Grabowska & Mazur-Marzec 2011; Kokocinski et al. 2011; Ostermaier et al. 2012).
Among the dominant species, the common producers of cyanotoxins were present. Therefore, we found it important to investigate the concentration of microcystins in lake water and phytoplankton samples. The dissolved (extracellular) fraction of cyanotoxins, which is released during bloom events, is sometimes overlooked in environmental studies, even though it may have a significant effect on the current state and quality of the water. Knowledge about the maximum MCs concentrations in reservoirs is of great importance, particularly in recreational areas as health outcomes may also result from exposure through swimming (contact with skin), inhalation or ingestion of cyanotoxin-containing water. Some investigations showed that even low concentrations of MCs may pose a significant health risk during the recreational use of water bodies (Ueno et al. 1996; Chen et al. 2009).
The analysis of biomass-bound (intracellular) cyanotoxins should also be conducted as this fraction of harmful biomolecules could be an additional route of their transfer and/or accumulation in aquatic animals, increasing the potential risk of human exposure through fish consumption.
MCs congeners detected in samples from Razliv and Suzdal are known to be produced by dominant cyanobacterial species present in the lakes. According to the published data,
Some of the microcystin congeners seem to be stable components of the cyanobacterial bloom. They were detected in samples regardless of the season and the investigated water bodies. The identified MCs were mainly hydrophilic arginine-containing counterparts. The main toxin variants were MC-LR, MC-YR, MC-RR and desmethylated-MC-RR. These variants were also the most common MCs in Finland (Spoof et al. 2003), Poland (Grabowska & Mazur-Marzec 2011) and other European countries located at the same latitude (Kokocinski et al. 2011).
Concentrations of extracellular microcystins determined in natural waters are usually in the range of 0.1-10 μg l−1 (Sivonen & Jones 1999; Spoof et al. 2003; Welker 2008). Most of the extracellular MCs concentrations measured in our study were also within this range. Only some of the values determined in August and September 2010 in water samples from Razliv exceeded the guideline value for recreational water (WHO, 2003) and reached the maximum of 41.37 μg l−1 (16 Aug. 2010). The total concentrations of dissolved toxins determined in hypertrophic Razliv (Tables 1 and 2) were generally higher as compared with eutrophic Suzdal.
In our study, the concentration of cyanotoxins in bloom samples only to some extent depends on cyanobacterial biomass (Supplementary table S2). In 2010, when the contribution of cyanobacteria to the total phytoplankton biomass was low in both lakes studied (Fig. 1 A, D), the median values of the extracellular MCs concentration were higher than in the samples from the two other years (Table 1, 2). As it was proved, there are significant differences in toxin profiles and in the intensity of toxin production among cyanobacterial strains (Apeldoorn et al. 2007; Welker 2008; Kurmayer & Christiansen 2009). In spite of the fact that
In addition to hepatotoxins, some species of freshwater cyanobacteria can produce neurotoxins. Anatoxin-a (AN) is a secondary amine with potent neurotoxicity. This cyanotoxin is produced by several cyanobacterial genera, including
In our study, AN was detected only in Suzdal during warm periods in 2010 and 2011. Maximum concentrations of AN were recorded at the beginning of summer seasons when
Although the maximum concentration of AN in water (0.54 μg l−1) detected in mid-July in 2010 was not high, the occurrence of this “fast-death factor” in freshwater ecosystems should be monitored due to its high toxicity
In this work, the occurrence and distribution of cyanobacterial toxins was studied in two lakes typical for Saint Petersburg region in Russia: Lake Sestroretskij Razliv and Lower Suzdal Lake. The observed cyanobacterial assemblages: “
During our study, the presence of fifteen different congeners of microcystins, mainly hydrophilic arginine-containing counterparts, and the neurotoxic anatoxin-a was determined. The increased variety of microcystins’ congeners and higher MCs concentration in hypertrophic Razliv was likely caused by higher variability of phytoplankton composition and frequent changes in dominant species.
The measured concentrations of extracellular MCs in the lakes (0.1-10 μg l−1) were mainly within the reported range for natural waters and only sporadically exceeded the guideline value for recreational water.
Further monitoring investigations should be conducted for several seasons to better understand the cyanobacterial response to environmental changes and to better assess the potential risk to water users in Northwestern Russia.