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Review

Evidence-Based Framework to Manage Cyanobacteria and Cyanotoxins in Water and Sludge from Drinking Water Treatment Plants

by
Farhad Jalili
1,
Saber Moradinejad
1,*,
Arash Zamyadi
2,
Sarah Dorner
1,
Sébastien Sauvé
3 and
Michèle Prévost
1
1
Department of Civil, Mineral and Mining Engineering, Polytechnique Montréal, Montréal, QC H3C 3A7, Canada
2
Faculty of Engineering and Information Technology, University of Melbourne, Melbourne, VIC 3010, Australia
3
Department of Chemistry, University of Montréal, Montréal, QC H3C 3J7, Canada
*
Author to whom correspondence should be addressed.
Toxins 2022, 14(6), 410; https://doi.org/10.3390/toxins14060410
Submission received: 9 May 2022 / Revised: 12 June 2022 / Accepted: 13 June 2022 / Published: 15 June 2022
(This article belongs to the Special Issue Management of Cyanobacteria and Cyanotoxins in Waters)
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Abstract

:
Freshwater bodies and, consequently, drinking water treatment plants (DWTPs) sources are increasingly facing toxic cyanobacterial blooms. Even though conventional treatment processes including coagulation, flocculation, sedimentation, and filtration can control cyanobacteria and cell-bound cyanotoxins, these processes may encounter challenges such as inefficient removal of dissolved metabolites and cyanobacterial cell breakthrough. Furthermore, conventional treatment processes may lead to the accumulation of cyanobacteria cells and cyanotoxins in sludge. Pre-oxidation can enhance coagulation efficiency as it provides the first barrier against cyanobacteria and cyanotoxins and it decreases cell accumulation in DWTP sludge. This critical review aims to: (i) evaluate the state of the science of cyanobacteria and cyanotoxin management throughout DWTPs, as well as their associated sludge, and (ii) develop a decision framework to manage cyanobacteria and cyanotoxins in DWTPs and sludge. The review identified that lab-cultured-based pre-oxidation studies may not represent the real bloom pre-oxidation efficacy. Moreover, the application of a common exposure unit CT (residual concentration × contact time) provides a proper understanding of cyanobacteria pre-oxidation efficiency. Recently, reported challenges on cyanobacterial survival and growth in sludge alongside the cell lysis and cyanotoxin release raised health and technical concerns with regards to sludge storage and sludge supernatant recycling to the head of DWTPs. According to the review, oxidation has not been identified as a feasible option to handle cyanobacterial-laden sludge due to low cell and cyanotoxin removal efficacy. Based on the reviewed literature, a decision framework is proposed to manage cyanobacteria and cyanotoxins and their associated sludge in DWTPs.
Keywords:
cyanobacteria; cyanotoxins; pre-oxidation; sludge; accumulation; management; water treatment plant
Key Contribution: Cyanobacteria and cyanotoxins management in DWTPs is a triangular activity that includes monitoring, treatment, and sludge handling and interrelation.

1. Introduction

A cyanobacterial bloom occurrence may result in metabolite (cyanotoxins and taste and odor agents) production and release, which is considered a widespread problem in drinking water resources around the world [1,2,3,4,5,6,7,8,9,10].
Conventional treatment processes, including coagulation, flocculation, sedimentation, and filtration, are widely applied to remove cyanobacterial cells and cell-bound cyanotoxins [11,12,13,14]. However, conventional treatment processes may not be able to remove dissolved metabolites (e.g., cyanotoxins) efficiently [12,15,16,17,18,19,20,21,22]. Moreover, toxic cyanobacterial breakthrough has been reported in the effluent of conventional treatment processes and even after post-oxidation [18]. Therefore, additional treatment such as oxidation or powdered (PAC)/granular activated carbon (GAC) may be required to control dissolved metabolites [23,24,25,26].
Pre-oxidation enhances cyanobacteria cell removal during the coagulation/sedimentation process [27,28,29,30,31,32,33,34] and may decrease the cell breakthrough potential from the downflow processes. However, it is reported that pre-oxidation may cause cyanobacteria cell damage (decrease in cell viability) and cell-bound cyanotoxin release [35,36,37]. The level of cell lysis/damage and cyanotoxin degradation/release following pre-oxidation depends on the oxidation exposure (CT as residual concentration x contact time), and it is the driver to find the best pre-oxidation practice against cyanobacteria and cyanotoxins [38,39].
Furthermore, conventional treatment processes cause cell accumulation in drinking water treatment plants’ (DWTPs) sludge, even in DWTPs with low cyanobacterial cell numbers in the intake water [13,18,40,41,42,43,44]. Several studies have demonstrated that cyanobacterial cells could survive in the stored sludge and release cyanotoxins for up to 12 days [13,40,45,46,47,48,49,50,51,52]. Recent studies revealed a new challenge on the probability of extended survival time and even cyanobacterial growth during sludge storage [53,54,55]. Thus, recycling the supernatant of stored cyanobacteria-laden sludge to the head of the DWTPs can increase health-related concerns [55,56]. Such challenges highlight the importance of the treatment and management of cyanobacteria-laden sludge [57,58,59].
The objectives of this study are to: (1) critically review shreds of evidence of the pre-oxidation impact on the cultured-based and natural bloom studies, (2) perform a critical review of the fate of cyanobacteria and cyanotoxins in conventional treatment plants’ sludge and during sludge storage, and (3) develop an operational decision framework to determine the best practice to minimize risks associated with cyanobacteria and cyanotoxin presence in DWTPs.
This critical review provides insight into the fate of cyanobacteria and their associated metabolites throughout DWTPs and their sludge; furthermore, a practical decision framework to mitigate health and operational risks is developed.

2. Impact of Conventional Treatment on Cyanobacteria and Cyanotoxin Accumulation in Sludge

Different studies have reported that conventional treatment processes can remove 62–99% of the cyanobacterial cells in DWTPs [13,18,40,41,42,56]. It has been demonstrated that potential toxic cyanobacterial cells such as Microcystis, Dolichospermum, and Aphanocapsa can be removed using conventional processes [12,56,60,61].
The long-term monitoring of a high-risk DWTP (Lake Champlain—Quebec) during cyanobacterial bloom seasons from 2008 to 2011 showed an extreme accumulation of cyanobacteria cells (up to 107 cells/mL) and cyanotoxins (up to 60 μg/L microcystin-LR (MC-LR)) in the sludge of the clarifier [12,18]. Monitoring of the same DWTP in 2017 showed that cyanobacteria cell accumulation in the sludge holding tank was up to 31-fold higher than taxonomic cell counts in the intake water [56]. An investigation of four DWTPs in the Great Lakes (Ontario) with low cyanobacterial cell influx (<1000 cells/mL) revealed that cyanobacterial cells and cyanotoxins accumulated in the sludge by up to 100 and 12 times higher than the raw water, respectively [44]. Zamyadi, et al. [57] reported a 406% and 2600% cell count increase in the thickened and centrifuged sludge, respectively, in a DWTP equipped with dissolved air flotation (DAF). A similar high accumulation was also reported for the backwash of the direct filtration process [45].
Pre-oxidation may decrease the risk of cyanobacterial accumulation in the clarifier and sludge [43]. Two DWTPs (the same source for intake water with low cyanobacteria cells; maximum < 500 cells/mL) with chemically enhanced conventional treatment processes were studied, but only one of the DWTPs was equipped by pre-ozonation [43]. Pre-ozonation (initial concentration: 0.3–0.8 mg/L, contact time: 6.3 min) decreased cell accumulation in the surface of the clarifier and filters by up to 1450 times as compared to the DWTP without pre-ozonation. Accordingly, an up to 7 times lower cell accumulation was observed in the sludge of the DWTP with pre-ozonation (Figure 1).
In many DWTPs, the supernatant of the stored sludge is recycled to the head of the plant as the spent filter backwash water [45,57,62]. A full-scale study on a low-risk DWTP (3400 cells/mL at the intake water) documented that cyanobacterial cell counts in intake water increased by up to 43% after recycling the supernatant. Surprisingly, 80% of the transferred cells from the supernatant water were viable [60]. A recent laboratory investigation on intake water that contained 1 × 106 cells/mL of cultured M. aeruginosa reported that although conventional treatment maintained the treated effluent parameters at below WHO and USEPA guidelines, recycling of the sludge supernatant resulted in an additional increase in cells and cyanotoxins levels in the influent by up to 7 × 104 cells/mL and 0.26 µg/L MC-LR, respectively [63].

3. Pre-Oxidation Impact on Cyanobacteria Cells, Viability, and Cyanotoxins

3.1. Impact of Pre-Oxidation on Cyanobacteria Cell Counts

Cyanobacterial entry into DWTPs can be dampened by using pre-oxidation. Pre-oxidation may cause cell lysis, damage, and cyanotoxin release and degradation. Several studies were conducted to evaluate the pre-oxidation impact on cyanobacteria (e.g., cell viability and lysis) and cyanotoxins (release and degradation). A recent study tried to map the treatment barriers against cyanobacteria cells and cyanotoxins in drinking water facilities [10]. The results showed that the efficiency of the multi-barrier approach depends on the species present, metabolite concentration, and pre-oxidation dose [10]. Table 1, Table 2, Table 3 and Table 4 summarize the literature on the impact of pre-oxidation on cyanobacteria (cultured-based and natural blooms) for four common oxidants (chlorine, ozone, potassium permanganate, and hydrogen peroxide). Table 1, Table 2, Table 3 and Table 4 show that CT (residual concentration × contact time) is a main driver of cyanobacterial cell lysis, damage, cyanotoxin release, and degradation.
Although some studies have reported a reduction of more than 90% in taxonomic cell counts following pre-oxidation in the lab-cultured cells, Zamyadi, et al. [35] reported a cell reduction of 70% at high chlorine exposure (CT 296 mg min/L). Fan, et al. [37] showed a limited impact of chlorine exposure (CT 104 mg min/L) on the taxonomic cell counts of Microcystis aeruginosa (logarithmic phase). These observations might be related to the cyanobacteria stage of life and agglomeration. Furthermore, comparing the taxonomic cell count percentage in cultured-based and natural bloom studies demonstrates the lower impact of pre-oxidation during natural blooms. Figure 2 exhibits a lower impact of pre-ozonation (2 mg/L) on cell number reduction in a natural bloom in comparison with lab-cultured cyanobacteria.
Table 1, Table 2, Table 3 and Table 4 and Figure 2 show that pre-oxidation, even at high CTs, may not be able to cause complete cell lysis. Consequently, it is important to clarify how far the pre-oxidation can cause viability loss and cyanotoxin release.
Table
Table 1. Summary of the literature on the impact of pre-chlorination on cyanobacteria (cultured and natural blooms). HV: high viability, LV: low viability, DV: development stage, MA: maintenance stage.
Table 1. Summary of the literature on the impact of pre-chlorination on cyanobacteria (cultured and natural blooms). HV: high viability, LV: low viability, DV: development stage, MA: maintenance stage.
Dominant Cyanobacteria
(Cell Density)		Lab/FieldCl2 Dose (mg/L)Contact Time (min)CT (mg min/L)Cell Count Reduction %Cell Viability %ToxinsReferenceComment
Microcystis
(2 × 106 cells/mL)		Lab1–2-min. 15
max. 90		-min. 83
max. 18.4		99% degradation[66]Saline solution; exact dose and contact time were not provided; no residual; CT evaluation weak; no cell-bound
D. circinalis
(46,000 cells/mL)		Lab2
3		0–60min. 1.8
max. 50		-min. 15%
0 for CT 5.8		>100% release (CT 5.8)
>90 degradation (CT 50)		[67]River water; using fluorescein diacetate (FDA) for viability
Microcystis
(6 × 104 cells/mL
(2.5 × 105 cells/mL)
(5 × 105 cells/mL)		Lab2
4.5
10		0–60min. 3
max. 296.1		max. 76%->100% release (CT 5)
>90 degradation (CT 35)		[35]River water, ultrapure water; no viability was reported
Microcystis
(7 × 105 cells/mL)		Lab3, 4, 51, 2, 5, 10, 20, 30, 60min. 2.8
max. 104		Limited impact<5% (CT 4)25% degradation (CT 2.8)
Complete degradation (CT 104)		[37,68]Ultrapure water
Microcystis
(2 × 106 cells/mL)		Lab0.5
0.7
1.5		5, 11, 50, 60, 120min. 2.5
max 180		-<5% (CT 180)10% degradation
40% increase in released		[69]Lake water; no CT reported
Microcystis
(106 cells/mL)		Lab0.2, 0.4, 0.8Range 0–480min. 12
max. 396		-18% (at CT 12)
0.1% (at CT 396)		-[70]Lake water; no CT reported; no cell count; no toxin
Microcystis
(106 cells/mL)		Lab1, 2, 4, 81, 2, 4, 8, 16, 32, 60HV
min. 0.98
max. 361
LV
min. 0.98
max 200		-HV
95–0% (CT > 15)
LV
44–0% (CT > 15)		HV
CT↑—degradation↑
Complete (CT 108)
CT↑—degradation↑
> 50% release CT > 7
> 62% degradation at highest CT		[71]Ultrapure water; two viability range
Microcystis
(1 × 106 cells/mL)
(2 × 106 cells/mL)		Lab1, 2, 4, 81, 2, 4, 8, 16, 32, 60DV
min. 3.8
max 356
MA
min 3.7
max 293		>95% reduction (CT > 13.3)
>95% reduction (CT > 11.9)		No cell viability after oxidationSame as cell death[72]Ultrapure water; two stage of life
Microcystis-Colony
(105 cells/mL)		Lab0.3, 0.5, 1, 2Range 0–20 minmin. 0.97
max. 52		-Depends on colony size
(0–95%)		Release and degradation Colony-size-dependent[73]Lake water; different colony size; no cell count
Natural bloomFieldCl2/DOC: 0.05–3.60–20 minmin. 0.15
max 6.8		>80% increase (CT 6.8)88% reduction Complete release CT:4 (Cl2/DOC: 0.3)[74]No CT provided; CT estimated; Chl-a measured as cell damage surrogate
Natural bloom
US: (3 × 106 cells/mL) - Planktothrix agardhii
Canada: (3 × 105 cells/mL) -
D. spiroides		FieldCl2/DOC:
0.05, 025, 0.15, 0.1, 1		0–20 minUS
min 0.13
max 15
CA
min 0.3 max 21		-Complete degradationComplete degradation
CT 11 (US), CT 7.5 (CA)		[75]No cell viability; no cell count; Chl-a measured as cell damage surrogate
Natural bloom
(3.3 × 105 cells/mL)
D. spiroides
(5.4 × 104 cells/mL)
M. aeruginosa		Field0.2, 0.60–120 minmin 0.15
max 3.84		min. CT 5% decrease
max. CT 34% decrease		min CT: 82%
max CT:55%		CT 3.84: 23% decrease[76]Soft chlorination (low dose)
Natural bloomField2, 50–60 minmin 1.14
max 14.8		min. < 5% reduction
max. > 50% reduction		-2 mg, CT 10, >200% release
5 mg, CT 20, >200% release		[77]No cell viability
Table
Table 2. Summary of the literature on the impact of pre-ozonation on the cyanobacteria (cultured and natural bloom).
Table 2. Summary of the literature on the impact of pre-ozonation on the cyanobacteria (cultured and natural bloom).
Dominant Cyanobacteria
(Cell Density)		Lab/FieldO3 Dose (mg/L)Contact Time (min)CT (mg min/L)Cell Count Reduction %Cell Viability %
(for CT)		ToxinsReferenceComment
Microcystis
(2 × 106 cells/mL)		Lab1
2		-min. 12
max 16		-CT > 54, complete lossCT = 12 complete
degradation		[66]Saline solution; exact dose and contact time were not provided; no residual; CT evaluation weak
Microcystis
(7 × 105 cells/mL)		Lab2, 4, 65min. < 0.22
max. 2.29		-Min CT: 50%
Max CT: 8.5%		>100% release (high CT)
50% degradation		[37,68]Ultrapure water
Microcystis
D. flos-Aquae
(2.5 × 104 cells/mL
(1.5 × 105 cells/mL)		Lab0.5, 2, 40.5–10min. < 0.2
max. 22		32% for 2 mg/L
41% for 4 mg/L		Complete loss,
CT < 0.2		-[64]Ultrapure; no flow cytometry
Microcystis
(2 × 105 cells/mL)
Oscillatoria
(2800 cells/mL)
Lyngbya sp.
(1600 cells/mL)		Lab0.63–524 hmin. 0.5
max 17		100% reduction (CT 0.5)Complete loss,
(CT > 2)		-[78]River water; Chl-a measured as cell damage surrogate; no toxin measurement
Microcystis, Dolichospermum
(4 × 105 cells/mL)		Lab0.5, 1, 25, 10max. 2.5>95% reductionComplete loss-[79]Natural water; no toxin measurement
Microcystis, Dolichospermum
(1.2 × 105–2 × 106 cells/mL)		Field2, 3, 4, 50–10min. 1.4
max 16.8		75% reduction (CT 16.8)CT 3.2: 45%
CT 16.8: 15%		CT < 2, more than 100% release[65]Natural bloom
Natural bloom
US (3 × 106 cells/mL)—Planktothrix agardhii
CA (3 × 105 cells/mL)—
D. spiroides		FieldO3/DOC:
0.05—0.75		0–20US-min. 1.5
max. 3
CA-min 0.2
max. 4.1		-->80% degradation
CT 4.1(CA)		[75]No cell viability; no cell count; Chl-a measured as cell damage surrogate
Natural bloom
(3.3 × 105 cells/mL)
D. spiroides
(5.4 × 104 cells/mL)
M. aeruginosa		Field0.1, 0.30–10max: 0.86max CT 14% decreasemax CT: 79%14% degradation
No release		[76]Soft ozonation (low dose)
Table
Table 3. Summary of the literature on the impact of potassium permanganate on cyanobacteria (cultured and natural bloom).
Table 3. Summary of the literature on the impact of potassium permanganate on cyanobacteria (cultured and natural bloom).
Dominant Cyanobacteria (Cell Density)Lab/FieldKMnO4 Dose (mg/L)Contact Time (h)CT (mg min/L)Cell Count Reduction %Cell Viability %
(for CT)		ToxinsReferenceComment
Microcystis
(2 × 106 cells/mL)		Lab1–2-min. 15
max. 600		-min. CT: 60%,
CT > 60: complete loss		CT: 30 Complete dissolved degradation[66]Saline solution; exact dose and contact time were not provided; no residual; CT evaluation weak
Microcystis
(7 × 105 cells/mL)		Lab1, 5, 100.25–7min. 28.7
max. 2642		14% cell number reduction (CT max)CT 2600: complete lossRelease at CT > 70
Complete degradation CT 2600		[37,68]Ultrapure water
Microcystis, Dolichospermum
(4 × 105 cells/mL)		Lab2, 520max. 45610% reduction at highest CTCT 456: 18% viability-[80]Natural water; no toxin measurement
Microcystis
Bloom from Lake Erie		Lab
Field		0.5–81–5min. 120
max. 1920		-Cell, CT 1920: 2%
Bloom, CT 1920: 40%		-[81]No cell count and toxin; no CT; CT with lower doses was unable to decrease viability
Table
Table 4. Summary of the literature on the impact of hydrogen peroxide on cyanobacteria (cultured and natural bloom). h: hour, d: day.
Table 4. Summary of the literature on the impact of hydrogen peroxide on cyanobacteria (cultured and natural bloom). h: hour, d: day.
Dominant
Cyanobacteria (Cell Density)		Lab/FieldH2O2 Dose (mg/L)Contact TimeCT (mg h/L)Cell Count Reduction %Cell Viability %
(for CT)		ToxinsReferenceComment
Microcystis
(3.7 × 106 cells/mL)		Lab3.4, 174 h, 2 d, 4 dmin. 13.6
max. 1632		min. CT: 8% reduction
max. CT: 89% reduction		K+ release
min. CT: 81%
max. CT: 5%		CT > 816
26% MC release		[82]K release as a surrogate for cell damage; no CT provided
Microcystis
(7 × 105 cells/mL)		Lab10.2, 51, 1020.1 d–7 hmin. 189.3
max. 17,678		Limited changemin. CT: 86%
CT 4770: 7%		No release,
CT 364: >95% degradation		[37,68]Ultrapure water
Pseudanabaena
(107 cells/mL)		Lab3, 5, 10, 202 h, 4 h, 8 h, 2 d, 4 dmin. 6
max. 960		min. CT: No change
max. CT: >90% reduction		CT 120: 2%-[83]Reservoir water; no toxins
Microcystis
(6 × 106 cells/mL)		Lab1–150.1 d–7 dmin. 2.4
max. 2520		CT 1680: 95% reductionmax. CT
3% viability		CT > 1512,
82% degradation		[84]Culture; no CT provided
Microcystis, Dolichospermum
(4 × 105 cells/mL)		Lab5, 106 hmin. 13.9
max. 96.1		<5% reductionmin. CT: 39%
max. CT: 30%		-[79]Natural water
Natural bloom:
(3.3 × 105 Cells/mL)
D. spiroides:
(5.43 × 104 cells/mL)
M. aeruginosa		Field106 h–1 dmin. 47
max. 140.7		max. CT 52% reductionmin. CT: 60%
max. CT: 40%		No release
max.; 15% MC degradation		[76]-

3.2. Chlorination

Figure 3 is a reconstructed graph from the cell viability results following pre-chlorination based on the oxidant exposure (CT). Parameters such as background water quality (e.g., pH and dissolved organic carbon (DOC)) which have an impact on the oxidant demand are included in the CT concept. Therefore, a comparable level of damage should be found by comparing cell viability results using oxidant exposure (CT) for lab-cultured and natural blooms. Figure 3 demonstrates that at the same level of chlorine exposure, the natural bloom is more resistant to pre-chlorination as compared to lab-cultured cells. In other words, lab-cultured studies are not representative of natural bloom pre-chlorination. Fan, et al. [73] reported that the level of cell damage and toxin release depends on the colony size. Figure 3b shows the cultured-based studies fitted with the Chick–Watson equation. Although the results from different unicellular studies are aligned with each other, the colonial Microcystis chlorination shows a different cell damage rate. This could be related to the agglomeration of cyanobacteria cells and increasing the mucilage sheath in colonial cyanobacteria [73]. Despite using the CT calculation to compare the results, Figure 3c demonstrates different cell damage rates for each study of real bloom after chlorination, and the same level of chlorine exposure may not result in the same level of cell damage. Figure 3c shows that cyanobacterial bloom oxidation could be site- and bloom-specific, depending on the agglomeration, cyanobacteria (bloom) stage of life, and metabolic functions. Higher cell damage following pre-oxidation (especially with higher CTs) can lead to higher cyanotoxin release, which cannot be removed during conventional treatment. Soft chlorination showed cell damage by up to 45% and total microcystin (MC) degraded by up to 23%, while no cyanotoxin release was observed [76]. In addition, soft chlorination may cause lower disinfection by-products as a lower oxidant concentration is used in this approach.

3.3. Ozonation

Figure 4 shows the impact of pre-ozonation on cyanobacteria cell damage for cultured-based and natural bloom studies. Figure 4a demonstrates lower cyanobacteria cell damage for a specific ozone exposure for natural blooms as compared to the lab-cultured cyanobacteria. The model fit results (Figure 4b) show a higher cell damage rate for the lab-cultured cyanobacteria in comparison to the natural bloom. As per soft oxidation, soft pre-ozonation was reported to cause up to 21% of cell damage and 14% of MC degradation, while no MC release was observed simultaneously [76]. Such an observation implies the effectiveness of soft pre-ozonation to damage the cells without cyanotoxin release.

3.4. Potassium Permengeanate

Figure 5 demonstrates that the viability loss of the lab-cultured studies harvested in the logarithmic phase is lower than those that harvested in the stationary phase. This observation implies the impact of the cyanobacteria stage of life on pre-oxidation efficiency. A comparison of the cell viability results of the lab-cultured with natural bloom studies following potassium permanganate pre-oxidation confirms the higher resistance of real cyanobacterial bloom cells (Figure 5). In addition, the degradation rate constant of dissolved MCs was higher than that released by MCs for high potassium permanganate doses [36,81].

3.5. Hydrogen Peroxide

Matthijs, et al. [86] reported that a concentration of 2 mg/L H2O2 was able to decrease cyanobacteria (natural bloom) by two logs within 3 days. In addition, cyanobacteria remained at a low abundance level for 7 weeks following H2O2 addition. Figure 6 demonstrates that natural blooms are more resistant to H2O2 than the lab-cultured cyanobacteria, as observed for other oxidants (Figure 2, Figure 3, Figure 4 and Figure 5). Foo, et al. [87] reported that the impact of H2O2 on cyanobacteria is dependent on the residual concentration (C) and contact time (T). In addition, the authors concluded that toxic and non-toxic Microcystis aeruginosa are impacted by H2O2 with the same trend. Zhou, et al. [84] stated that a low dose of H2O2 (<5 mg/L) would have a low and recoverable impact on the lab-cultured Microcystis. On the other hand, the higher the H2O2 dose (>8 mg/L), the higher necrosis, cell death, and consequent cyanotoxin release. A medium dosage of H2O2 with low to medium contact time can activate apoptosis-like programmed cell death (AL-PCD) [84]. The cellular energy required for AL-PCD is provided from the transcriptional, biochemical, and structural changes. Zhou, et al. [84] documented the maximum cell death with low MC production by AL-PCD activation. Zamyadi, et al. [17] studied the impact of H2O2 on blooms and lab-cultured cyanobacteria (Microcystis aeruginosa). The results highlighted a delayed impact of H2O2 on cyanobacteria cells after complete depletion of H2O2 during stagnation (up to one week) [17]. Chl-a and phycocyanin (PC) fluorescence were significantly declined by 93% and 74% in natural bloom and lab-cultured samples, respectively. Additionally, the lab-cultured results revealed delayed MC release during stagnation [17].
Besides the current oxidants, peracetic acid (PAA) has been used in wastewater treatment facilities as a disinfection alternative for chlorine [88]. Almuhtaram and Hofmann [89] studied the impact of PAA and PAA/UV on cyanobacteria and cyanotoxin removal. The results show that 10 mg/L of PAA with 60 min contact time was able to degrade MC-LR by 80% (3.46 M−1 s−1 lower reaction rate as compared to HOCl 1.2 × 102 M−1s−1). In addition, the results elaborated that PAA alone can barely remove cyanobacteria, except at a high dose (10 mg/L) and with lower cyanobacterial cell counts (105 cells/mL).

3.6. Considerations on the Impact of Pre-Oxidation on Downflow Processes

The impact of pre-oxidation on downflow processes should also be considered as it may influence the removal of cyanobacteria by coagulation, flocculation, and sedimentation. Previous studies have been reported that pre-oxidation has a positive impact on enhancing cyanobacterial removal through coagulation/flocculation and sedimentation [27,28,31,32,34,90]. Pre-oxidation can cause morphological deformation [82] and changes in the surface charge of the cells, leading to increased cell removal efficiency during coagulation/flocculation [37].
KMnO4 increases the binding potential to the coagulant by oxidizing organic matter (extracellular and released cell-bound) to lower molecular weight fractions, as well as forming colloids (by MnO2) to be adsorbed to the cyanobacterial cells and forming larger flocs [32,34,81]. Xie, et al. [27] reported that KMnO4 exposure (CT: 10 mg min/L, estimated) could increase cyanobacteria cell removal by 22% during coagulation/flocculation. In addition, pre-ozonation with CT: 4, 10, and 20 mg min/L (estimated) led to an increase in cyanobacteria cell removal during coagulation by 14%, 20%, and 24%, respectively [27]. Cyanobacteria cell removal during coagulation was improved in a full-scale DWTP equipped by pre-ozonation systems (CT: 2.52–3.78 mg min/L (estimated)) [43]. Pre-oxidation may cause metabolite release (organic matter and cell-bound cyanotoxins) following cyanobacterial cell damage. Besides the challenge to remove dissolved cyanotoxins, coagulation efficiency can be compromised by high algal organic matter release following pre-oxidation. Xie, et al. [27] showed that due to pre-ozonation with CT > 4 mg min/L (estimated), cyanobacteria cell viability was completely degraded, and consequently, organic matter concertation increased. Further, Barešová, et al. [91] demonstrated that pre-ozonation (CT < 40 mg min/L (estimated)) could interrupt the coagulation (Al/Fe-based) efficiency of DOC removal (in comparison with higher CTs) due to the degradation of high molecular weight algal organic matter to low molecular weight compounds.
It is noteworthy to recall that H2O2 can have a delayed impact on cyanobacteria and, potentially, cyanotoxin release after complete degradation of the oxidant [17]. This delayed cyanotoxin release should be considered in the downstream processes, as well as in sludge handling.
The oxidant exposure must be adjusted to maximize cell damage and cyanobacteria cell removal (directly or after coagulation) and minimize cyanotoxin release and cell accumulation in the sludge, simultaneously. Figure 7 summarizes the pre-oxidation (soft and normal) advantages/disadvantages of cyanobacteria and cyanotoxins during water treatment. In fact, soft pre-oxidation (low CT of Cl2 and O3) can (1) partially degrade cyanobacteria cells, (2) cause low cyanotoxin release, (3) improve coagulation efficiency to remove cells, and (4) cause low cell accumulation in the downflow processes.

4. Sludge Storage, Oxidation, and Handling

Cyanobacteria and cyanotoxins (cell-bound) accumulate in the sludge of clarifiers throughout the flocculation/coagulation/sedimentation processes. This cyanobacteria-laden sludge remains in the sludge holding tank before disposal. In addition, potential options to treat cyanobacteria-laden sludge need to be considered. Furthermore, safe (healthy, both operationally and environmentally) cyanobacteria-laden sludge handling approaches are required.

4.1. Fate of Cyanobacteria and Cyanotoxins during Sludge Storage

Several studies (Table 5) demonstrated that cyanobacteria cells could stay viable within 2–12 days in the stored sludge. The loss of viability and consequent cyanotoxin release caused an increase in dissolved cyanotoxin concentrations during sludge storage [13,40,45,46,47,48,49,50,51,52]. However, dissolved cyanotoxins in stored sludge can be adsorbed onto the remained PAC injected into the intake water [56], flocs [50] or it can be biodegraded by cyanotoxin degrader species [58,92].
Besides cell survival potential during sludge storage, some studies have hypothesized that cyanobacteria can also grow in stored sludge [53,54,55]. Water Research Foundation (WRF) and Water Research Australia [53] documented that concentrations of DOC, MC-LR, and cylindrospermopsin in stored coagulated sludge contained M. aeruginosa and C. raciborskii exceeded the expected concentrations by 4–10-fold based on the cell quota (if all cell-bound metabolites are released) within 7–16 days, respectively. Dreyfus, et al. [55] studied the fate of stored sludge that contained cultured M. aeruginosa, D. circinale, and C. raciborskii within 18 days. The authors demonstrated that DOC, MC-LR, MC-LA, and CYN concentrations increased by up to 5-, 2.2-, 1.2-, and 2.5-fold during storage, respectively. Another investigation on stored sludge containing cultured M. aeruginosa and D. circinale reported that taxonomic cell counts increased by up to 4.2-fold in sludge stored in a lagoon within 7 days [54]. The authors also reported that the concentrations of cyanobacterial metabolites increased by up to 5 times in the sludge supernatant within 20 days. In the worst case, cyanobacteria could survive by up to 35 days in the stored sludge [54]. Despite the important findings of the previous studies on cell survival and metabolite release during sludge storage, cyanobacterial cell growth during sludge storage is yet to be explored in detail. In these studies, cell and metabolite increase during sludge storage might be due to the cell growth or to either the (1) underestimation of cell quota, (2) increase of metabolite production per cell during storage, or (3) additional cell settling from the supernatant to the sludge during the storage [53,54,55].
Our recent study on the cyanobacteria-laden sludge of a DWTP documented cell depletion, survival, and growth in different sludge samples [58]. Cell growth was observed in four out of eight sludge samples (different sampling dates) stored in the dark for 7–38 days. In the worst-case scenario, taxonomic cell counts increased from 2.7 × 106 to 5.3 × 106 cells/mL within 16 days (96% cell growth). Cell growth was also confirmed by increasing cyanobacterial biomarkers such as the “Pentose phosphate pathway” marker, which is responsible for the heterotrophic growth of cyanobacteria [93].
Table
Table 5. Impact of sludge storage on cyanobacteria and cyanotoxins. STX: saxitoxin, PACl: colyaluminium chloride, CTSAC: Chitosan-aluminum chloride.
Table 5. Impact of sludge storage on cyanobacteria and cyanotoxins. STX: saxitoxin, PACl: colyaluminium chloride, CTSAC: Chitosan-aluminum chloride.
Initial Characteristics of Cyanobacteria/
Coagulation/Sedimentation Process		Initial Condition of Cyanobacteria and Cyanotoxins in the Stored SludgeObservationReference
Cultured M. aeruginosa
(1 × 106 cells/mL)
(Jar test, 70 mg/L alum)		8 × 106 cells/mL,
2500 µg MC-LR/L		Cell survival (2 days); cell lysis and cyanotoxin release (2 days); degradation of dissolved cyanotoxins (8–10 days)[13]
Cultured D. circinale and C. raciborskii (1.0 × 105 cells/mL)
(Jar test, 40 mg/L alum)		Sludge supernatant:
D. circinale:
1300 cells/mL
STX: 0.4 µg/L		Cells remained viable up to 7 days; cell lysis and toxin release within 3 days[45]
Cultured M. aeruginosa
(2 × 106 cells/mL)
(Jar test, 15 mg/L AlCl3) 		18 µg/L dissolved MCsCell lysis and cyanotoxin release after 6 days[40]
Cultured M. aeruginosa
(1 × 106 cells/mL)
(Jar test, 4 mg/L PACl-optimum dose)		20 µg/L dissolved MCsCell lysis and cyanotoxin release within 6–12 days[46]
Microcystisflos aquae
(5.2 × 105 cells/mL)
(Jar test, 100 mg/L alum)		Sludge supernatant:
MC-RR, MC-YR: < 2 µg/L		Cell survival (5 days); cell lysis and cyanotoxin release (5–10 days); degradation of dissolved cyanotoxins (up to 15 days)[62]
Cultured M. aeruginosa
(1 × 106 cells/mL)
(Jar test, 15 mg/L ALCl3, 4 mg/L PACl)		−0.9 bar vacuum pressure for dewatering the sludge
23 µg/L total MCs		Cell lysis and cyanotoxin release within 4–6 days; optimum sludge storage time for AlCl3 and PACl was suggested to be 4 and 2 days, respectively.[47]
Cultured M. aeruginosa
(1 × 106 cells/mL)
(Jar test, 0–70 mg/L FeCl3)		~1 µg/L dissolved MCsCell lysis and cyanotoxin release (2–8 days); degradation of dissolved cyanotoxins (> 10 days)[48]
Myponga reservoir
Cultured M. aeruginosa (2.3 × 105 cells/mL)
Cell-bound MC-LR: 4.7 µg/L
Dissolved MC-LR: 2.0 µg/L
(Jar test-80 mg/L alum)		Sludge supernatant after 1 day storage:
Cells: 4300 cells/mL
Cell-bound MC-LR: 0.5 µg/L
Dissolved MC-LR: 2.5 µg/L		Cell survival (4 days); cell lysis and cyanotoxin release (4–7 days); degradation of dissolved cyanotoxins (> 4 days)[53]
Myponga reservoir
Cultured M. aeruginosa (3.1 × 105 cells/mL)
DOC: 10.1 mg/L
Cell-Bound MC-LR: 5.0 µg/L
Dissolved MC-LR: 2.9 µg/L
(Jar test-80 mg/L alum)		Sludge supernatant after 1 day storage:
DOC: 5.2 mg/L
Cell: 2760 cells/mL
Cell-bound MC-LR: <DL
Dissolved MC-LR: 4.0 µg/L		Cell growth (within 7–16 days) confirmed by DOC and MC-LR cell quota
Myponga reservoir
Cultured C. raciborskii (3.1 × 105 cells/mL)
DOC: 10 mg/L
Cell-bound CYN: 2.5 µg/L
Dissolved CYN: 0.7 µg/L
(Jar test-80 mg/L alum)		Sludge supernatant after 1 day storage:
DOC: 6.0 mg/L
Cell: 7080 cells/mL
Cell-bound CYN: 1.0 µg/L
Dissolved CYN: 0.8 µg/L		Cell growth (within 7–23 days) confirmed by DOC and CYN cell quota
River Murary
Cultured C. raciborskii (3.1 × 105 cells/mL)
DOC: 8.63 mg/L
Cell-bound CYN: 2.7 µg/L
Dissolved CYN: 0.3 µg/L
(Jar test-80 mg/L alum)		Sludge supernatant after 1 day storage:
DOC: 4.9 mg/L
Cell: 4140 cells/mL
Cell-bound CYN: 0.3 µg/L
Dissolved CYN: 0.9 µg/L		Cell growth (within 15–23 days) confirmed by DOC and CYN cell quota
Cultured M. aeruginosa
(1 × 106 cells/mL)
(Jar test- 15 mg/L AlCl3, 50 mg/L FeCl3, 15 mg/L PAFC)		20 µg/L dissolved MCs
1–4.2 mg/L dissolved polysaccharides
4 mg/L chla		Cell lysis and toxin release (2–10 days)[49]
Cultured M. aeruginosa
(2 × 106 cells/mL)
(Jar test, 2.6 mg/L chitosan- 7.5 mg/L AlCl3 (CTSAC)		9 µg/L dissolved MCs
(after coagulation)
18 µg/L dissolved MCs
(without coagulation); the difference is due to adsorption in CTSAC		Toxin release (0–4 days); degradation of dissolved cyanotoxins (6–10 days)[50]
M. aeruginosa, D. circinale, C. raciborskii
(3.0 × 105 cells/mL)
(Jar test, 80 mg/L Alum)		Sludge supernatant after 1 day storage:
DOC: 5.2–6.5 mg/L
Cell: 2162–7080 cells/mL
Cell-bound MC-LR: <0.5 µg/L
Dissolved MC-LR: 2.5–4.0 µg/L
Cell-bound CYN: 1.0 µg/L
Dissolved CYN: 0.8 µg/L		Increased DOC, MC-LR, MC-LA, and CYN to higher the expected values
(hypothesis: increase of the metabolite production, cell growth or both)		[55]
M. aeruginosa and D. circinale
(8.6 × 104 cells/mL)
(Jar test, 80 mg/L Alum)		Non-coagulated sludge: 5.0 × 106 cells/mL
Coagulated sludge: 5.4 × 105 cells/mL		Cell survival (up to 35 days); 4.2× increase in cell counts in the sludge lagoon within 7 days; increased metabolites to higher the expected values (up to 5×); increased cell counts in the sludge
(hypothesis: cell growth, additional settling, or both)		[54]
Cultured M. aeruginosa
× 105 cells/mL)
(Jar test, 15 mg/L AlCl3, 50 mg/L FeCl3, 15 mg/L PAFC)		1 µg/L dissolved MCs
Cell lysis and toxin release (4–6 days); degradation of dissolved cyanotoxins (6–10 days)[51]
Cultured Oscillatoria sp.
(1.0 × 104 cells/mL)
(Jar test, 5 and 10 mg/L PAFC)		1.0 mg/L chla
2.3 µg/L cell-bound protein
8.6–11.4 µg/L dissolved CYN		Increase in chla level after 4 days, suggesting cell growth; loss of cell integrity after 2 days, while cells remained viable up to 8 days; increase in dissolved CYN, showing toxin release within 4 days[94]
Cultured C. raciborskii
(1 × 106 cells/mL at late exponential phase)
(Jar test, 10 mg/L PAFC)		1.1 µg/L dissolved CYN
2 mg/L cell-bound protein		Cell lysis and toxin release after 6 days; degradation of dissolved cyanotoxins after 10 days[52]
n/aSludge of a DWTP containing natural cyanobacterial blooms stored for 7–35 days in the darkness (8 samples).
0.7 × 105–5.6 × 106 cells/mL
25–7130 ng/L cell-bound MCs
38–349 ng/L dissolved MCs		Cell growth in 4/8 samples after 9–35 stagnation days; cell death in the rest 4/8 samples; degradation of dissolved cyanotoxins after 8 days[58]

4.2. Cyanobacteria-Laden Sludge Treatment

A summary of studies on the treatment of cyanobacteria-laden sludge is presented in Table 6. The available data demonstrated that sludge oxidation could not completely remove cyanobacteria cells and metabolites from the sludge [57,59]. Sludge is often stored after oxidation, while its supernatant can be recycled to the head of the DWTP. Thus, the impact of oxidation on sludge storage should be investigated. Recent findings showed no remarkable benefits in sludge oxidation followed by sludge storage as compared to only sludge storage [59]. The maximum additional taxonomic cell count decreased by a combination of oxidation (KMnO4 or H2O2) and storage was 32% as compared to storage only. However, oxidation/storage could cause a remarkable cell growth (by up to 145%) and toxic gene copy numbers of mcyD increase (by up to 13.0×) in some sludge samples [59]. This phenomenon can be attributed to gene expression regulation due to the presence of oxidative stresses [58,59,95,96]. Similarly, sludge oxidation could not completely remove cyanobacteria and cyanotoxins from the supernatant sludge [59]. Finally, the costs and by-product formation during the oxidation of organic-matter-rich sludge should be considered [58].

4.3. Sludge Handling Challenges

In general, the sludge supernatant is recycled to the head of the DWTP or is discharged into the source [13,56,97]. The solid phase either can be transferred to the WWTP or is applied for landfilling [98,99,100]. Less environmentally friendly approaches such as untreated residual discharge into lakes or ponds can be also applied in some circumstances [101]. The re-use of DWTPs’ residuals is growing [99,102,103,104]. However, an investigation demonstrated that the half-life of MC analogs varies from 8 to 18 days in soil [105]. Since there is a risk of soil and groundwater contamination, landfill and field applications of cyanobacteria-laden sludge should be avoided. Overall, cyanobacteria-laden sludge should be treated before disposal either in situ or via sending it to wastewater treatment plants.
Flocs may have a protective role during sludge storage for M. aeruginosa [40,46,47,48,52]. In contrast, Li, et al. [52] documented that polyaluminium ferric chloride (PAFC) can stimulate the lysis of C. raciborskii and CYN release by up to 94% during sludge storage. This may occur in the sludge and lead to cyanotoxin release. However, all studies have been conducted in laboratory conditions and on cultured-based cyanobacteria. In fact, due to complex parameters such as the presence of various cyanobacterial cells in various forms (aggregated, multicellular), ages, and viabilities, the design of such experiments in full scale is complex.
Stresses such as oxidation and storage can shift cyanobacterial communities towards resistant genera (e.g., Microcystis and Aphanocapsa), which can produce MCs [56,58,59]. Thus, the survival probability of MC producer species can increase during sludge oxidation or storage. The fate of cyanotoxins in the sludge is complex due to the simultaneous occurrence of various phenomena such as cell survival, growth, lysis, cell-bound cyanotoxin release, and released cyanotoxin degradation [53,54,55,56,59,106,107]. Based on the increased risk of cell lysis and cyanotoxin release during sludge storage, some studies have suggested that cyanobacteria-laden sludge should be disposed of prior to 4 days to avoid metabolite release [47,51,108]. However, these studies only focused on metabolite release and not on cell survival/growth phenomena. Additionally, the possibility of sludge disposal can be a technical and financial challenge in large DWTPs.

5. Decision Framework to Manage Cyanobacteria and Cyanotoxins in Drinking Water Treatment Plants

5.1. Framework Basis

Since cyanobacterial cells and their associated metabolites, including cyanotoxins, as well as taste and odor agents such as geosmin and 2-Methylisoborneol (MIB), affect water and sludge quality, monitoring should be applied for the evaluation of the water treatment chain and sludge handling.
Microscopy taxonomic cell count techniques have been widely applied to evaluate the water and sludge in previous studies [12,18,43,44,56,77]. Previous cyanobacterial monitoring guidelines were prepared based on taxonomic cell counts and biovolumes [109,110,111]. A recent study suggested 0.3 mm3/L biovolumes as the vigilance level [109]. However, bias related to human error [112], the negative impact of Lugol’s iodine on biovolumes [113], cell underestimation/overestimation due to the presence of aggregated cells [114], and the presence of debris and sediments, especially in the sludge samples [56], may affect the results. More importantly, the significant time required for taxonomic cell counts is a major barrier in using them for a real-time/practical approach.
In situ fluorometry using on-line probes is a compromising technique for measurement of PC based on relative fluorescence units (RFU) in water resources [18,115,116,117,118,119]. However, the correlation between RFU and biovolume is complex and site-specific [119,120,121]. Previous investigations have reported that various RFUs ranging from 0.7 to 1.8 could correlate with a 0.3 mm3/L biovolume in different sources and bloom events [116,119]. Therefore, it is recommended to perform a correlation between on-line probe readings (RFU) and biovolumes for each water resource. It is noteworthy that the limits of detection and quantification of on-line probes should be considered [116,118].
MC concentration has been introduced in several guidelines such as those of the WHO (1.0 μg/L MC-LR) [122,123] and Health Canada (1.5 μg/L) [124]. Geosmin and MIB negatively affect water quality, raise complaints about taste and odor, and decrease the public’s confidence about the treated water safety [125,126,127,128,129]. Thus, they should be monitored throughout the treatment chain and the recycled sludge supernatant. Using enzyme-linked immunoassay (ELISA) tests for cyanotoxins measurement has been accepted for cyanotoxin monitoring [44,130,131,132]. The reported thresholds for geosmin and MIB are 1.3–4.0 ng/L and 6.3–15 ng/L, respectively [133,134,135]. Since the taste and odor agents are not harmful, but increase complaints and concerns about the water quality [126,127,129,134], olfactory detection can be considered for monitoring and detection [128,136].

5.2. Decision Framework

A decision framework to manage cyanobacteria and cyanotoxins in DWTPs is presented in Figure 8. The objective of this framework is to minimize cell breakthrough and accumulation throughout DWTPs and sludge. The three steps, (i) source water risk assessment, (ii) treatment breakthrough assessment and management, and (iii) sludge and supernatant risk assessment and management, should be taken for cyanobacteria and cyanotoxin control in DWTPs and sludge. This framework can help water utilities to understand appropriate approaches/strategies against cyanobacteria and cyanotoxins in DWTPs.
Overall, taxonomic cell counts, MCs, and taste and odor agents should be monitored in the (i) intake water, (ii) treatment chain, and (iii) sludge supernatant. These points are subjected to cyanobacteria and cyanotoxin accumulation, leading to a negative impact on water quality.
The optimization of conventional processes may include coagulant dose adjustment, applying aid-flocculants, and lowering the sedimentation and filtration rate during cell breakthrough [12,137,138,139]. Secondary barriers such as pre-oxidation, PAC injection, and GAC, in case of metabolite breakthrough, should be applied [15,25,39,65,140,141,142,143,144]. The impact of supernatant recycling or discharging on the source/intake water quality should be considered during toxic cyanobacterial blooms. Supernatant treatment may be required in the presence of cyanotoxins or taste and odor agents. MC concentration levels should be monitored in the sludge (solids) in case of landfilling or land application. In the case of elevated concentrations of MCs, sludge treatment is required.

6. Conclusions

○
Using the exposure unit (CT) is recommended for cyanobacteria and cyanotoxins oxidation studies, rather than using dose or contact time individually.
○
Regardless of the oxidant type, lab-cultured studies cannot depict the complete picture of natural cyanobacterial bloom behavior during oxidation and may overestimate the oxidation efficiency. In addition, cyanobacterial bloom oxidation is site- and bloom-specific, which could be related to the level of agglomeration, cyanobacteria (bloom) stage of life, and metabolic functions.
○
Soft pre-chlorination and pre-ozonation can compromise cell viability with no or limited cyanotoxin release. Overall, soft pre-oxidation may cause lower disinfection by-products compared to normal pre-oxidation.
○
The cyanobacteria in stored sludge can not only survive, but also grow and release cyanotoxins, even in the dark. Although dissolved cyanotoxins can be degraded during sludge storage, the potential risk of growth and cyanotoxin release should be considered. In fact, the cell growth/depletion in stored sludge is complex and not easy to predict. Therefore, the worst-case scenario should be considered during sludge handling.
○
Due to the low efficacy of sludge oxidation as compared to only stored sludge, as well as the occurrence of cell growth, and gene expression regulation during oxidation/storage, oxidation cannot be a reliable approach in sludge treatment and management.
○
Management of cyanobacteria and cyanotoxins in sludge should be initiated with the minimization of cyanobacteria and cyanotoxin accumulation throughout DWTPs.
○
To control the negative impacts of cyanobacterial accumulation in DWTPs, recycling sludge supernatant to the head of the DWTPs should be regulated during cyanobacterial seasons. Suitable treatment and disposal approaches should be set into guidance and regulations for sludge-containing cyanotoxins.

Author Contributions

Conceptualization, F.J., S.M., S.D., A.Z., S.S. and M.P.; methodology, F.J., S.M., S.D. and M.P.; validation, F.J., S.M., A.Z., S.D. and M.P.; formal analysis, F.J., S.M. and M.P.; investigation, F.J., S.M., S.D., A.Z. and M.P.; writing—original draft preparation, F.J. and S.M.; writing—review and editing, F.J., S.M., S.D., A.Z., S.S. and M.P.; visualization, F.J. and S.M.; supervision, S.D., S.S. and M.P.; project administration, S.S., S.D. and M.P.; funding acquisition, S.D. and S.S. All authors have read and agreed to the published version of the manuscript.

Funding

The authors sincerely acknowledge the financial supports of Algal Blooms, Treatment, Risk As-sessment, Prediction, and Prevention through Genomics (ATRAPP) projects, Génome Québec, Genome Canada and the NSERC Industrial Chair on Drinking Water at Polytechnique Montréal (grant number ALLRP 560764-20).

Institutional Review Board Statement

Not applicable.

Informed Consent Statement

Not applicable.

Conflicts of Interest

The authors declare no conflict of interest.

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Figure 1. Cyanobacterial accumulation in two low risk DWTPs (maximum influx cell: <500 cells/mL). Only DWTP1 had pre-ozonation. The average values are from August to October 2011, adapted from [43].
Figure 1. Cyanobacterial accumulation in two low risk DWTPs (maximum influx cell: <500 cells/mL). Only DWTP1 had pre-ozonation. The average values are from August to October 2011, adapted from [43].
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Figure 2. Comparison of cell count reduction following ozonation (2 mg/L) in the (a) cultured Dolichospermum, Microcystis [64], (b) Natural bloom [65].
Figure 2. Comparison of cell count reduction following ozonation (2 mg/L) in the (a) cultured Dolichospermum, Microcystis [64], (b) Natural bloom [65].
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Figure 3. (a) Comparison of the cell viability results of cultured-based Microcystis and Dolichospermum [37,68,71,72,85] and natural cyanobacterial blooms [74,76,77] following pre-chlorination. [74] used Chl-a as a proxy for cell viability. (b) Cell viability experimental data and fitted model of unicellular [37,68,71,72,85] and colonial Microcystis [73] following pre-chlorination. (c) Cell viability experimental data and fitted model for three different cyanobacterial blooms following pre-chlorination.
Figure 3. (a) Comparison of the cell viability results of cultured-based Microcystis and Dolichospermum [37,68,71,72,85] and natural cyanobacterial blooms [74,76,77] following pre-chlorination. [74] used Chl-a as a proxy for cell viability. (b) Cell viability experimental data and fitted model of unicellular [37,68,71,72,85] and colonial Microcystis [73] following pre-chlorination. (c) Cell viability experimental data and fitted model for three different cyanobacterial blooms following pre-chlorination.
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Figure 4. (a) Comparison of the cell viability results of cultured-based Microcystis, Dolichospermum, Oscillatoria, Lyngby asp. [37,64,68,78,79], and natural blooms [65,76] following pre-ozonation. (b) Cell viability experimental data and fitted model for cultured-based and natural bloom samples following pre-ozonation.
Figure 4. (a) Comparison of the cell viability results of cultured-based Microcystis, Dolichospermum, Oscillatoria, Lyngby asp. [37,64,68,78,79], and natural blooms [65,76] following pre-ozonation. (b) Cell viability experimental data and fitted model for cultured-based and natural bloom samples following pre-ozonation.
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Figure 5. (a) Comparison of the cell viability results of cultured-based and natural bloom samples for different studies following potassium permanganate peroxidation: Microcystis [37,68], Microcystis, Dolichospermum [66,79], and natural blooms [76]. (b) Comparison of the cell viability results of cultured-based samples (Microcystis) following potassium permanganate peroxidation adapted from [81]. (c) Comparison of the cell viability results of natural bloom samples (from Lake Erie) adapted from [81].
Figure 5. (a) Comparison of the cell viability results of cultured-based and natural bloom samples for different studies following potassium permanganate peroxidation: Microcystis [37,68], Microcystis, Dolichospermum [66,79], and natural blooms [76]. (b) Comparison of the cell viability results of cultured-based samples (Microcystis) following potassium permanganate peroxidation adapted from [81]. (c) Comparison of the cell viability results of natural bloom samples (from Lake Erie) adapted from [81].
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Figure 6. Comparison of the cell viability results of cultured-based cyanobacterial cells (Microcystis, Pseudanabaena) [37,68,83,84] and natural bloom cells [76,86] after oxidation by hydrogen peroxide.
Figure 6. Comparison of the cell viability results of cultured-based cyanobacterial cells (Microcystis, Pseudanabaena) [37,68,83,84] and natural bloom cells [76,86] after oxidation by hydrogen peroxide.
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Figure 7. Summary of pre-oxidation (low and medium-high CT) impact on cyanobacteria/cyanotoxins and downflow processes (#: very low impact, +: increase, and -: decrease). Low CT for Cl2 = CT < 4 mg min/L, low CT for O3 = CT < 1 mg min/L, low CT for KMnO4 = CT < 50 mg min/L, and low CT for H2O2 = CT < 50 mg h/L.
Figure 7. Summary of pre-oxidation (low and medium-high CT) impact on cyanobacteria/cyanotoxins and downflow processes (#: very low impact, +: increase, and -: decrease). Low CT for Cl2 = CT < 4 mg min/L, low CT for O3 = CT < 1 mg min/L, low CT for KMnO4 = CT < 50 mg min/L, and low CT for H2O2 = CT < 50 mg h/L.
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Figure 8. Decision framework for cyanobacterial bloom management in drinking water treatment utilities.
Figure 8. Decision framework for cyanobacterial bloom management in drinking water treatment utilities.
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Table
Table 6. Data of cyanobacteria-laden sludge treatment. MIB: 2-Methylisoborneol.
Table 6. Data of cyanobacteria-laden sludge treatment. MIB: 2-Methylisoborneol.
Source of SludgeScaleTreatment Agent/DosageContact TimeInitial ConditionsCell Count ReductionMetabolite ReductionReference
Sludge thickenerLaboratory3 mg/L KMnO42 h5.0 × 104 cells/mL Pseudanabaena>95%-[57]
Laboratory10–100 mg/L PAC1 h100/L MIB-42–100% MIB
Full-scale10 mg/L KMnO415 h (max.)4.3 × 105 cells/mL
(natural blooms)		13–98% total and Pseudanabaena cell counts-
Full-scale10 mg/L KMnO4
20 mg/L PAC		KMnO4: 24–72 h
PAC: 1 h 		3.7 × 105 cells/mL
120 ng/L MIB
(natural blooms)		40–52% in total and Pseudanabaena cell counts20–22% MIB
Sludge holding tankLaboratory5 mg/L
KMnO4		60 min2.3–2.7 × 106 cells/mL
63–161 ng/L MCs
(natural blooms)		46–55% total cell counts0.3–24% MCs[59]
10 mg/L KMnO459–62% total cell counts2–32% MCs
10 mg/L
H2O2		24 h58% total cell counts27% MCs
20 mg/L
H2O2		77% total cell counts41% MCs
Full-scale
(shock oxidation)		10 mg/L KMnO424–72 h2.4 × 106 cells/mL
88–1083 ng/L MCs
(natural blooms)		24–43% total cell counts
(31% cell count increase after 48 h in one sample)		MCs:
3–25% decrease in one sample
37–589% increase in one sample
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Jalili, F.; Moradinejad, S.; Zamyadi, A.; Dorner, S.; Sauvé, S.; Prévost, M. Evidence-Based Framework to Manage Cyanobacteria and Cyanotoxins in Water and Sludge from Drinking Water Treatment Plants. Toxins 2022, 14, 410. https://doi.org/10.3390/toxins14060410

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Jalili F, Moradinejad S, Zamyadi A, Dorner S, Sauvé S, Prévost M. Evidence-Based Framework to Manage Cyanobacteria and Cyanotoxins in Water and Sludge from Drinking Water Treatment Plants. Toxins. 2022; 14(6):410. https://doi.org/10.3390/toxins14060410

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Jalili, Farhad, Saber Moradinejad, Arash Zamyadi, Sarah Dorner, Sébastien Sauvé, and Michèle Prévost. 2022. "Evidence-Based Framework to Manage Cyanobacteria and Cyanotoxins in Water and Sludge from Drinking Water Treatment Plants" Toxins 14, no. 6: 410. https://doi.org/10.3390/toxins14060410

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