The Efficiency of Microstrainers Filtration in the Process of Removing Phytoplankton with Special Consideration of Cyanobacteria.

The research presented in this manuscript concerns the evaluation of the effectiveness of microstrainers, which are designed to reduce the amount of plankton in treated surface water. The efficiency of microstrainer filtration analysis is very important for the proper course of the water-treatment process not only in the Water-Treatment Plant (WTP) in Zielona Góra (central western Poland) but also in other WTPs around the world. The qualitative and quantitative monitoring of the abundance of plankton including cyanobacteria during the particle-filtration process allows not only for the assessment of the potential cyanotoxic risk in surface water providing a source of drinking water, but also allows the evaluation of the action and the prevention of adverse impacts of microstrainers. Over four years of research, it was observed that the largest amount of cyanobacteria before microstrainer filtration took place in May. The dominant species was Limnothrix redeckei. The microstrainer removal of plankton and cyanobacteria was statistically significant. The quantity of removed plankton increased with its increasing content in raw water. The particle-filtration process, by reducing the amount of cyanobacteria, contributes to a decrease in intracellular microcystins.

1. Introduction

1.1. The Significance of the Presence of Phytoplankton Including Cyanobacteria in the Process of Water Treatment

Pollution and eutrophication lead to the presence of high concentrations of organic and inorganic compounds which enhance phytoplankton (including cyanobacteria) blooms and concomitantly decrease water quality. The occurrence of these blooms in the source water for drinking-water production is of critical importance to drinking-water providers. Phytoplankton can have both a physical impact (e.g., clogging of filters) and chemical impact (e.g., production of cyanotoxins, disinfection by-products, and taste and odor compounds) on the treatment process [1,2,3].

Strong growth of undesirable cyanobacteria and algae species is a serious problem in reservoirs intended as drinking-water intakes for large urban agglomerations in Poland. This is the kind of problem that is faced by the Warsaw water-supply company, which delivers water from the Vistula River via the Czerniakowski Settling Pond, the dam reservoir in Przeczyce and the Zegrzyński and Dobromierz Reservoir [4]. Toxic cyanobacterial blooms occurred in the following reservoirs: Kozłowa Góra [5] Goczałkowice, Turawa, Otmuchów, and Nysa, which supply the inhabitants of Silesia with water [6] in the Dobczyce Reservoir, supplying the city of Cracow with drinking water [7] and the Sulejów Reservoir, which is the source of drinking water for the inhabitants of Łódź [4].

One of the sources of raw water for the Zielona Góra water-supply company is the water from the Obrzyca River, in whose catchment area massive blooms of cyanobacteria occur [8]. In the area under study species of toxic cyanobacteria were identified, including those which synthesize the most dangerous hepatotoxin, microcystin MC-LR [9]. Periodic cyanobacterial blooms in the catchment area of the Obrzyca River and at its source, Sławskie Lake, initiated research on the possibility of controlling cyanotoxic risk [8]. The research has been conducted with the use of microstrainers in the technological line for water purification at the Water-Treatment Plant (WTP) in Zielona Góra.

1.2. The Methods of Cyanobacteria and Cyanotoxin Elimination in Treated Water Including Process of Water Treatment for the Inhabitants of Zielona Góra

The amount of phytoplankton, including cyanobacteria, can be reduced in the processes of coagulation and flocculation as a result of aggregation of smaller particles into larger ones. However, studies have shown that the removal rate of cells and cyanotoxins is variable, and influenced by treatment conditions and by the phytoplankton species present in the water [10]. During coagulation, certain problems may arise such as cell lysis, leading to the release of intracellular toxins [11].

Although chloamountrination and ozonation are effective in removing microcystins, powdered activated carbon is one if the major treatment barriers for the removal of cyanotoxins in WTPs. Activated carbons are unique and versatile adsorbents because of their extended surface area, microporous structure, high adsorption capacity, and economic feasibility. The introduction of powdered activated carbon during coagulation allows for the removal of cyanobacterial toxins from drinking water [12].

Ozonation in the water-treatment chain may result in algal cells lysis and increase dissolved microcystins. Effectiveness of ozonation varies depending upon the disinfectant dose and types of cyanotoxins [11].

Membrane filtration is a physical process that separates contaminants by size and charge depending on the physical/chemical characteristics of the membrane. An important point when considering filtration is the lysis of cells. Membrane filtration is a pressure-driven process which uses size exclusion, charge repulsion, adsorption, and/or diffusion processes for removal mechanisms. Generally, there are four processes that are considered feasible and more commonly used for membrane treatment in drinking-water applications: microfiltration, ultrafiltration, nanofiltration, and reverse osmosis. Two types of low-pressure membrane filtration, microfiltration, and ultrafiltration, have been shown to be effective in the removal of intact cyanobacterial cells. These membranes removed more than 98% of the cells but are unable to reject dissolved toxins [13].

During low-pressure membrane treatments of cyanobacterial cells, including microfiltration and ultrafiltration, there have reportedly been releases of intracellular compounds including cyanotoxins and compounds with an earthy/musty odor into the water, probably owing to products of cyanobacterial cell breakage being retained on the membrane [14].

Microstrainers consist of a finely woven stainless-steel wire cloth mounted on a revolving drum that is partially submerged in the water. Water enters through an open end of the drum and flows out through the screen, leaving suspended solids behind. Captured solids are washed into a hopper when they are carried up out of the water by the rotating drum. Microstrainers consist of a very fine screen used primarily to remove algae other aquatic organisms and small debris that can clog treatment plant filters [15]. Application of microstrainers as an improvement to the water purification process is used in the WTP in Stuttgart (Constance Lake) where 12 microstrainers with a mesh width of 15 µm are used.

The Obrzyca River (the right tributary of the Oder River) is the surface water which is purified in WTP Zawada and supplied as drinking water to the local population (mainly the inhabitants of Zielona Góra). Surface water is one of the main sources of raw water used for the purposes of the municipal water-supply system in Zielona Góra [2,16]. The percentage share of particular water sources in the consumption water supply for the inhabitants of Zielona Góra in the years 2011–2014 is presented in Figure 1.

Figure 1

The percentage share of particular water sources in the consumption water supply for the inhabitants of Zielona Góra in the years 2011–2014.

The quality of water taken from the Obrzyca River falls within category 3 (water requiring highly efficient physical and chemical treatment) [17]. The poor quality of raw water supplied to WTP Zawada and the need to treat the groundwater and surface water collectively causes numerous problems in the process of water treatment. Surface water is characterized by pollution typical of eutrophic waters (high color, oxidizability, periodic blooms, and increased levels of orthophosphates). The latter are part of household and industrial sewage, but they may also come from surface runoffs from arable land treated with artificial fertilizers containing phosphorus compounds. Surface water is strained with grids and sieves. It is then pumped through a pipeline to the first element of the processing system, where it is strained in three microstrainer drums (Figure 2) fitted with a 10 μm screening mesh. The diagram of the process of surface water treatment at WTP is presented in [2].

Figure 2

Microstrainers in WTP Zawada. 1 raw water supply; 2 slide flat; 3 mesh baskets; 4 submersible pump; 5 sprinklers; 6 drainage trough; 7 drum drive; 8 clean water outflow.

This study aims to demonstrate that the microstrainers operating at WTP in Zielona Góra are a useful tool for the water-treatment technology intended to eliminate plankton, including cyanobacteria and their toxins. The microscopic analysis of the abundance of plankton including cyanobacteria during the microstrainer process allows not only for the assessment of potential cyanotoxic threat in supplied drinking water, but also evaluation of the action, and prevention of adverse impacts of the microstrainers.

2. Results

2.1. The Amount of Plankton Including Cyanobacteria at WTP Zawada Before and After Microstrainers

In the analyzed raw water, the largest share was diatoms, then cyanobacteria. The smallest participation in phytoplankton was green algae. The microstrainer removal efficiency of plankton and cyanobacteria, depending on the level, are presented in Table 1.

Table 1

Microstrainers efficiency in removing plankton and cyanobacteria in WTP Zawada from 2011 to 2014.

Microorganisms	Number of Results	Range of Quantity [103 org. dm−3]	Removal Efficiency
			%	Average [%]
Plankton	8	> 100	47.4–83.7	65.1
	7	50–100	25.2–85.0	53.7
	7	10–50	13.6–76.8	53.7
	41	< 10	9.1–93.8	50.2
Cyanobacteria	4	> 100	51.1–81.1	65.9
	6	50–100	41.2–85.7	58.6
	10	10–50	13.9–93.0	49.7
	43	< 10	5.00–81.0	48.6

Most samples were with the lowest level of contamination. The widest range and the lowest average of removal percentage for plankton and cyanobacteria occurred when the amount was the lowest (< 10·103 org.·dm−3). Average removal percentage > 50% took place throughout the entire research area for plankton but > 50 103 org.·dm−3 for cyanobacteria.

The largest amount of plankton before microstraining was observed in May 2011 and was 497·103 org.·dm-3 (Figure 3) and the dominant group was cyanobacteria.

Figure 3

Efficiency of plankton removal after microstraining process in WTP Zawada from 2011 to 2014.

The smallest amount of plankton before microstraining was observed on July 4, 2012 (0.96·103 org.·dm−3). On the same day, the amount of cyanobacteria was 0.12·103 org.·dm−3 and the reduction in plankton reached 79.2%. The maximum degree of plankton removal, totaling 93.98%, took place in June 2011 and the minimum (9.1%) in September 2013. Removal of greater than half of the total plankton was detected in 42 samples (63.6%) including cyanobacteria (60.6%), diatoms (51.5%), green algae (63.6%).

The number of removed plankton increased with its increasing content in raw water as presented in Figure 4. The student’s t-test analysis showed significant differences between the amount of plankton (tcalc 2.02; tcrit 1,95; p > 0.05) before and after microstraining.

Figure 4

Relationship between amount of plankton in raw water and removed in WTP Zawada.

2.2. The Quantitative and Qualitative Analysis of Cyanobacteria at WTP in Zawada Before and After Microstrainers

The amount of cyanobacteria in samples before and after microstraining fell into the following ranges respectively: 0.02–243·103 org.·dm−3; 0.02–118·103 org.·dm−3 (Appendix A, Table A1). The largest amount of cyanobacteria before microstraining was observed in May 2011 and the dominant species was Limnothrix redeckei (Meffert).

Table A1

The quantitative and qualitative analysis of cyanobacteria in WTP Zawada (before and after microstraining) sampled in the years 2011–2014.

Sampling Date[D/M/Y]	Dominant Cyanobacteria Species	Amount of Cyanobacteria (103 org.·dm−3)	Dominant Cyanobacteria Species	Amount of Cyanobacteria (103 org.·dm−3)
	BEFORE Microstrainers		AFTER Microstrainers
2011
4/05/2011	Limnothrix. redeckei	243	Limnothrix. redeckei	44.2
11/05/2011	Limnothrix redeckei	238	Limnothrix redeckei	63.8
13/05/2011	Limnothrix redeckei	241	Limnothrix redeckei	118
18/05/2011	Limnothrix redeckei	60.5	Limnothrix redeckei	35.6
19/05/2011	Limnothrix redeckei	43.9	Limnothrix redeckei	28.2
25/05/2011	Dolichospermum affinis	35.0	Dolichospermum afffinis	15.5
1/06/2011	Dolichospermum affinis	0.05	-	Not detected
8/06/2011	-	Not detected	-	Not detected
15/06/2011	Dolichospermum affinis	0.16	-	Not detected
22/06/2011	Microcystis aeruginosa	0.08	-	Not detected
29/06/2011	Microcystis aeruginosa	0.14	Microcystis aeruginosa	0.02
06/07/2011	Microcystis aeruginosa	0.37	Microcystis aeruginosa	0.22
14/07/2011	Dolichospermum affinis	0.24	Dolichospermum affinis	0.05
20/07/2011	Dolichospermum affinisMicrocystis aeruginosa(co-dominance)	0.27	-	Not detected
27/07/2011	Microcystis aeruginosa	29.5	Microcystis aeruginosa	2.06
02/08/2011	Microcystis flos-aquae	62.7	Microcystis flos-aquae	15.3
23/08/2011	Dolichospermum affinis	3.50	Dolichospermum affinis	2.13
30/08/2011	Dolichospermum affinis	25.9	Dolichospermum affinis	5.70
14/09/2011	Dolichospermum affinis	2.44	Dolichospermum affinis	0.55
21/09/2011	Dolichospermum affinis	54.6	Dolichospermum affinis	7.80
28/09/2011	Dolichospermum affinis	99.0	Dolichospermum affinis	35.3
2012
9/05/2012	Dolichospermum affinis	0.14		Not detected
16/05/2012	Dolichospermum affinis	0.29	Dolichospermum affinis	0.22
23/05/2012	Dolichospermum affinis	0.56	Dolichospermum affinis	0.12
6/06/2012	-	Not detected	-	Not detected
13/06/2012	Microcystis flos-aquae	0.02	-	Not detected
20/06/2012	Dolichospermum flos-aquae	0.04	-	Not detected
27/06/2012	Dolichospermum affinis	1.34	Dolichospermum affinis	0.61
04/07/2012	Dolichospermum. flos-aquaeDolichospermum spiroidesMicrocystis aeruginosa(co-dominance)	0.12	Dolichospermum spiroides	0.03
25/07/2012	Dolichospermum planctonica	1.81	Dolichospermum planctonica	1.01
02/08/2012	Dolichospermum planctonica	0.06	Dolichospermum planctonica	0.05
08/08/2012	Dolichospermum affinis	0.27	Dolichospermum affinis	0.12
28/08/2012	Aphanizomenon flos-aquae	0.07	Aphanizmenon flos-aquae	0.07
05/09/2012	Planktothrix agardhii	0.86	Planktothrix agardhii	0.46
11/09/2012	Planktothrix agardhii	2.22	Planktothrix agardhii	0.40
19/09/2012	Dolichospermum planctonica	2.28	Dolichospermum planctonica	0.64
25/09/2012	Planktothrix agardhii	70.7	Planktothrix agardhii	29.6
2013
15/05/2013	Dolichospermum affinisOscillatoria granulata(co-dominance)	0.68	Dolichospermum. affinisOscillatoria granulata(co-dominance)	0.49
21/05/2013	Pseudoanabaena limnetica	1.92	Pseudoanabaena limnetica	1.27
29/05/2013	Pseudoanabaena limnetica	4.83	Pseudoanabaena limnetica	2.02
4/06/2013	Pseudoanabaena limnetica	1.31	Pseudoanabaena limnetica	0.87
12/06/2013	Pseudoanabaena limnetica	0.26	Oscillatoria granulata	0.19
19/06/2013	Pseudoanabaena limnetica	0.40	Pseudoanabaena limnetica	0.15
25/06/2013	Pseudoanabaena limnetica	0.16	Pseudoanabaena limnetica	0.07
10/07/2013	Dolichospermum planctonica	24.3	Dolichospermum planctonica	19.2
31/07/2013	Dolichospermum affinis	0.96	Dolichospermum affinis	0.33
7/08/2013	Dolichospermum spiroidesMicrocystis aeruginosa(co-dominance)	86.6	Dolichospermum spiroidesMicrocystis aeruginosa(co-dominance)	35.1
13/08/2013	Microcystis aeruginosa	3.16	Microcystis aeruginosa	1.30
3/09/2013	Dolichospermum affinis	2.41	Dolichospermum affinis	2.40
11/09/2013	Dolichospermum affinis	14.7	Dolichospermum affinis	7.90
17/09/2013	Dolichospermum affinis	15.1	Dolichospermum affinis	14.9
24/09/2013	Dolichospermum affinis	16.6	Dolichospermum affinis	14.3
2014
7/05/2014	Limnothrix redeckei	0.54	Limnothrix redeckei	0.49
14/05/2014	Pseudoanabaena limnetica	3.02	Pseudoanabaena limnetica	1.75
28/05/2014	Pseudoanabaena limnetica	0.07	-	Not detected
4/06/2014	Pseudoanabaena limnetica	0.15	-	Not detected
11/06/2014	Pseudoanabaena limnetica	0.22	-	Not detected
17/06/2014	Pseudoanabaena limnetica	0.20	Pseudoanabaena limnetica	0.19
24/06/2014	Dolichospermum flos-aquae	3.31	Dolichospermum flos-aquae	0.94
2/07/2014	Dolichospermum planctonica	0.64	Dolichospermum planctonica	0.20
8/07/2014	Pseudoanabaena limnetica	0.14	-	Not detected
15/07/2014	Dolichospermum spiroides	0.60	Dolichospermum spiroides	0.31
23/07/2014	Dolichospermum planctonica	14.4	Dolichospermum planctonica	8.30
19/08/2014	Oscillatoria granulata	0.15	Oscillatoria granulata	0.04
26/08/2014	Oscillatoria granulata	0.25	Oscillatoria granulata	0.05
2/09/2014	Oscillatoria granulata	0.32	-	Not detected
10/09/2014	Planktothrix agardhii	213	Planktothrix agardhii	91.1
16/09/2014	Oscillatoria granulata	6.80	Oscillatoria granulata	2.28
24/09/2014	Microcystis aeruginosaPlanktothrix agardhii(co-dominance)	34.4	Microcystis aeruginosaPlanktothrix agardhii(co-dominance)	13.3

Maximum values of cyanobacteria before micro-sieves in one year were underlined. Maximum values of cyanobacteria before microstrainers one year were underlined.

The most frequent species of cyanobacteria found on microstrainers was Dolichospermum affinis (Lemmermann) (28% of the analyzed samples) (Appendix A, Table A1). Other species of cyanobacteria of the same genus that were dominant in the analyses were: Dolichospermum flos-aquae (Lyngbye), Dolichospermum planctonica (Brunnthaller), Dolichospermum spiroides (Klebahn). The second in terms of the frequency of dominance was Pseudoanabaena limnetica (Lemmermann) 19 samples and L. redeckei 12 samples (9.09%) of 132 samples, most frequently in May or June. Oscillatoria granulata (N.L. Gardner) occurred in September in 10 samples. The genus Microcystis was dominant in 18 samples, of which Microcystis aeruginosa (Kützing) in 15 samples (7.6%) in summer months and Microcystis flos-aquae (Wittrock) in 3 (1.5%) in August. The Planktothrix agardhii (Anagn. & Komárek) dominated in 8 samples in September. Other species occurring in the samples included Aphanizomenon flos-aquae (Ralfs ex Bornet & Flahault), Merismopedia glauca (Kützing), Microcystis viridis (Lemmermann). M. wesenbergii (Komárek in N.V. Kondrat.), Oscillatoria tenuis (Agardh ex Gomont), Snowella lacustris (Komárek & Hindák), and Woronichinia naegeliana (Elenkin).

The decrease in the amount of cyanobacteria due to microstraining ranged from 5 to 93%. The maximum degree of cyanobacteria removal occurred on 27 July 2011 (Figure 5).

Figure 5

Efficiency of cyanobacteria removal after microstrainers process in WTP Zawada from 2011 to 2014.

The number of removed cyanobacteria increased with its increasing content in raw water. The student’s t-test analysis showed significant differences between the amount of cyanobacteria (tcalc 2.05; tcrit 1,95; p > 0.05) before and after microstraining.

On that day, the amount of cyanobacteria fell from 29.5 to 2.06·103 org.·dm−3. The amounts of cyanobacteria and their reduction in particular years are presented in Appendix A, Table A1, and Figure 5.

The maximum amount of cyanobacteria in 2011, totaling 243·103 org.·dm−3, was observed in May and the dominant species was L. redeckei. In 2007, as a result of the microstraining process, in 10 of the analyzed samples a decrease in the quantity of cyanobacteria by more than half was observed, which constitutes 48% of all samples examined in that year (Appendix A, Table A1).

The largest amount of cyanobacteria in 2012, totaling 70.7·103 org.·dm−3, was detected in September, and the dominant species was P. agardhii. In 2012, as a result of the microstraining process, in 9 of the analyzed samples a decrease in the amount of cyanobacteria by more than half was observed, which constitutes 75% of all samples examined in that year (Appendix A, Table A1).

The maximum quantity of cyanobacteria in 2013 was in August (86.6·103 org.·dm−3) and the dominant species were D. spiroides, M. aeruginosa. In 2013, as a result of microstrainer filtration, in 6 of the analyzed samples a decrease in the amount of cyanobacteria by more than half was observed, which constitutes 40% of all samples examined in that year (Appendix A, Table A1).

The largest quantity of cyanobacteria in 2014 was detected in September (213·103 szt.·dm−3) and the dominant species was P. agardhii. In 2014, as a result of microstrainer work, in 5 of the analyzed samples, a decrease in the amount of cyanobacteria by more than half was observed, which constitutes 38% of all samples examined in that year (Appendix A, Table A1).

In the years 2011–2014 a decrease in the quantity of cyanobacteria by over 50% was observed in 30 samples (29.2%).

2.3. The Content of Microcystins and the Amount of Cyanobacteria at WTP in Zielona Gora Before and After Microstrainers

Due to the large amount of cyanobacteria in May 2011 at WTP Zielona Góra, an additional series of hydrobiological analyses was performed with a simultaneous microcystin determination using the HPLC method. In the analyzed samples, neither extracellular nor intracellular MC-YR and MC-RR microcystins were found. The only intracellular microcystin detected was MC-LR, whose content is presented in Table 2. The highest concentration of the intracellular MC-LR (0.116 µg·dm−3) was observed on May 11, 2011, when the amount of cyanobacteria equaled 238·103 org.·dm−3 and the dominant species was Limnothrix redeckei (Appendix A, Table A1).

Table 2

Amount of cyanobacteria and intracellular MC-LR content before and after microstrainers filtration (WTP Zawada).

Date of Sampling [D/M/Y]	BEFORE Microstrainers Process		AFTERMicrostrainers Process
	Amount of Cyanobacteria Colony[103 org.·dm−3]	Intracellular MC-LR[µg·dm−3]	Amount of Cyanobacteria Colony[103 org.·dm−3]	Intracellular MC-LR[µg·dm−3]
11/05/2011	238	0.116	63.8	0.032
13/05/2011	241	0.098	118	0.040
18/05/2011	60.5	0.056	35.6	0.036
19/05/2011	43.9	0.044	28.2	0.032
25/05/2011	35.0	0.040	15.5	0.029

The MC-LR content in the cells of the cyanobacteria sampled from May 12 to May 25, 2011, before and after microstraining, fell within the range 0.029–0.116 µg·dm−3. In all 5 samples the MC-LR content did not exceed 1 µg·dm−3. The student’s t-test analysis showed significant differences between the amount of intracellular MC-LR (tcalc 2.40; tcrit 2.31 p > 0.05) before and after microstrainer filtration.

3. Discussion

To reduce the number of algae by approximately 80%, including cyanobacteria by 68%, in September 1994 microstrainers were installed at WTP Zielona Góra. The WTP is the only plant in Poland using microstrainers in the water-treatment system [2].

The use of the non-reagent process of particle filtration on microstrainers as a pre-treatment process for surface water abounding in algae is justified because it reduces the amount of precursors of oxidation by-products, improving physical and chemical indicators of water quality (e.g., turbidity, color, and total organic carbon (TOC)). Also, indirectly, reducing the amount of cyanobacteria causes a decrease in the amount of intracellular toxins [3].

The microstrainer filtration ensures considerable reduction in the content of phytoplankton, including cyanobacteria. In 2009, the effectiveness of micro-sieving in the removal of cyanobacteria (35.8–68.8%) increased along with their growing amount. The reduction in the amount of cyanobacteria was accompanied by decreased contents of the intracellular MC-LR [2]. In the last year of this study, with increased amounts of cyanobacteria, the dominant species was P. agardhii, which has high capacity for synthesizing hepatotoxins dangerous to humans. To eliminate any toxic threat from cyanobacteria to Zielona Góra water-supply system, one should introduce constant MC-LR monitoring in drinking water. In the last year of this research (2014), the maximum amount of cyanobacteria equaled 213 103 org.·dm−3 (Table 2), which is one of the highest values in the research period. The dominant group was the P. agardhii species, which is particularly dangerous because it can produce up to three times as much microcystin as other cyanobacteria e.g., Microcystis sp. In Polish reservoirs, the most frequently occurring form of microcystin during P. agardhii domination is MC-RR. This process may have an adverse impact on the quality of treated water in the future. To estimate the cyanotoxic risk at a drinking-water intake, a systematic (annual) monitoring of cyanobacterial toxins should be introduced, especially in the summer–autumn season [18]. In the studies, cyanobacteria bloom comprising P. agardhii also occurred in September.

The analysis of microcystin amounts in May 2011 showed low content of intracellular MC-LR (<1 µg·dm−3), permitted in drinking water [19]. However, it must be stressed that in that period of research, the dominant species was L. redeckei, which is able to produce neurotoxins and not the studied hepatotoxins [20]. In the temperate zone, this species plays an important role in mesotrophic reservoirs, especially in colder seasons. Little is known about toxicity of this species, despite the urgency of the problem due to the frequent massive occurrences of this species in drinking-water reservoirs [21].

To eliminate any toxic threat from cyanobacteria to residents of Zielona Góra in drinking water supplied by waterworks, constant monitoring not only of hepatotoxins but also neurotoxins should be introduced. Microscopic analysis should be used as a preliminary test for estimating the potential cyanobacterial risk in water [22].

4. Materials and Methods

The efficiency of plankton removal on microstrainers at WTP Zawada was estimated by means of a hydrobiological analysis. 63 samples taken before and after microstraining were analyzed from May to September 2011–2014. The assumed sampling frequency was once a week on condition that the microstrainers were in operation. This research is aimed at estimating the levels of plankton removal by microstrainers at WTP and taking appropriate action (the cleaning of microstrainers, removing leaks).

The samples for hydrobiological analysis were taken using a Sedgewick-Rafter counting chamber with a volume of 0.001 dm3 in a given number of fields with the following parameters: height 1 mm, area 1 mm2. A MN 358/A (OPTA-TECH, Warszawa, Poland) microscope was used for observation [2]. For cyanobacteria with straight filaments, 100 µm was set as one individual (org.). Curved trichomes of Dolichospermum spp. and one colony of Microcystis spp. were indicated as individuals [23]. When converting the colony count from 0.001 dm3 into 1 dm3 sample concentration by the plankton net was taken into account [24]. The results of hydrobiological analysis were expressed as: org.·dm−3. Species identification was done with identification keys for algae [25,26,27,28].

To determine the microcystin concentration in water and cyanobacteria cells in May 2011, an additional series of chromatographic analyses (HPLC) of water samples was performed, which were then sent to the Department of Applied Ecology, University of Łódź. The chromatographic analysis was carried out with the use of Agilent 1100 chromatograph with Diode Array Detection (DAD) (Agilent, Waldbronn, Germany) [29].

A student’s t-test was used to analyze the significance of difference between the amount of plankton, including cyanobacteria and their toxins before and after microstraining at a significance level of α = 0.05. The statistical analysis was performed using the following programs: StatSoft Statistica version 10.0 and Microsoft Excel 2010.

5. Conclusions

The microstrainer removal of plankton and cyanobacteria from 2011 to 2014 was statistically significant. The quantity of removed plankton increased with increasing content in raw water.

Cyanobacteria blooms occurred in surface water which is treated in WTP Zielona Góra. Cyanobacteria species occurring in WTP are capable of microcystin synthesis (e.g., Planktothrix agardhii bloom in September 2014). Therefore, cyanotoxin monitoring should be introduced especially in the summer–autumn season.

The microstrainer process, by reducing the amount of cyanobacteria, contributes to a decrease in intracellular microcystins. However, after particle-filtration process, cyanotoxic cyanobacteria may still occur. Therefore, cyanotoxin testing is justified.

The largest amount of cyanobacteria occurred in May and equaled 243·103 org.·dm−3 (domination of Limnothrix redeckei) before the microstrainer process. To eliminate any toxic threat from cyanobacteria to residents of Zielona Góra in drinking water supplied by waterworks, constant monitoring of not only hepatotoxins but also neurotoxins should be introduced. It is necessary to perform microscopic analysis as a preliminary test for estimation of the potential cyanobacterial risk in surface water for drinking-water supply.