Abstract
The interactions between bacteria and microalgae play pivotal roles in resource allocation, biomass accumulation, nutrient recycling, and species succession in aquatic systems, offering ample opportunities to solve several social problems. The escalating threat of harmful algal blooms (HABs) in the aquatic environment and the lack of cheap and eco-friendly algal-biomass processing methods have been among the main problems, demanding efficient and sustainable solutions. In light of this, the application of algicidal bacteria to control HABs and enhance algal biomass processing has been promoted in the past few decades as potentially suitable mechanisms to solve those problems. Hence, this comprehensive review aims to explore the diverse interaction modes between bacteria and microalgae, ranging from synergistic to antagonistic, and presents up-to-date information and in-depth analysis of their potential biotechnological applications, particularly in controlling HABs and enhancing microalgal biomass processing. For instance, several studies revealed that algicidal bacteria can effectively inhibit the growth of Microcystis aeruginosa, a notorious freshwater HAB species, with an antialgal efficiency of 24.87 %–98.8 %. The review begins with an overview of the mechanisms behind algae-bacteria interactions, including the environmental factors influencing these dynamics and their broader implications for aquatic ecosystems. It then provides a detailed analysis of the role of algicidal bacteria in controlling harmful algal blooms, as well as their role in bioflocculation and the pretreatment of microalgal biomass. Additionally, the review identifies and discusses the constraints and challenges in the biotechnological application of these interactions. By exploring the strategic use of algicidal bacteria, this review not only underscores their importance in maintaining aquatic environmental health but also in enhancing biomass processing efficiency. It offers valuable insights into future research avenues and the potential scalability of these applications, both in situ and at an industrial level.
Keywords: Algicidal bacteria, Biological pretreatment, Cell wall, Environmental factors, Flocculation, Harmful algal blooms, Interaction
Graphical abstract
1. Introduction
Microbial communities have an intricate web of interdependencies, primarily driven by the exchange of resources [1]. The interactions range from synergistic exchanges of nutrients and signalling molecules to the release of antagonistic chemicals, and play vital roles in resource partitioning, biomass accumulation, nutrient recycling, and species succession in natural aquatic systems. Microalgae and bacteria are among the major components of microbial communities, sharing an interconnected evolutionary history that accompanied the ability to secret inhibitory biochemicals during scrambling for resources [2]. Moreover, algal surfaces can provide a conducive microhabitat for bacteria, offering abundant nutrients, colonization space, and protection against predation. On the other hand, bacteria can contribute to this symbiosis through distinct physiological characteristics, such as antibiotic production and polysaccharide degradation, thereby establishing mutualistic relationships with their algal counterparts.
The interactions between bacteria and algae are diverse, encompassing both direct and indirect interactions [3]. The direct interactions involve physical contact and sometimes pre-contact chemical signalling, while indirect interactions are mediated by the secretion of substances that influence neighbouring cells. These interactions can either promote or inhibit the growth and physiology of these microorganisms. Until now, numerous secondary metabolites have been identified in aquatic environments that play key roles in mediating the interactions between these microbes [4,5].
The scientific discovery of the intimate microalgae-bacteria interaction is traced back several decades [[6], [7], [8], [9]]. The early research predominantly focused on the adverse effects of bacteria on microalgae and the ecological implications [7,10,11]. This trend persisted into the 1990s, with studies highlighting the negative impact of bacteria on harmful microalgae [[12], [13], [14], [15], [16]]. This discourse paved the way for the use of bacteria strains as a potential tool to control the proliferation of harmful algae. Since the 2000s a growing body of literature has emerged, demonstrating the application of bacteria in mitigating the impact of harmful microalgae [[17], [18], [19], [20], [21], [22], [23], [24]]. Parallelly, the application of algicidal bacteria has emerged as an economical and environmentally sustainable approach in the downstream processing of algal biomass [25].
Although several review papers have been reported since the 1990s on the algicidal bacteria and their interaction with microalgae [2,26] those articles differ in focus areas and depth. Moreover, as most of those review papers emphasized on the specific topics; for example, some focused on strategies and ecological roles of algicidal bacteria [27], information about the application of algicidal bacteria in managing harmful algal blooms (HABs) [28], controlling HABs with microorganisms [29], controlling HABs with biological methods [30] and controlling cyanobacterial impact with algicidal bacteria [31]. However, literature reviews that holistically address the various types of microalgae-bacteria interactions and their application, particularly the role in controlling HABs and enhancing biomass processing have been lacking. Moreover, due to intensified eutrophication and climate change, the threat of HABs to aquatic ecosystems is escalating altering the environmental health. Additionaly, the rapid economic expansion and population growth coupled with the lack of low-cost, accessible and sustainable means of microalgal biomass pretreatment pos prominent challenges in the food and energy production sectors. Hence, more efforts are expected from the scientific investigation to pursue on eco-friendly and viable solutions to these pressing challenges in the environmental health and production sectors.
Thus, this review aimed to present a comprehensive and critical analysis of the environmental and biotechnological application and perspective of algicidal bacteria on microalgae, providing an in-depth and coherent exploration of the various modes of microalga-bacteria interaction, species-specificity of microalgae-bacteria interaction, and the role of algicidal bacteria amenability to control formation of HABs, and processing of microalgal biomass. In this paper, microalgae encompasses both the eukaryotic algae and the prokaryotic photosynthetic bacteria, the blue green algae (cyanobacteria).
2. Algae-bacteria interaction mode, factors influencing the interaction, and the ecological implications
2.1. Microalgae-bacteria mode of interaction
There are different levels of interactions between microalgae and bacteria, such as free-living interactions (Fig. 1a), phycospheric (Fig. 1b), and contact (Fig. 1c), and each has its own set of mechanisms and outcomes [27]. Predominantly, the direct interactions occurred within the phycosphere, whereas in some cases, the bacteria can physically attach to algae, or form close association by which the algae and bacteria interact through diffusible molecules [32]. Many of these interactions involve the trading of specific molecules produced by a participant species which are subsequently metabolized by the other species and establish a complex metabolic network between the species. Generally, algae-bacteria interactions encompass three various patterns, including gene transfer, signal transduction and nutrient exchange, which are influenced by biotic and abiotic environmental factors [33].
Fig. 1.
A diagram illustrating different forms of bacteria and microalgae interaction in an open aquatic environment in a) free-living interaction b) phycospheric interaction with the diffusive boundary created between the outside periphery and phycosphere, where the microalga exuded dissolved organic carbon (DOC), while both partners exchange nutrients (nitrogen-N, phosphorus-P, and carbon dioxide-CO2) with gradient of concentration from the inner part to the periphery, and c) cell-to-cell contact interaction involved in entanglement with bacterial flagella.
Even though the diffusive boundary layer is always changing and chemical flows are complicated in fluid environments that are always changing, algae and bacteria are constantly interacting in the phycosphere [9] (Fig. 1b). The study by Kim et al. [34], supported the concept that in phycosphere the organic matter exuded from the algal cell decreases, creating a gradient going away from the algae where specific bacteria can take advantage of it. This indicates microalgae in the phycosphere have the opportunity to select different types of bacterial species depending on the concentration and type of exudate. Furthermore, the interaction of algae and bacteria in the phycosphere could be enhanced by signal molecules secreted and released by both partners. When these signal molecules are released by bacteria and enter into the microalgal cells, they may bind to specific target molecules, and initiate a response that indicates whether the bacterium was synergetic or algicidal. This signalling mechanism likely confers a fitness and competitive advantage over algae-bacteria interaction which does not have such a signalling mechanism other than traditional chemotactic means of response. Thus, it is likely that the association between certain species of bacteria and algae could be linked to the sense of shared signal [35].
Maintaining physical proximity has a significant impact on enhancing metabolite exchange between microorganisms as nutrients are scarce in open-ocean environments [34], hence microbes may prefer closer association. This leads to the formation of microscale patches of concentrated microbes throughout oceanic environments [35]. Some algae can engage in close associations with bacteria, which can be characterized by algicidal or bacterioprotective effects [36]. This interaction could involve the expression of several genes, as the transcriptome and metabolic analysis of the diatom Thalassiosira pseudonana and heterotrophic bacterium Ruegeria pomeroyi revealed the presence of the bacterium-induced recognition cascade by the diatom and triggered differential expression of over 80 genes [32]. Such interactions underscore the complexity and specificity of the relationship between microalgae and bacteria, emphasizing the dynamic nature of these ecological relationships.
The interaction between algae and bacteria is facilitated by a range of metabolomic products, including stimulators, potential toxin inducers, cyst inducers, growth inhibitors, algicides and chemosensors [37]. These biochemical exchanges have driven the evolution of diverse symbiotic relationships between these groups, which led to various forms of symbiosis that range from mutualism and competition to parasitism and predation [38,39] (Table 1).
Table 1.
The negative and positive interaction modes between bacteria and microalgae.
| Mode of interaction | Actions | References | |
|---|---|---|---|
| Mutualism | Exchange of material between bacteria and microalgae | Vitamins | [1,40] |
| Iron siderophores | [41] | ||
| Vitamins, growth-promoting factors and DOC | [42,43] [37,44,45] | ||
| Indole-3-acetic acid (IAA) | [[46], [47], [48]] | ||
| Nitrogen | [49,50] | ||
| Competition | Scrambling for resources | Nitrate and DOC | [51] |
| Nitrogen | [52] | ||
| Predation and parasitism | Inhibiting algal activity | Releasing of lytic enzymes | [[53], [54], [55], [56]] |
Typically, algae-bacteria interactions can constitute the exchange of materials as resource or signal molecule for communication purpose [57] (Fig. 2). The signal molecules can activate or inhibit the expression of genes or biological activities, which could result changes in the metabolism of cells and growth. For instance, the Sulfitobacter species promotes the cell division of diatom by releasing indole-3-acetic acid (IAA). The molecules like tryptophan, IAA, diatom-excreted organosulfur molecules and bacterial excreted-ammonium served as signalling molecules. Moreover, bacteria can apply quorum sensing to communicate with each other or with microalgae and influence the growth and physiology [58]. Likewise, microalgae can secrete a certain signal substance (quorum quenching) that inactivate the signal substance of bacterial quorum sensing [59]. This results in disrupted communication between the cells of algicidal bacteria and avoids their deleterious effects (Table 1 and Fig. 2).
Fig. 2.
A diagram illustrating the free exchange of resources, the negative and the positive interactions between microalgae and bacteria facilitated through the free exchange of nutrients or signal molecules and quorum sensing. Where, the dissolved organic matter (DOM), the cell degrading product (CDP), tryptophan and thamin originated from the microalgae and then assimilated and act on bacteria, while indole acetic acid (IAA), vitamins, siderophores, acetate, lytic enzymes originated from bacteria then acted on microalgae, and the quorum sensing can be applied within bacteria or between bacteria and microalgae facilitating the interactions. The illustration depicted is based on [27,60].
The mutualistic interaction between algae and bacteria involves the exchange of resources that facilitate a synergistic relationship [61] (Table 1). Several members of bacteria live closely with phytoplankton for organic carbon, while potentially competing for other essential nutrients [51]. The nature of relationship between algae and bacteria can be competitive or mutualistic and varies according to the ecophysiological condition of the participant microbes (Table 1). In line with that, a transition from mutualistic interactions to pathogenic behaviour has been reported in response to changes in algal growth conditions [62].
The interactions between algae and bacteria can also be antagonistic or harmful, leading to the demise of one or both participants. This is often evident in microbial parasitism, where parasitic bacteria may reside on the surface of the host, penetrate host cells [63,64], or rely on extracellular lytic factors for pathogenesis [[53], [54], [55], [56]]. Hence, the toxicity of bacteria on eukaryotic algae can occur through the secretion of toxic molecules [65] or via an intracellular life cycle within the host cells [66].
Moreover, microalgae secrete organic molecules that act as a defence mechanism to deter the attachment of unwanted or algicidal bacteria. In addition to the production of antibacterial molecules, algae employ various strategies for defence, including the production of antibacterial molecules and the manipulation of bacterial signalling (Fig. 2). The manipulation can involve mimicking [67,68], modifying [35] or inactivating [59] the signal molecules that enables the algicidal bacteria to communicate with each other and produce the algicidal molecules within the phycosphere or environment. The molecules secreted by microalgae can interfere with the communication pathways among cells of algicidal bacteria, which can effectively mitigate the detrimental effects. Another mechanism for microalgae to defend themselves is harboring bacteria that are capable of antagonizing harmful bacteria species [69].
2.2. Factors affecting interaction modes between microalgae and bacteria
Environmental factors, such as, temperature, and nutrient type and availability, significantly influence the association between algae and bacteria. As nutrient exchange is a fundamental driver of algae-bacteria interaction, environmental factors that alter the nutrient exchange equilibrium would likely affect the mode of interaction. For instance, from the abiotic environmental component, the nature of inorganic nitrogen sources (e.g., nitrate, ammonium, or a combination) can impact the quantity of extracellular organic compounds released by algae, which in turn, affects the mutualistic interactions between the bacteria and algae [70]. In line with this, Cao et al. [71] demonstrated that an excess of phosphorus and optimal nitrogen:phosphorus ratio fosters mutualistic interactions, as bacteria benefit from the dissolved organic carbon from algae. Conversely, an excess of carbon shifts the relationship towards competition, with bacteria up taking nutrients and thereby inhibiting algal growth.
A study on Phaeocystis globosa and its microbiomes revealed that the microbiome allowed the culture to grow when B-vitamins were withheld, but the collapse of the culture accelerated when nitrogen was withheld, indicating the shift in nutrient balance would likely result in switching off the interaction mode. Moreover, the production of signal molecules such as tryptophan and IAA was detected when the co-culture of the green alga Chlorella sorokiniana and the bacterium Azospirillum brasilense was provided with a nitrogen-rich medium, however, the production of these molecules was undetected when the culture was provided with nitrogen or carbon-free media [72]. Iron limitation was also found to trigger the production of bioactive peptides and glycosides in Chlorella, inhibiting infection by the pathogen Vampirovibrio chelorellavorus [73]. In addition to nutrients, temperature is another critical factor that affects bacterial behaviour and community composition. For instance, a bacterium from the genus Ruegeria (Rhodobacteriaceae) exhibited opportunistic pathogenicity towards the coccolithophore Emiliania huxleyi at 25 °C, but did not affect the growth at 18 °C [74].
The other factor that determines the interaction mode is the cue that the bacteria receive from the microalgae (Fig. 2). A notable example is Phaeobacter gallaeciensis (Roseobacter clade of alphaproteobacterial) initially mutually interacts by promoting the growth of coccolithophore Emiliania huxleyi through synthesizing and secreting broad-spectrum antibiotics and growth stimulant phytohormones, which suppress the growth of parasitic bacteria and promote algal growth, respectively. The bacterium in return receives nutrients including organic carbon and surface area to colonize the microalga. However, this mutualistic symbiosis shifts when p-coumaric acid (algal lignin breakdown product and indicator of algal aging) is released from E. huxleyi, inducing P. gallaeciensis to produce potent and selective algaecides (roseobacticides) which transforms the mutualistic interaction into an opportunistic pathogen [62]. Similarly, Segev et al. [75] showed the roseobacter Phaeobacter inhibens transitioned from promoting the growth of E. huxleyi to a pathogen killing the host alga. Recently, an investigation on the interaction of E. huxleyi and the bacterium Sulfitobacter sp. showed dimethylsulfoniopionate (DMSP) released by the alga played a pivotal role in switching the lifestyle of Sulfitobacter, however, the alga also produces benzoate which negates the DMSP-induced pathogenetic lifestyle and allows co-exitance of the alga and bacterium [76].
2.3. The species-specificity in algae-bacteria interaction
The concept of species-specific interaction between algae and bacteria has been a subject of debate for several years, with various studies providing evidence for and against this notion. Sison-Mangus et al. [77] posited the existence of specific associations between particular algae and bacterial species. In contrast, Meyer et al. (2017) argued for more random associations, a stance supported by the strong influence of environmental factors on the bacterial community of the diatom Leptocylindrus sp. [78], noticeable shifts in bacterial communities over cultivation time [[79], [80], [81]], the development of distinct bacterial communities in different laboratory cultures of Pseudo-nitzschia multiseries [82], and the growth enhancement effect of random bacteria (Escherichia coli laboratory strains) on diatoms [83].
A complex mode of interaction of bacteria with the marine green alga Tetraselmis suecica were fluctuated across different growth phases [84], suggesting coadaptation and co-evolution may not be prerequisites for effective algae-bacteria interactions [85]. Stock et al. (2022) also observed that microbiomes associated with diatom are heavily influenced by environmental factors, often in a random manner. However, they noted that host microhabitat selective filtering constrain the phylogenetic and functional assembly of these microbiomes. Corroborating these, Grossart et al. [86] observed the appearance and disappearance of certain bacterial species during algal growth, indicating the pronounced differences in environmental conditions could exert selection pressure on bacteria are highly adaptable to the changing environment.
Despite the availability of reports to support the above claim, there is a consistent presence and association of specific bacterial species with a particular algal species, both in culture and natural environmental conditions (Table 2). In addition, bacterial production frequently appeared to be correlated with phytoplankton biomass population in marine environments [87]. Moreover, the study by Kerkhof et al. [88], presented an indication that the composition of the bacterial community is influenced by the algal species composition. This implies that the two groups have adapted to coexist, benefiting from each other's presence. For example, diatoms release organic-rich compounds that seem to nourish the phycosphere, this may entail the release of signal molecules by diatoms which can be perceived by specific bacteria. Then, those bacteria able to perceive the diatom signals form a consistent associations and engagement of a specific interaction with the diatom.
Table 2.
Studies indicating the presence of a species-specific association between bacterial community and phytoplankton species and the type of experimental conditions.
| Experimental conditions | Key findings | References |
|---|---|---|
| In natural environment | Bloom of Lingulodinium polyedrum (dinoflagellates) accompanied by shift in bacterial community and enzyme activity. | [89] |
| There was a shift in bacterial diversity depending on whether toxin-producing Pseudo-nitzschia (diatom) species was dominated the algal bloom. | [90] | |
| Algal toxins can modify the structure of the bacterial community, although other factors such as algal biomass and nutrient concentrations can also contribute to the changes. | [91] | |
| Phytoplankton bloom and other related environmental variables influenced the composition of the bacterial community. | [92] | |
| Unique bacteria assemblage observed with blooms of Cochlodinium (Margalefidinium) polykrikoides (dinoflagellate). | [93] | |
| Unique bacteria assemblage observed with blooms of cosmopolitan diatom species Thalassiosira and Chaetoceros. | [94] | |
| In microcosm experiment | Two phylotypes affiliated with Cryomorpahceae and Flavobacteriaceae of Bacteroidetes largely appeared in a microcosm dominated by phytoflagellates, and other two phylotypes (together with Alphaproteobacteria (Roseobacter) and Gammaproteobacteria (Methylophaga)) affiliated with Flavobacteriaceae were characteristically found in diatom-dominated microcosm. | [87] |
| In mesocosm experiment | The dominance of the diatom species Thalassiosira coincided with decreased bacterial abundance and shift in bacterial community composition. | [80] |
| There could be species-specific responses of phytoplankton to bacteria signal molecules. | [95] | |
| In laboratory experiments | The extracellular polymeric substance (EPS) of the bacterium Variovorax paradoxus promoted the growth of the green microalgae Tetradesmus obliquus and Coelastrella sp., and the EPS collected from T. obliquus promoted the growth of the bacterium V. paradoxus but the EPS collected from Coelastrella sp. did not promote the growth of the bacterium. | [96] |
| The flavobacterium K. algicida releases a protease with a mass of >30 kDa that acts against a subset of diatoms (Skeletonema, Thalassiosira, and Phaeodactylum) but not Chaetoceros. | [97] | |
| S. costatum is susceptible to the lysis of K. algicida while Chaetoceros didymus was resistant. | [98] | |
| There was deterministic type of association between P. globosa and the bacterial assemblage, with species-specific and beneficial interactions. | [99] | |
| Bacterial transplant experiments showed the bacteria are mutualistic to their native hosts but they become commensal or parasitic when they are introduced into foreign hosts. | [77] | |
| 6 strains of marine diatoms exhibited lower complexity of satellite bacterial assemblages compared to bacterial assemblages in the natural environment, and each algal culture characterized by a distinct satellite assemblage. | [100] | |
| The bacterial genera Marinobacter and Bolneola dominated in the dinoflagellate Prorocentrum donghaiense (non-toxic) and Karenia mikimotoi (toxic), respectively, whereas the genera Loktanella and Roseivirga, and Alteromonas, Methylophaga and Thalassospira specifically present in P. donghaiense and K. mikimotoi according to their respective order. | [101] | |
| Non-axenic cultures of phytoplankton harbour bacterial communities where S. costatum (diatom), P. tricornutum (diatom) and Dunaliella bardawil (green alga) were dominated by Marivita (∼80 %), Dinorseobacter (∼47 %) and Halomonas (∼87 %), respectively. | [102] | |
| Isolates of the dinoflagellate karlodinium veneficum constituted persistently similar bacterial assemblage regardless of the various geographic locations the microalgae isolated. | [103] |
The marine phytoplankton communities are generally dominated by bacterial communities of Flavobacteriales, Rhodobacterales, and families within the Gammaproteobacteria [104] (Table 2). To sustain together, the relationships should remain either mutually beneficial or unilaterally beneficial, which supports long-term and stable coexistence Deng et al. [105]. Furthermore, two heterotrophic bacterial phyla, Proteobacteria and Bacteroidetes, appear to be consistently observed with diatoms and these bacteria are generally confined to a small number of genera (conserved bacterial associations with diatoms) [35]. Research on the bacterial communities of four strains of Asterionellopsis gracialis (diatom) and three strains of Nitzschia longissima (diatom) indicated each diatom species harbour a unique bacterial community while bacterial composition from the same species is highly conserved at the genus level [106]. A study on bacterial communities associated with cyanobacteria cultures indicated that the bacterial communities were different in different cyanobacteria, however, the similarity values of the cluster analysis among the same species of cyanobacterium were higher than those of the other cyanobacteria cultures, showing evidence for species-specific associations [107]. Additionally, more similarities between the attached bacterial communities of Thalassiosira rotula (diatom) and Akashiwo sanguinea (dinoflagellates) were observed compared to four other species of diatoms and dinoflagellates, supporting the idea of species-specific association between algae and bacteria [79].
An experiment performed on Alexandrium cultures indicated that there was no significant difference in the microbial community even though the strains of Alexandrium exhibit intraspecific differences according to the geographic location they were isolated, indicating consistent species-specific interaction could occur between the bacteria and the Alexandrium, disregarding the phenotypic variations of the individual [108]. Likewise, higher bacterial species resemblance in different Alexandrium cultures (which were originally isolated from different geographic areas) than the bacterial community of different phytoplankton groups isolated from the same location was observed, indicating the presence of bacterium-phytoplankton specificity [109].
Abate et al. [102] provided exogenous ethanol to the non-axenic culture of three microalgae isolates to investigate the satellite bacterial community response. Their result indicated that, although some bacterial species increased their abundance, generally the bacterial community structure remained unchanged. In addition to that, the same report showed three microalgae species constituted distinct satellite bacterial communities, indicating there was a specific bacterial community association with different microalgae species. Likewise, Sapp et al. [79] stated that microalgae harbour specific bacterial communities. Additionally, a highly specific interaction between Cylindrotheca strains and their associated bacterial strains was also observed [85].
Several research studies indicated that the interaction between microalgae and bacteria does not strictly maintain species-specificity; however, there is also evidence showing the consistent co-existence of certain types of bacteria with specific groups, which could be considered an indication for species-specific association between the two groups [110]. Thus, the species-specificity association should be treated as a particular taxon not as the whole group as bacteria or microalgae, acknowledging the complexity of these interactions.
There might be various reasons for the association of specific bacteria with specific groups of algae; one of the reasons for such interaction could be nutritional preferences. For example, the association between algae and Bacteroidetes, is attributed to the bacteria's prevalence in nutrient-rich environments characterized by an abundance of biomacromolecules or substantial organic molecule concentrations [111]. Moreover, metagenomic and metaproteomic analyses have further elucidated these associations [112].
The study on Synechococcus and its associated bacteria revealed distinct metabolic roles of Flavobacteria members preferentially degrade complex organic compounds and biopolymers in early culturing stages, while the alphaproteobacteria member Oricola sp. dominates later stages by utilizing low-molecular-weight dissolved carbon [112]. On the other hand, synthetic phycosphere systems demonstrated that the composition of bacterial communities can be predicted based on the phytoplankton taxa and their metabolite exudates, which indicates that resource availability is a key factor in bacterial community assembly [113]. This suggests that phytoplankton can shape bacterial associations by releasing specific metabolites, potentially recruiting microbiomes that are beneficial to their growth [113].
The other explanation, in addition to the nutritional habit of the bacteria, for the occurrence of group-specific association, is the mutual benefit of the two groups could maintain the association. For instance, the co-occurrence of methylamines and methylotrophic bacteria together with heterotrophic bacteria and diatoms was investigated, and the result showed the bacteria Methylophaga sp. and Donghicola sp. involved in the supply of nitrogen source to the diatom P. tricornutum (which could potentially provide the DOC needed by the bacteria) through degradation of methylamine [114]. In addition, the Roseobacter clade of alphaproteobacteria is known to be the most abundant group associated with marine microalgal culture and phytoplankton blooms, suggesting there might be a close association between the members of this group and phytoplankton. Corroborate, positive chemotaxis towards dinoflagellates exudate (both DMSP and amino acids) exhibited by members of Roseobacter, and the close association between Roseobacter (that can degrade DMSP) and algae indicates there is unilateral or bilateral benefit from the association.
Moreover, direct interaction between Roseobacter and algae has been deduced from the observation that some Roseobacter members attach to the surface of dinoflagellates species. The mutual benefit of these bacteria and phytoplankton arises from the fact that the members of these bacteria are aerobic anoxygenic phototrophs, and may obtain light and nutrients by epibiosis with phytoplankton and in return, they may provide antibiotics and growth stimulants to phytoplankton. Furthermore, the requirement of certain bacterial groups (Marinobacter sp. and Brachybacterium sp.) for growth-promoting factors have been exhibited by the dinoflagellate G. catenatum [115].
2.4. The role of algicidal bacteria in natural environments
Algicidal bacteria are those bacteria capable of inhibiting or lysing the algal cells, and they are distributed in seas, lakes and land environments [116]. Some algicidal bacteria significantly influence the growth of microalgae determining the initiation and demise of algal blooms. Several studies performed both laboratory and field research have explored the influence of algicidal bacteria and their metabolites on phytoplankton biomass production and species composition. One notable study by Fukami et al. [117], investigated the bacterial impact on the growth and composition of algal species during the bloom of the dinoflagellate Gymnodinium nagasakiense. This research revealed that bacteria in the natural community initially stimulated the growth of G. nagasakiense and the diatom Skeletonema costatum. However, as the G. nagasakiense bloom approached its peak, the stimulative effect of bacterial community on the diatom diminished and eventually became inhibitory to both algal species during the decline of the G. nagasakiense bloom. These findings highlighted the critical role of bacterial communities in dictating the succession, development and decay of algal blooms.
In another study, Bigalke et al. [118] examined the effects of algicidal bacteria (K. algicida) on a natural plankton community within an indoor enclosure. The introduction of these pathogenic bacteria induced a cascade of changes in the phytoplankton succession. Specifically, the algicidal bacteria precipitated a rapid decline in the bloom-forming diatom species Chaetoceros socialis, which was susceptible to bacterial lysis. Conversely, the haptophyte Phaeocystis, resistant to the lytic bacteria, exploited the removal of its competitors and subsequently bloomed. This experiment demonstrated the potential of algicidal bacteria to shift the entire plankton population dynamics, where resistant species rapidly capitalize on the resources freed by the demise of susceptible species.
Further studies in freshwater environments have identified a correlation between algicidal bacteria and bloom-forming cyanobacteria species. These organisms coexist in a state of equilibrium until environmental changes favour the bacteria, prompting them to lyse the algae [10]. Additionally, the application of bacterial quorum sensing signals (Alkylquinolone) in phytoplankton cultures has been shown to induce prolonged S-phase arrests and accumulated DNA damage, which implies a significant role in bacterial signalling in microbial community dynamics [58].
The investigation of microbial dynamics in Hiroshima Bay (Japan) indicated that a population of algicidal bacteria forms a close relationship with phytoplankton blooms, which might influence the species structure of the system by affecting a specific group of species [119]. Moreover, the presence of growth-inhibiting-bacteria on the surface of seagrass along the Akkeshi-ko Estuary and Akkeshi Bay (Japan) inhibited the growth of toxic dinoflagellate Alexandrium catenella resulting in the elimination of A. catenella from the estuary and coastal area waters, while the A. catenella cells frequently observed in the offshore areas [120].
3. The emerging role of bacteria in HAB management
Algal bloom is the excessive growth of algae. Although algal blooms are often beneficial or harmless, they have been considered as an indicator of ecosystem disruption, eutrophication, or altered environmental states [121,122]. Some algal blooms can harm the environment, aquatic life, public health and socio-economics of human life [123,124]. Hence, the excessive growth of harmful algae or those that cause negative impact is referred to as harmful algal blooms. The impact of HABs on socioeconomic activities has markedly increased in recent years, likely linked to global climate change and rapidly increasing anthropogenic pressure on water bodies [110].
As the alarming explosion of HABs threatens the well-being of the ecosystem and human health, several methods, including physical and chemical methods have been developed to mitigate the HABs impact. However, these traditional methods come with some limitations, especially related to their side effects on the environment, higher operational cost and non-species-specific effects [125].
The physical methods include filtration, salvage, flotation, sonication, ultraviolet radiation, laser-irradiation, gamma-ray irradiation, and flocculation using clay, soil and sediment modified by chitosan and solar-driven TiO2 photocatalysis, the chemical methods include ozone, chlorine dioxide, hydrogen peroxide, potassium ferrate and copper sulfate, and the biological methods including macrophytes, filter-feeding bivalves, zooplankton and fish have been reported as feasible mechanisms to mitigate the HABs events [126 and the references there in]. However, as most of these physical (potential risk to other aquatic organisms and high cost), chemical (environmental safety concern) and biological (difficulties to implement in a large natural water bodies) methods have some drawbacks, other biological methods such as using heterotrophic bacteria have been reported as an alternative means to curb the impact of HABs [127,128].
As microalgae and bacteria are known to entimatelly interact dictating the physiology and growth of each other [95], bacteria that inhibit or cause mortality of phytoplankton have been a point of interest in controlling the proliferation of harmful algae. So far, several algicidal substances produced by bacteria that have potential value in controlling the formation of HABs have been reported, including prodigiosin [129], serin protease [130], questiomycins [131] and isatin [132], biosurfactant agent sophorolipid [133] and hydroxylamine [134].
3.1. The HAB forming species and the effect of algicidal bacteria on them
The formation of HABs has been reported in members of various algal groups including dinoflagellates, prymnesiophytes, diatoms, raphidophytes, pelagophytes, and cyanophytes. Some of the HAB members are well known for recurrently forming harmful blooms in marine and coastal waters (dinoflagellates) [135], whereas the others predominantly occur in freshwaters (cyanobacteria) [136]. In addition to the ecological variation in the distribution of HAB-forming species at the group level, the distribution of toxigenic species within one group could be varied; where some groups (dinoflagellates) can have toxigenic species in every clade, whereas some groups (prymnesiophytes) have toxigenic species in one clade, mainly in the family Prymnesiaceae [137].
Many members of dinoflagellates are known to produce toxins and form HABs. The toxigenic species of dinoflagellates are distributed in several genera of four different major clades [137]. In light of this, several papers have reported the algicidal effect of bacteria on different HABs forming species of dinoflagellates including P. donghaiense, A. tamarense, Heterocapsa circularisquama, Pfiesteria piscicida, Gyrodinium uncatenum and Prorocentrum minimum (Table 3).
Table 3.
Bacterial species exhibiting algicidal activity against harmful algal bloom (HAB) species.
| Algal class (eukaryotic and prokaryotic) | Algae species | Bacterial species | References |
|---|---|---|---|
| Dinoflagellate | P. donghaiense | Paracoccus sp. | [138] |
| Sulfitobacter porphyrae, | [23] | ||
| Alteromonas sp. | [22] | ||
| A. tamarense | Bervibacterium sp. | [[139], [140], [141]] | |
| Vibrio sp. | [142] | ||
| Mangrovimonas yunxiaonensis | [143] | ||
| Heterocapsa circularisquama | EHK-1 | [144] | |
| Pfiesteria piscicida, Gyrodinium uncatenum and Prorocentrum minimum | Shewanella sp. | [145]. | |
| Haptophytes | P. globosa. | Hahella spp. | [146,147] |
| Microbulbifer sp. | [148] | ||
| Streptomyces alboflavus, Streptomyces malaysiensis | [149,150] | ||
| Raphidophytes | G. catenatum, Chattonella marina and Heterosigma akashiwo | Pseudoalteromonas sp. and Gammaproteobacterium (MS-02-063) | [16] |
| H. akashiwo | Hahella sp. | [151] | |
| Bacillariophytes | Skeletonema costatum | Pseudoalteromonas sp. | [152] |
| Halobacillus sp. | [153] | ||
| Alteromonas sp. | [154] | ||
| Streptomyces somaliensis | [155] | ||
| Cyanobacteria | Microcystis aeruginosa | Stenotrophomonas sp. | [156] |
| Raoultella planticola and Aeromonas sp. | [157] | ||
| Exiguobacterium sp. | [158] | ||
| Enterobacter hormaechei | [128] | ||
| Acinetobacter sp. | [159] | ||
| Bacillus lichenformis | [160] | ||
| Aeromonas | [161] | ||
| Aphanizomenon flos-aquae | Pseudomonas mendocina | [162] | |
| Microcystis wesenbergii and Phormidium | Bacillus lichenformis | [160] | |
| Microcystis flos-aquae, Anabaena cylindrica, A. flos-aquae and Nodularia spumigena | Aeromonas | [161] | |
| A. flos-aquae | Bacillus thuringiensis | [163] | |
| Synechococcus sp. | Stenotrophomonas sp. | [156] | |
| Enterobacter sp. | Oscillatoria | [164] | |
| Alcaligenes aquatilis | Lyngbya aestuarii | [165] | |
| Microcystis aeruginosa and Aphanizomenon gracile | Morganella morganii | [166] |
Haptophytes are members of marine phytoplankton that play an important role in biogeochemical cycles. Their cells are known for possessing two smooth flagella and an inserted organelle (haptonema) between the flagella. Few planktonic species are known to form harmful blooms in this group. The members of the genera Phaeocystis form blooms that can produce copious foam and toxins, whereas Prymnesium and Chrysochromulina are linked with ichthyotoxicity in coastal marine, and freshwater systems [137]. Particularly, P. globosa is one of the most notorious HABs-forming species that can secrete hemolytic toxins. Given its substantial ecological impacts, extensive research has been dedicated to understand the P. globosa's toxic mechanisms and finding ways to mitigate its adverse effects.
Heterokonts are another major eukaryotic algae known for their two unequal flagella, and they include several classes of algae. In this group, there are two major classes of phytoplankton, including Raphidophyceae and Bacillariophyceae, both known for harbouring many toxic species. Within Raphidophyceae, certain strains from genera such as Chattonella and Heterosigma are notorious for forming HABs in estuaries and coastal marine systems, while Gonyostomum species are known for freshwater blooms that can be lethal to fish. However, reports on the algicidal activity of bacteria against these Raphidophyceae species are limited, as summarized in Table 3. Among the Bacillariophyta the genera Skeletonema and Chaetoceros and the toxin-producing species of Pseudo-nitzschia are noticeable. Specifically, Chaetoceros spp. has been documented to harm fish through their long spines that can clog gills, leading to death by physical obstruction [137]. While a substantial amount of research, including [[167], [168], [169]], documented the algicidal activity of certain bacterial strains against diatom species, there remains a gap in understanding this activity specifically against HABs-causing diatom species.
Cyanobacteria represent a highly diverse group of prokaryotes notorious for forming harmful algal blooms (CyanoHABs) in freshwater, which produce toxins detrimental to aquatic life and contaminate the water, rendering it unfit for use. For the past 50 years, the activity of various algicidal bacteria has been explored as an alternative method to mitigate the impact of HABs. Some of the significant findings from extensive research were summarized in Table 3, which focuses on the effectiveness of these bacteria against a range of cyanobacterial species, including Microcystis aeruginosa, Aphanizomenon flos-aquae, Microcystis wesenbergii, Phormidium sp., flos-aquae, Anabaena cylindrica, Nodularia spumigena and Synechococcus sp. For instance, several studies indicated that the growth inhibitory efficiency of algicidal bacteria on M. aeruginosa ranged from 24.87 % to 98.8 % [170].
3.2. Mechanisms by which algicidal bacteria attack the microalgae
The mechanistic process of algicidal activity on algae has been reported by describing its effect on the morphology and physiology of the target organisms. To understand the morphological and physiological alterations, the physical attachment and entanglement, integrity of the cell wall and organelle structures can be detected by microscopic observations, the activity of reactive oxygen species and oxidative stress indicators can be analysed by fluorescence assay, the photosynthetic structure and function can be analysed by measuring chlorophyll concentration and fluorescence techniques, and gene expression and metabolism can be detected by transcriptome and proteomics analyses. Generally, there are two main mechanisms by which algicidal bacteria can attack the algae: 1) directly invading the algal cells, and 2) indirectly killing or inhibiting the growth of the algae via secreting extracellular active metabolites or competing for resources (Fig. 3 and Table 4). Approximately 70 % of the algicidal bacteria act indirectly, while 30 % are suggested to act directly, and algicidal bacteria exhibiting both mechanisms are rarely identified [171]. As a first report of algicidal bacteria, Shilo [7] discovered that a bacteria resembling Myxobacter inhibited the growth of several filamentous blue-green algae by lysing the algae cell wall when there was close contact with the polar tip of the bacteria. Furthermore, four freshwater bacterial isolates that resembled myxobacterales caused lysis to several species of blue-green algae when they grew with vegetative cells of the algae, but bacteria-free filtrate was not sufficient to lyse the cells, and heterocysts were not susceptible to the lysis at all [8]. Some algicidal bacteria directly attach to the algal cell and lyse them, as observed in the marine bacterium Saprospira sp. lyses the cells of Chaetoceros ceratosporum (diatom) by direct contact. The bacterium glid to the diatom, causing the diatom cells to aggregate and undergo lysis by producing microtubule-like structures [169].
Fig. 3.
An illustration depicting a) the direct and indirect attack with an exemplary predatory lifestyle of Vampirovibrio chlorellavorus where sections indicating the bacterium locating the prey-the bacterium seeks out the host (C. vulgaris) cells via chemotaxis and flagella (i), attachment and formation of secretion apparatus (ii), ingestion-hydrolytic enzymes are transferred to the prey cells where they degrade algal cell contents (iii), binary division-algal cell exudates are ingested by V. chlorellavorus allowing it to replicate by binary division, and releasing of progeny (iv), the illustration depicted based on Soo et al. [172], b) the direct and indirect attack of bacteria on microalgae, and c) indirect attack of bacteria by secretion of hydrolytic enzymes.
Table 4.
Some references indicating the indirect and direct mode of attack and the mechanisms of algicidal effects.
| Bacterial strain | Target algal species | Mode of action and mechanisms | References |
|---|---|---|---|
| Alcaligenes denitrificans | M. aeruginosa | Direct attack: algal cell lysis | [173] |
| Bacillus sp. and Brevibacillus sp. | Microcystis aeruginosa | Indirect attack: Damages to the photosynthesis system, morphological injury of algal cells, oxidative stress, and dysfunction of the DNA repair system |
[174] |
| Pseudomonas putida | Microcystis aeruginosa | Indirect attack: Inhibition of photosynthetic apparatus synthesis |
[175] |
| Streptomyces jiujiangensis | M. aeruginosa | Indirect attack: Damage vegetative cells, crumpling, perforation, breakage of filamentous and, increase reactive oxygen species (ROS) and decrease chlorophyll |
[176] |
| Sulfitobacter porphyrae | Prorocentrum donghaiense | Indirect attack: Destroying algal cell membrane and causing intracellular leakage, decline of chlorophyll a content, photosynthetic efficiency (Fv/Fm) and the electron transport rate (rETR), and increased of ROS production |
[23] |
| Vibrio alginolyticus | Chaetomorpha valida | Indirect attack: Morphological damage, dispersion of intracellular pigments, decrease in chlorophyll-a content and Fv/Fm, downregulation of genes related to photosynthesis, increased ROS and downregulation of peroxisomes |
[177] |
The non-photosynthetic cyanobacterial strains such as Bdellovibrio species are known for their predatory behaviour, causing the clumping, decoloration, refractile bodies and finally the death of algal cells [172]. The Vampirovibrio chlorellavorus is a well-known epibiotic pathogen that infects Chlorella sp., attaches to algae, forming peripheral vacuoles and gradually dissolving the cell contents [172,178]. The genomic analysis of V. chlorellavorus revealed it has several genes attributing to its predatory life style. These attributes include genes for signal transduction pathway coupled with functional flagella and extension of pili for movement towards chemoattractants or away from chemorepellents, and genes for proteases and carbohydrate-active enzymes that involve in solubilization and ingestion of algal cytoplasmic contents [172]. The predatory life-style of the V. chlorellavorus is depicted in Fig. 3a.
The bacterium Paucibacter sp. degrades M. aeruginosa mediated by both direct (physical attachment) and indirect (secretion of metabolites) attacks, whereby both washed bacterial cells and cell-free culture supernatant can kill the algal cells, causing oxidative stress, altering the photosynthetic system, fatty acids, carbohydrate, and protein metabolism [179]. Moreover, the authors showed that most genes responsible for antioxidant activity, microcystin synthesis, photosynthesis, and other metabolic pathways in M. aeruginosa were downregulated. The bacterium Sagittula stellata showed algicidal activity against Nannochloropsis oceanica by the direct attack (or predation) preceded by indirect attack via the secretion of extracellular algicidal metabolites, accompanied by loss of organelle integrity, inhibition of transcription of the ribulose-1,5-bisphosphate carboxylase/oxygenase small subunit and proliferating cell nuclear antigen–related genes and promoted transcription of heat shock protein gene [180]. Meanwhile, microscopic and chemotactic analysis indicated that the bacterium Labrenzia sp. moveed towards algal cells (P. tricornutum cells) for direct contact and preceded cell lysis [167] (Fig. 3b).
A study on the effect of chitinase-producing algicidal bacteria (as diatoms are encased in a special cell wall called frustule, a box-like structure made of silica that is further shelled and interjoined with chitin; they are susceptible to chitinase enzyme) on the diatom T. pseudonana, showed that the bacteria move chemotactically and fasten themselves on the alga cells with their flagella, then degrade the algal cell wall by chitinase, followed by algal cell lysis and death [168] (Fig. 3b).
In the other case, algicidal activity can be effective only through indirect contact, whereby metabolites can attack algal cells and cause growth inhibition and death [141,142] (Fig. 3c). During the attack, the algicidal agent could degrade the cell wall and membranes resulting in leakage of cytoplasmic content and ultimate death of the algal cell or it can attack the cellular structure and organelle function in the cytoplasm and consequent death. For instance, the extract (which is non-protein, and heat and pH resistant) of the bacterium M. yunxiaonensis showed algicidal activity on the dinoflagellate A. tamarense by destroying the cell membrane and nuclear structure, then killed the cells [143]. Whereas the hydrophobic compound ((2-isobutoxyphely)amine) extracted from the marine actinomycete bacterium (strain BS01) exerted algicidal activity on A. tamarense by degrading the cytoplasm content including nuclear structure, which resulted in loss of organelle integrity and death, this reflected in loss of mobility and sinking of cells to the bottom of the experimental-flask while external morphology of the cells remained intact [139]. The extracellular active compound (which is sensitive to temperatures above 50 °C and pH beyond 3 to 11) produced by the algicidal bacterium (Streptomyces alboflavus) inhibited the movement of P. globosa by causing flagellar falloff, and death of algal cells [150]. The protease extracellularly released by flavobacterium K. algicida acts against specific diatom genera including, Skeletonema, Thalassiosira and Phaeodactylum [97].
Regarding the impact of algicidal agents on algal physiology, several studies reported algicidal activity disrupted the normal physiology of the algae. The treatment of A. tamarense with algicidal bacterium Deinococcus sp. resulted in decreased content of total protein and antioxidant enzymes, which coincided with overproduction of ROS, loss of cell membrane integrity and lipid peroxidation, a decrease of photosynthetic efficiency, down-regulation of photosynthetic-related gene expression, destruction of nuclear structure and inhibition of proliferating cell nuclear antigen related gene expression [127]. The physiological and biochemical effects of algicidal bacteria Vibrio sp. [142] and Brevibacterium sp. [141] on A. tamarense were investigated by exposing the algal cells to the supernatant of each bacterium. The analysis after treating algal cells with bacterial supernatant showed an increase in ROS activity, suggesting oxidative damage to the cells. Additionally, there was a decrease in cellular pigment concentration, maximum photochemical quantum yield (Fv/Fm), and relative electron transport rates, all indicative of damage to the photosynthetic apparatus and system.
The supernatant of Paracoccus sp. extract can lyse P. donghaiense cells by disrupting their structure, indicated by an overproduction of malondialdehyde (a sign of lipid peroxidation and membrane damage), breaking the cell at the megacytic zone, and impairing photosynthetic efficiency and electron transport, along with the loss of photosynthetic pigments [138]. Fuxing et al. [23] also found that Sulfitobacter porphyrae secretes an extracellular compound, resistant to heat and temperature changes, that damages the cell membrane of P. donghaiense. This leads to intracellular leakage, increased ROS production (suggesting oxidative damage), and decreased fatty acid unsaturation (reducing membrane fluidity and causing membrane rigidity), resulting in membrane dysfunction and cell death.
The filtrate of the bacterium (Alteromonas sp.) exhibited algicidal activity against the dinoflagellate (P. donghaiense) through the digestion of polysaccharides in the cell wall [22]. An algicidal exudate produced by Shewanella sp. also caused algal cell deaths accompanied by increased DNA degradation, ROS concentration and protease-associated program cell death [181]. The destruction of photosynthetic apparatus and cell breakage of M. aeruginosa were also reported by algicidal bacteria [157]. The study by Zhang et al. [182] showed the bacterium Brevibacillus laterosporus lyse cells of M. aeruginosa with an extreme morphological deformation. Moreover, the transcriptome analysis showed that this bacterium destroys the algal cell by efflux pump transporters, and secretion of hydrolytic enzymes, protease, antibiotics and another secondary metabolite which results in the algal cell death [182].
3.3. Strategies to apply the algicidal bacteria and the unresolved issues in the application
Although there is limited scientific data regarding the controlling of HABs with naturally occurring algicidal bacteria, the research interest in developing application strategies and management systems for controlling HABS with algicidal bacteria or their product has been increasing [28]. There are several application strategies including direct dispersal of algicidal bacteria and/or algicidal, deployment of immobilized bacteria, using multifunctional system, and deployment of substrates to recruit naturally occurring algicidal bacteria [28]. The deployment of these strategies varies depending on the type of HABs species, moreover, it requires an assessment of location, cost, feasibility and social acceptance. Although the application of algicidal bacteria and their product in their native environment is a preferable means of controlling HABS, there is a scarcity of scientific data evaluating its impact on natural communities. There are few prominent reports in this regard, and [183,184] recommended that the field trial is necessary to confirm the outputs are aligned with laboratory results. When transferring the laboratory-controlled studies to the field, it brought major challenges and complexities as it was influenced by various factors.
The algicidal activity of the bacteria can be influenced by various conditions including the growth phase and physiological status of the bacteria, the physicochemical condition including temperature, pH and oxygen level of the bacteria, and the growth phase and cell number of the target cells. Numerous conditions can influence the algacidal activity of the bacteria, posing several challenges to the technology of using bacteria to mitigate HABs. For example, the potency of the bacteria is dependent on the physicochemical and biological condition of the water column. Moreover, it has also been indicated that the algicidal activity of a bacterium is greatly influenced by the temperature and algal growth stage [185], the degradability of the algicidal compound in the environment, non-selectivity of algicidal activity [125], growth condition of the algicidal bacteria [125] and the presence of other bacteria that can digest the algicidal substance [36].
As mentioned above, the application of heterotrophic bacteria to control the formation of HABs has been challenged by some limitations; the specificity of the target group, efficiency and side effects on the biophysical condition of the water are some of them. For instance, a coculture study on algicidal and denitrifying bacteria (Brevunfimonas diminuta and Pseudomonas stutzeri), with colonial M. aeruginosa in a microcosm system showed that the abundance of Microcystis cells in the lower-water layers decreased due to the inhibitory effect of algicidal bacteria, while there was a rapid increase in Microcystis abundance in the upper layer, even when the ratio of algicidal bacteria to Microcystis was significantly increased [186]. Moreover, the same study showed the algicidal bacteria promoted the removal of dissolved total nitrogen in the upper and middle layers of Microcystis blooming water column, while the bacteria also enhanced the release of dissolved phosphorus in all layers. Furthermore, the algicidal bacterium Xanthobacter autotrophicus killed the HABs species M. aeruginosa resulting in massive algal biomass decay, which in turn, perturbed the water quality whereby the nutrient and microcystin concentration increased [187]. These results indicated that the application of algicidal bacteria should be followed by precautions to avoid undesired impacts on water quality and environmental health.
Besides its variation in efficacy across different environmental conditions, the algicidal activity of a bacteria also suffers from a lack of species-specificity to some extent. For instance, Pseudomonas chlororaphis produces metabolites that have broad spectrums that can kill fungi and phytoplankton [125], which is an undesirable feature in field applications. Similarly, the bacterium Bacillus fusiformis also showed algicidal activity non-selectively against a wide range of phytoplankton species including M. aeruginosa, Chlorella sp. and Scenedesmus sp. [188]. The algicidal activity of Labrenzia sp. was tested on multiple phytoplankton taxa, including chlorophytes, chrysophytes, cyanophytes, xanthophytes, pyrrophytes, and bacillariophytes. It effectively inhibited P. tricornutum (bacillariophyte), M. aeruginosa (cyanophyte), and six chlorophyte species [167]. This demonstrates the lack of species-specificity of Labrenzia sp. across different phytoplankton classes, highlighting the need for testing algicidal bacteria on various phytoplankton species before natural environment application.
The dosage of algicidal bacteria is another critical factor to consider during HABs treatment. For instance, the abundance of algicidal bacteria (B. fusiformis) showed a direct correlation with the mortality of algal cells, displaying greater degradation of algal biomass with greater initial bacterial cells [188]. Zhang et al. [189] also observed a dosage-dependent effect of Aeromonas sp. against M. aeruginosa. Moreover, when there is a low concentration of algicidal bacteria in the culture system it not only minimizes the growth inhibition process but can also promote the growth of HABs-forming species [190]. This indicates a need for high concentrations of algicidal bacteria for effective HAB control. The minimum concentration of algicidal bacteria required to kill the HABs species is commonly very high; Aeromonas sp. 2.1 × 108 cfu mL/L [161] compared to the concentration of algicidal bacteria found in natural conditions 0.8 cell mL/L [144]. However, bacterial behaviours like chemotaxis and swarming can intensify the effect by concentrating the bacteria around the target organism [16].
In addition to the dose, the mode of algicidal bacteria inoculation is another factor that influences the efficacy. For example, in vivo and in situ experiments showed that the bacterium X. autotrophicus displayed algicidal activity against M. aeruginosa whereby the massive decay of M. aeruginosa did not benefit the bacterium rather repeated inoculation of low concentration of the bacterium required for the optimum algicidal activity [187]. The physicochemical growth condition also significantly impacts the algicidal activity. For instance, oxygen availability markedly affects the activity of P. chlororaphis against the diatom P. tricornutum [125]. A study on the impact of algicidal bacteria on the dinoflagellate HAB species Karenia brevis in a non-axenic culture system revealed that the surrounding bacterial communities significantly influence K. brevis's susceptibility to algicidal agents [36]. This indicates, besides the growth conditions of both the algicidal bacteria and the algae, the composition and abundance of other bacterial communities also affect algicidal effectiveness.
Furthermore, a recent study showed that the growth stage of the HABs also affects their susceptibility level to the algicidal agent, with early-stage treatments being more effective [157]. This report showed a mechanism that designed to curb the HABs impact before the bloom of algae would give a better result. Additionally, physiological and morphological resistance mechanisms in HAB species, like cyst formation in certain dinoflagellates, present additional challenges to algicidal strategies [144]. While algicidal bacteria offer a promising avenue for HAB control, their application is complex and multifaceted. Future research should focus on enhancing the specificity and environmental viability of algicidal agents, understanding the optimal conditions for their application, and exploring innovative strategies to overcome the current limitations.
4. Utilizing bacteria in microalgae biomass processing
The important features such as fast growth and rapid biomass accumulation capability of microalgae promoted its amenability in various applications, including renewable biofuels and human food [191]. However, the high cost of algal biomass production and processing including harvesting and pretreatment remained the primary challenge in this sector.
4.1. The role of bacteria in harvesting microalgal biomass
The process of production of biofuel and valuable metabolites from microalgae involves cultivation, harvesting, extraction and conversion. From these processes, harvesting is one of the important steps that separate biomass from the culture media, and it can cover up to 20–30 % of the total production cost [192]. The low concentration of microalgal cells in the media and their small size (microscopic) caused technical difficulties and high operational costs during harvest, rendering microalgal biomass cultivation less attractive economically. To simplify this challenge, the utilization of algal species that are large-sized and capable of autoflocculation has been also proposed [192], although this technique is not practical since there are other criteria to be fulfilled as cultivable species. Thus, the commonly used harvesting method includes flocculation, centrifugation, gravity sedimentation, ultrasonication and filtration [193].
For microalgae, the centrifugation method can be considered as alternative because of its effectiveness and rapidity, however, it requires energy, which increases the operational costs. Membrane filtration would also be preferred, but the operational cost for membrane replacement is high as well [193]. From these, flocculation is simple, cheap and feasible for large volumes of microalgae biomass, thereby reducing operational costs of membrane replacement and energy output [194,195]. The microalgal biomass can be harvested through flocculation employing either physicochemical (autoflocculation) or biological methods. Then, flocs can be aerated to the surface or allowed to settle to the bottom by gravity sedimentation. As the surface of the microalgae cell wall is negatively charged to keep the algal cells stably suspended in the water by repelling each other (Fig. 4a), flocculation methods aimed to intervene with the surface negative charge and promote the agglomeration of cells (Fig. 4b).
Fig. 4.
A diagram illustrating a) the stable suspension of microalgae in the media due to the repulsion force created by the negatively charged surface of microalgae, and b) the flocculation of the microalgae biomass due to the bioflocculation effect of a bacterial exocellular polymeric substance (EPS).
Generally, the flocculation of cells is attained by either charge neutralism, adsorption bridging, sweeping and patching [196]. For example, autoflocculation (occurs when pH value exceeds 9) of cells can be induced through various mechanisms including adjusting the pH by modification of H+/OH+ ions ratio, modifying the electrostatic interactions between cells by provision of Mg2+ , creating an alkaline condition (pH > 10) and coprecipitation with Mg2+ and Ca2+, creating an acidic condition and adding of inorganic flocculants such as iron chloride and aluminium sulfate and inorganic salt [194,197]. The flocculation of the biomass by inorganic coagulants and bioflocculants is more convenient than the traditional methods of centrifugation or gravity filtration, from which bioflocculants have received more attention as they are biodegradable and non-toxic [[198], [199], [200]].
In the natural environment, various bacterial species have been known to induce microalgae aggregation and preceded by the demise of algal bloom events and the sinking of particulate organic matter. For example, Grossart et al. [201] showed the aggregate formation effect of marine bacteria on two diatom species S. costatum and Thalassiosira rotula. This phenomenon attracted phycologists and microbiologists and was further explored for its amenability for application in the flocculation of microalgae during the harvest. Likewise, several flocculant agent-producing bacterial species have been reported for the last four decades [198,[202], [203], [204]]. These bioflocculants can be categorized as proteins, glycoproteins and polysaccharides [205].
The bacteria Nocardia amarae [206], Rhodococcus erythropolis [207] and Pacilomyces sp. [202] produce protein flocculant; Bacillus sp. [208] and Alcaligenes latus [209] produce polysaccharide flocculants; Arathrobacter sp. [210] and Arcuadendron sp. [211] produce glycoproteins. These studies highlight the potential of some bacterial species to be applied in flocculating the microalgae biomass. Subsequently, bacterial (Bacillus licheniformis) flocculant biopolymers capable of flocculating various organic and inorganic suspension effectivity and synergically with bivalent (Ca2+) or trivalent (Fe3+ and Al3+) cations at neutral pH have been reported [205]. Moreover, bioflocculation of microalgae by treating with another microalgae [212], fungi [213,214] and extracted bioflocculant [199] or self-induced autoflocculation [215] have been reported.
Various studies have documented enhanced flocculation performance from bacterial treatments. For instance, Kim et al. [216] found that treating Scenedesmus sp. with the flocculant bacterium Paenibacillus polymyxa resulted in high (95 %) flocculating activity. Similarly, Lee et al. [217] observed that the combined presence of Flavobacterium, Terrimonas, and Sphingobacterium significantly increased the flocculation of C. vulgaris from 2 % to 94 %. Oh et al. [218] reported the bioflocculant produced by the bacterium Paenibacillus sp. showed higher (83 %) flocculation activity towards C. vulgaris compared to aluminium sulfate (72 %) and polyacrylamide (78 %), especially at higher pH levels Citrobacter sp.'s treatment of C. pyrenoidosa yielded a 97.37 ± 2.96 % biomass harvest with improved FAME quality, where the flocculation mechanism was mainly facilitated through net catching, adsorption bridging, and sweeping mechanisms [219]. Recently, coculturing of the bacterium Streptomyces rosealbus and the microalgae C. vulgaris exhibited mutualistic interaction, which promoted algal biomass accumulation as well as flocculation [220]. The marine actinobacterium Streptomyces sp. showed bioflocculation activity towards microalgae Nannochloropsis [221].
Flocculation efficiency is influenced by various environmental factors, including buffer concentration, nutrient availability, bacterial dosage, pH, and salt types [222]. Takeda et al. [206] found that Nocardia amarae's flocculation efficiency improved in 10 mM and 50 mM buffer solutions compared to 1 mM sodium phosphate buffer. Increased flocculation activity of flocculant polymer produced by Bacillus subtilis was observed by the addition of Ca+2 [223]. Similarly, the effectiveness of a bioflocculant polymer from B. subtilis varied with cation concentration, temperature, and pH [204]. Ndikubwimana et al. [224] demonstrated that a bioflocculant from B. licheniformis increased the flocculation efficiency of Desmodesmus sp. from 43.8 ± 1.6 % to 98.2 ± 0.1 % when the culture's initial pH was adjusted from 7.2 to 3. Additionally, microalgae-bacteria bioflocculation has found applications in wastewater treatment [25,[225], [226], [227]].
Although several research studies indicated the potential of bioflocculant bacteria for microalgae biomass harvest, this technology suffers from several drawbacks. These include the production of flocculant agent by bacteria, which is critically affected by the physicochemical condition of the growth environment, the type of media has effects on the amount of flocculant agent, the flocculant agent can be utilized by other microbes, and some bacteria strains require to be kept in growth media until it produces an optimum amount of exopolysaccharide [228]. Hence, despite the increasing interest and studies on bacterial bioflocculation benefits in harvesting microalgae biomass, pilot projects tested on real-world applications are almost nonexistence. Hence, a significant amount of time and research studies are required in the future for the commercialization of this technology.
4.2. The role of bacteria in pre-treating microalgal biomass
Nowadays, the pertinence of cultivation of microalgal biomass for renewable sources of energy such as biodiesel, biogas, and bioethanol and desirable metabolites including pigments, proteins and lipids is increasingly recognized. Microalgae species rich in lipids are favoured as feedstock for biodiesel production, whereas those high in carbohydrates are suitable for fermentative biofuel production [229]. The Chlorophyceae, green microalgae, primarily consists of starch in the plastid and carbohydrates in the cell wall. As the majority of microalgae cell walls are composed of carbohydrates and do not have lignin in the cell wall matrix, they are a promising source of biofuel.However, the biotechnological exploitation of microalgae faces scientific, economic, and technological challenges, particularly during biomass processing [230,231]. Addressing these issues is crucial to fully harness microalgae's potential in biotechnological applications. A key obstacle is the complex, resistant nature of microalgae cell walls, making pretreatment a vital step in the biomass conversion process. Since the cell wall of microalgae is composed of rigid components such as cellulose and pectin, biological pretreatment is required to avoid the recalcitrance of the cell wall by disrupting it and allowing the hydrolytic enzyme to access the cell contents [232].
To improve the efficiency of microalgal biomass processing it could be pretreated with biological methods such as bacteria, fungi and enzymes [[233], [234], [235]], chemical methods including oxidative, acidic alkaline and organo-solvent [236], or mechanical and physicochemical methods such as pulsed electric field, ultrasonication, steam explosion, bead milling and microwave [[237], [238], [239]] to disrupt cell wall. The ideal method for the extraction or conversion of biomass should be eco-friendly and cost-efficient, providing net output energy with minimal impact on downstream processes. For example, the use of pretreatment chemicals could be effective in extraction efficiency but it has a significant effect on the downstream processes. Thus, the pretreatment of microalgal biomass with biological methods using bacteria has become one of the promising alternative approaches which have low energy demand, little effect on downstream processes, is ecofriendly and easily applicable [236]. Additionally, biological pretreatment allows the simultaneous production of different value-added products from mainstream compounds or byproducts [229]. Moreover, bacteria can also be involved in the conversion of microalgal biomass into organic acids and hydrogen [240].
Several studies showed biological pretreatment of microalgal biomass yields enhanced outcomes compared to untreated biomass [241]. For example, treating C. vulgaris with Bacillus thuringiensis for lipid extraction increased biodiesel production by 44.3 % [242]. Similarly, Chlorella sp. showed a 9.2–33.7 % increase in methane production after pretreatment with B. licheniformis under anaerobic conditions. Liquefaction of C. vulgaris also enhanced by the presence of bacterium for better production of methane [243]. The pretreatment of C. vulgaris by the bacterium Flammeovirga yaeyamensis showed 100 % increased lipid extraction efficiency [244]. The pretreatment of Nannochloropsis gaditana with two strains of Raoultella ornithinolytica under anaerobic conditions enhanced the yield of methane by 140.32 (the first strain) and 158.68 % (second strain) over non-pretreated microalgal biomass [245]. Given the wide range of applications for microalgal biomass, future research is expected to maximize the socioeconomic and scientific benefits obtained from microalga-bacteria interactions.
The biomass can be processed in biochemical, thermochemical, or hydrothermal routes. During the biochemical biomass conversion, the microalgae biomass could be processed through pretreatment, hydrolysis and fermentation steps. Then, fermentation being the final step, converts the soluble sugars from the upstream process into biofuels such as biobutanol, bioethanol, biohydrogen and biogas [229]. The specific pretreatment can vary depending on the intended bioconversion process and the desired end product. Although the biological treatment has shown significant potential, its large-scale application is limited by factors like insufficient cellulose modification, long incubation times, carbohydrate loss, and reduced yields in subsequent processes [246]. Furthermore, the variability in microalgae cell wall composition and properties, influenced by species and growth environment, complicates pretreatment and downstream processing [239]. Therefore, selecting the appropriate enzyme-secreting bacteria is imperative for effective pretreatment.
The application of bacteria as a pretreatment method could be enriched with some advantages over conventional physical, mechanical or biological methods. These include selective degradation of compounds, no need for corrosive chemicals, minimizing the release of chemicals that might interfere in the downstream process, needing relatively low operational energy, eco-friendly, can assist the downstream process including saccharification, and no need for continuous addition as the bacteria cells reproduce [236].
The hydrolytic bacteria applied in microalgae biomass for pretreatment are capable of causing an algicidal effect by disintegrating the cell wall and hydrolysing the intracellular content of macromolecules. Several bacterial species including Aeromonas sp., Pseudomonas pseudoalcaligenes, Chryseobacterium sp. and R. ornithinolytica [245], Sagittula stellata [180], B. licheniformis [247], Clostridium thermocellum [248] and F. yaeyamensis [244] are known for their ability to breakdown the microalgae cell wall. These bacteria produce various enzymes such as xylanase [249], cellulase and others [250], which facilitate the pretreatment process.
Different species of bacteria secrete a variety of enzymes including cellulase, protease, pectinase, lysozyme, lipase, xylanases, chitinase and amylases, which play crucial roles in biomass degradation [229]. The bacterium Chitinimonas prasine produces an algicidal agent (chitinase) that attacks the diatoms Thalassiosira pseudonana by degrading the cell wall and causing cell lysis [168], whereas the flavobacterium Kordia algicida attacks diatom species Skeletonema, Thalassiosira and Phaeodactylum by secreting extracellular protease enzyme [97]. Similarly, cell wall breakage of C. vulgaris by C. thermocellum [248] and cell membrane destruction of dinoflagellate Alexandrium tamarense by the bacterium Mangrovimonas yunxiaonensis [143] has been reported. As algicidal bacteria secrete enzymes that specifically lyse algal cell walls and perform hydrolysis, algicidal bacteria are considered ideal for biomass pretreatment. However, despite the extensive research on the algicidal effect of bacteria, there are limited studies on their use as a pretreatment method for microalgae biomass [248].
Microalgae contain biopolymers like polysaccharides (starch and cellulose), protein and lipids, which are vital parts of biofuel production. In pretreatment of microalgal biomass, the cellulose of microalgal biomass is degraded by three synergetic enzymes, endo-β-(1 → 4) glucanase, exo-β-(1 → 4) glucanase and β-glucosidase. Starch breakdown involves isoamylases, pullulanases, endo-α-amylases, exo-β–amylases and glucoamylases, where these enzymes step by step actions produce monomers of glucose and maltose [229]. The lipid component, an essential substrate for biodiesel, biogas, and biohydrogen, is initially hydrolysed into glycerol under anaerobic conditions and followed by converting into long-chain fatty acids with extracellular enzyme lipases. In protein hydrolysis, the proteolytic enzyme initially breaks down the polypeptide chain converting it into small peptides and subsequently into monomers of amino acids [229].
Several intrinsic or extrinsic factors affect the performance of bacterial pretreatment of microalgal biomass, including temperature, moisture content, pH, bacterial species type, pretreatment time, and bacterial inoculation concentration [229]. One of the key limitations in the conversion of biomass is the inefficient activity of the hydrolysing enzyme. To overcome this, studies have shown that chemical agents (methylmethanesulfonate, diepoxybutane, ethylmethanesulfonate, and sodium azide) and physical irradiations (X-rays, gamma rays, and ultraviolet) can enhance enzyme hydrolysis by inducing bacterial mutation [[251], [252], [253]]. However, due to the risks associated with these mutagens, alternative methods like plasma immersion ion implantation using argon or nitrogen have been explored. Regarding this, Sangwijit et al. [254] investigated the biomass hydrolysis potential of the cellulase-secreting bacterium Bacillus amyloliquefaciens by treating mutation inducer techniques, such as argon or nitrogen plasma immersion ion implantation. The result indicated that the cellulase activity of the mutant bacterial cells was enhanced compared to the control (wild type), under various temperatures, pH and biomass substrates. Additionally, genetic engineering and enzyme cloning have been used to further improve hydrolysing enzyme applications [249].
Although studies indicated that the combined effect of both bacteria cells and their cultivation media offered an effective means to increase metabolite yield during microalgae biomass pretreatment, the particular makeup of microalgae and its cell wall composition varies between species [180]. Hence, the effectiveness of bacterial lysing on microalgae would be variable with different algal species, implying that a specific study is required to determine viable applications of a particular species. Moreover, as the pure culture of bacteria has been employed in the pretreatment process, due to some shortfalls, such as the inability to implement in an open system, maintenance of the precondition for pure culture and a prolonged time for pretreatment necessitate the development of other strategies such as microbial consortia have been proposed [255,256]. These consortia are thought to work synergistically, improving adaptability, hydrolysis efficiency, productivity, substrate utilization, and pH adjustment [229]. However, there is still a research gap in demonstrating the effectiveness of microbial consortia in the pretreatment of microalgal biomass conversion.
5. Technological evaluation, environmental impacts and future perspective
The natural occurrence of algicidal bacteria and their response to algal blooms suggest avenues for enhancing the application of algicidal bacteria in HABs control. Although the application of algicidal bacteria technologies has gathered great interest in research and consideration for potential applications, it has also some limitations. So far, several bacterial strains and their algicidal product have proven useful means to inhibit algal cells via flocculation and lysis under controlled conditions. For instance, recently, the bacterium Streptomyces sp. HY exhibited algicidal activity towards several cyanobacteria species, including a 93.04 % removal rate of M. aeruginosa cells. In the same report, the authors also indicated the algicidal bacteria had a minor effect on a green algae Scenedesmus obliquus, which might considered as a preferable feature regarding target species selectivity [171]. Moreover, a complete removal of the HAB species Oscillatoria by the algicidal bacterium Enterobacter sp. has been reported [164]. Nevertheless, the scarcity of scientific data on its biosafety concerns remained largely unresolved, posing many uncertainties when it comes to its application in natural waters. For instance, the bacterium Pseudomonas putida showed algicidal activity towards M. aeruginosa and a wide range of phytoplankton groups [175], increasing the risk of side effects on aquatic life.
Moreover, although most of the algacidal bacteria currently under investigation are naturally occurring, the biosafety issues remained a concern with large-scale dispersal of algicidal bacteria. For example, the Shigella, Vibrio and Alcaligenes are naturally occurring algicidal bacteria, but they also bring danger to human health and aquatic life. Alternatively, a matrix of concentrated and immobilized bacteria can be deployed in HABs risk area to minimize the negative impacts [28]. For example, the immobilization of algicidal bacteria in alginate beads prevents the release of algicidal bacteria into the environment while allowing diffusion of the algicides, and with a similar algicidal activity of free-living counterparts [257].
The other major technological limitation for environmental application comes from the release of increased toxins into the water after the algal cell lysis by algicidal bacteria. To avoid this bifunctional system that can both lyse the alga cell and degrade the toxin has been proposed [29]. Furthermore, the lysis of algal cells also results in increased nutrient concentration. Owing to this, recently Ma et al. [258] showed that the algicidal bacteria Streptomyces sp. synchronized to actively remove nitrogen and the HAB species M. aeruginosa. An enhanced adsorption by algicidal bacteria to control the HAB species M. aeruginosa was also reported [259]. On the other hand, the microalgae particularly cyanobacteria in natural water tend to have stronger resistance than laboratory culture due to the colonial form of algal cells [170], indicating field trial is required before applications.
The variation of potency depending on the growth conditions is also another limitation. For example, the cell-free filtrate of the algicidal bacterium Shewanella sp. showed a significant algicidal effect towards dinoflagellate species blooms in a laboratory microcosm experiment performed in water collected from the field, while there was lower algicidal activity observed in laboratory monoculture [260]. The algicidal bacteria Lysobacter enzymogenes inhibited M. aeruginosa with dilute yeast extract, while in a microcosm experiment it did not affect the M. aeruginosa but inhibited the flagellates, ciliates, and fungi [170]. A more detailed discussion on factors affecting the efficiency of algicidal bacteria are described in Section 3.3.
In terms of techno-economic evaluation, the current approach of controlling HABs with algicidal is not economical and infeasible, requiring more research in the future to make it suitable for large scale application. To avoid or minimize this challenge, comprehensive investigations on the diverse interaction mode of algae and bacteria, selecting appropriate algicidal bacteria with high specificity and selectivity, analysis of its impact on the environment and economic feasibility are required (Fig. 5).
Fig. 5.
A schematic diagram showing the general processes involved in the utilization of algicidal bacteria in controlling HAB. Detailed information is indicated in Coyne et al. [28].
In terms of environmental impacts, as the utilization of algicidal bacteria enhances the output of HABs control, mass-scale application of the technology will come in the future, potentially posing a negative effect on the environment. Whether the utilized bacteria are wild-type species or genetically engineered, the risk of environmental contamination remains. For instance, genetic engineering techniques have been widely applied to increase the applicability of microbial biotechnology [57]. Engineered bacteria exhibited additional substrate specificity and increased algal cell wall disruptions, and growth inhibition of HABs has been reported [261,262]. However, the application of this in the natural environment might cause unpredictable effects on the environmental health and ecosystem. Hence, the application of engineered microorganisms into the natural environment requires extensive efforts to evaluate their biosafety and environmental impacts (Fig. 5).
Moreover, there is limited information about the effect of algicidal agents on the natural microbial ecosystem. Owing to this, Zhang et al. [263] conducted research by creating a microcosm of P. globosa (HABs forming species) and analysed the dynamics of microbial communities in response to the algicidal agent (prodigiosin); even though the contribution of Rhodobacteraceae increased, the algicidal agent did not affect the microbial communities. In contrast to that, the cell-free filtrate of algicidal bacterium Shewanella sp. caused a significant change in the eukaryotic community structure in laboratory microcosm experiments [260]. Furthermore, Zhang et al. [264] demonstrated that in near in situ simulated algal blooming seawater, low concentrations of algicidal molecules produced by Gammaproteobacteria caused substantial changes to phytoplankton community with the decline of diatoms and dinoflagellates. Hence, more comprehensive laboratory and field studies are needed to understand the effect of algicidal agents on the function of microbial communities and its cascading effect on higher trophic levels before its application in the natural environments.
Intensive studies and efforts are required in the future to deepen our understanding of interactions between algae and bacteria, comprehend the algal bloom patterns, prevent diseases from pathogenic microbes, mitigate effects on microbial communities, predict responses to environmental changes, and maximize the scientific and socio-economic benefits. As many research results indicated algal-growth-promoting or algae-inhibiting bacteria occur during or after the HABs event, and more laboratory and field metagenomics/metaproteomic data of the entire microbial community's diversity before, during and after the bloom event will be needed from future research to comprehend the dynamics of algicidal bacteria and other aquatic microbes. The result of this kind of research will create a wide opportunity to understand HABs process and mitigation mechanism by illuminating the identity and function of the whole microbial consortia under fluctuating environmental conditions.
Furthermore, by considering the occurrence of algicidal bacteria in natural water bodies [13], the growth of these algicidal bacteria increases following the blooms of algae [265], and the common communication means of bacteria by quorum sensing signals and using some metabolite produced by phytoplankton as a cue for initiation of algicidal activity [128], future research could be envisioned to enhance the algicidal activity by releasing mimicry compounds that can be used as a cue for the growth of algicidal bacteria (to initiate the growth of algicidal bacteria before the actual blooms of HABs) and investigating if there are possible means to halt the consequence of HABs event. Additionally, recent advancements have highlighted the potential of artificial intelligence (AI) and machine learning (ML) in improving microalgae-bacteria coculturing, particularly in wastewater bioremediation [266]. Machine learning algorithms have been employed to optimize growth conditions in coculturing systems, dynamically adjusting environmental parameters and nutrient levels to enhance biomass production and pollutant removal [[266], [267], [268]]. These novel AI/ML approaches offer promising avenues for more efficient and effective wastewater treatment processes, aligning with environmental management goals.
6. Conclusion
This comprehensive review paper explored the divers’ interactions mechanisms between microalgae and bacteria, highlighting their amenability to control harmful algal blooms and enhance biomass processing efficiency. Although several research studies have been conducted on the application of bioflocculant bacteria on microalgae biomass processing and algicidal bacteria to control HABs formation, the practical application of these technologies face several limitations that require thorough research in the future. These limitations include, optimization of growth conditions to large-scale applicability, the selection of complimentary species, target species specificity, and impacts on the natural environment. Addressing these issues will pave the way for advanced technologies that promote sustainable biomass processing and maintain aquatic environmental health.
Funding statement
This work was funded by the National Natural Science Foundation of China (No: 31971477) and the Hubei Provisional Science Fund (SFC2109150002).
Data availability
Has data associated with your study been deposited into a publicly available repository? NO.
Has data associated with your study been deposited into a publicly available repository? No data was used for the research described in the article.
Data will be made available on request.
Declaring ethical statement
The authors declare that the manuscript was prepared according to the updated, complete and ethical consideration.
CRediT authorship contribution statement
Rediat Abate: Writing – review & editing, Writing – original draft, Conceptualization. Yoong-Ling Oon: Writing – review & editing. Yoong-Sin Oon: Writing – review & editing, Conceptualization. Yonghong Bi: Conceptualization, Writing – review & editing. Wujuan Mi: Writing – review & editing. Gaofei Song: Writing – review & editing. Yahui Gao: Conceptualization.
Declaration of competing interest
The authors declare that they have no known competing financial interests or personal relationships that could have appeared to influence the work reported in this paper.
Acknowledgments
This work was funded by the National Natural Science Foundation of China (No: 31971477) and the Hubei Provincial Science Fund, China (SFC2109150002). We have used the free service of Biorender to draw illustrations.
Contributor Information
Rediat Abate, Email: rediat.abate@yahoo.com.
Yonghong Bi, Email: biyh@ihb.ac.cn.
Gaofei Song, Email: song@ihb.ac.cn.
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Data Availability Statement
Has data associated with your study been deposited into a publicly available repository? NO.
Has data associated with your study been deposited into a publicly available repository? No data was used for the research described in the article.
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