Next Article in Journal
Biomass Clusterization from a Regional Perspective: The Case of Lithuania
Previous Article in Journal
Overview of Possibilities of Solar Floating Photovoltaic Systems in the OffShore Industry

Biocrude Oil Production by Integrating Microalgae Polyculture and Wastewater Treatment: Novel Proposal on the Use of Deep Water-Depth Polyculture of Mixotrophic Microalgae

MoBiol Technologies Corporation, 1155-50 Kakioka, Ishioka 315-0116, Ibaraki, Japan
ABES, Faculty of Life and Environment Sciences, University of Tsukuba, 1-1-1 Tennodai, Tsukuba 305-8572, Ibaraki, Japan
Author to whom correspondence should be addressed.
Academic Editor: Alberto-Jesus Perea-Moreno
Energies 2021, 14(21), 6992;
Received: 8 September 2021 / Revised: 19 October 2021 / Accepted: 20 October 2021 / Published: 25 October 2021
(This article belongs to the Section I1: Fuel)


Microalgae have attracted significant attention worldwide as one of the most promising feedstock fossil fuel alternatives. However, there are a few challenges for algal fuels to compete with fossil fuels that need to be addressed. Therefore, this study reviews the R&D status of microalgae-based polyculture and biocrude oil production, along with wastewater treatment. Mixotrophic algae are free to some extent from light restrictions using organic matter and have the ability to grow well even in deep water-depth cultivation. It is proposed that integrating the mixotrophic microalgae polyculture and wastewater treatment process is the most promising and harmonizing means to simultaneously increase capacities of microalgae biomass production and wastewater treatment with a low land footprint and high robustness to perturbations. A large amount of mixotrophic algae biomass is harvested, concentrated, and dewatered by combining highly efficient sedimentation through flocculation and energy efficient filtration, which reduce the carbon footprint for algae fuel production and coincide with the subsequent hydrothermal liquefaction (HTL) conversion. HTL products are obtained with a relatively low carbon footprint and separated into biocrude oil, solid, aqueous, and gas fractions. Algae biomass feedstock-based HTL conversion has a high biocrude oil yield and quality available for existing oil refineries; it also has a bioavailability of the recycled nitrogen and phosphorus from the aqueous phase of algae community HTL. The HTL biocrude oil represents higher sustainability than conventional liquid fuels and other biofuels for the combination of greenhouse gas (GHG) and energy return on investment (EROI). Deep water-depth polyculture of mixotrophic microalgae using sewage has a high potential to produce sustainable biocrude oil within the land area of existing sewage treatment plants in Japan to fulfill imported crude oil.
Keywords: mixotrophic algae; polyculture; wastewater treatment; HTL; biocrude; nutrient recovery mixotrophic algae; polyculture; wastewater treatment; HTL; biocrude; nutrient recovery

1. Introduction

As a true alternative to fossil fuels, an ideal organism produced in large quantities of 4,474,330,000 tons worldwide must have at least 12 requirements (Table 1).
Land plants and algae, which are principally photosynthetic organisms, have attracted significant attention worldwide as promising feedstocks for future fossil fuel alternatives. However, whether edible or inedible, land plants require arable land concomitant with a large amount of freshwater resources and have relatively low lipid productivity for biodiesel production. Thus, they lack in sustainability for requirements (1), (3), (4), (5), (6), (11), and (12) in Table 1. Microalgae potentially have more advantages than land plants for requirement (1) to (7). According to model analysis on wastewater treatment by algae, the production cost of algae oil is lower than that of fossil fuels by simultaneously achieving algae biomass production and sewage purification [3]. Microalgae have a high potential to produce biofuel with a much lower land footprint than land plants due to their high oil yield capacity. However, photosynthetic microalgae must be cultured at a shallow water depth (<0.2 m) to avoid impairing light utilization efficiency. It means that microalgae with high biomass production (assuming 100 tons·ha−1·year−1 and 50% oil content), 2.8 million ha is required for the actual cultivation area alone to cover Japanese crude oil imports (0.13 × 109 tons·year−1 in 2020). In contrast, the total area of sewage treatment plants in Japan is 1.37 million ha, and it is necessary to increase the algae biomass productivity per land area to achieve the Japanese demand for crude oil by using the existing footprint of sewage treatment plants. Additionally, microalgae have some issues for the future commercial application in reference to requirements (8), (9), (11), and (12), such as a lower energy return on investment (EROI) and higher biomass production cost than land plants, the necessity for a large land area, and vulnerability to environmental and biological stresses, which should be solved for future use as an alternative to fossil fuel. In particular, the traditional lipid extraction–transesterification method for producing biofuel from lipid rich microalgae is energy intensive because it requires the drying of cultured microalgae. Hydrothermal liquefaction (HTL) of biomass into biofuel has attracted significant attention as a solution to serious issues imposed by traditional methods. HTL is advantageous. The reason is that it uses wet biomass directly and converts the entire algae biomass to biocrude oil. However, the differences of biochemical composition combined with various optimal conditions make general prediction and operation of HTL difficult [4]. Additionally, developments on conventional HTL processes to increase EROI, lower capital and process costs, and accelerate CO2 reduction through technology innovation are needed [4,5,6,7,8]. The development of innovative HTL technology to solve these issues is steadily progressing [4,9,10].
In many cases, monocultures of oil-rich and high-growth microalgae have been used for algal fuel production. However, good growth under optimal and suboptimal environmental conditions is limited by the tolerance level of the cultured species. Particularly in temperate regions, it is difficult to maintain monocultures of microalgae at high and stable algae production throughout the year due to large fluctuations in the annual temperature and solar radiation. In addition, microalgae monoculture is sometimes subjected to total algae biomass loss due to natural introduction of predator or pest species [11]. Therefore, it is difficult to establish a stable year-round biomass production without appropriate environmental controls using the monoculture concept in temperate regions. Temperate regions, occupying 10% of the earth and 30% of the land, are home to approximately half of the world’s population and have high land-use rates, with various industries being constructed. Thus, energy production in temperate regions is essential when considering global and national energy security. Microalgae biomass production in monoculture is more costly and energy-intensive than terrestrial energy crop production [12,13]. For these reasons, it is necessary to develop technology to produce stable algae-based fuels throughout the year in temperate regions with large environmental fluctuations and limited land area to make them competitive with fossil fuels [14].
The polyculture of native microalgae communities is more suitable for large-scale biomass production and has several advantages compared with monocultures of specific strains [11,15]:
  • stable culture and production because of the mixed component of algae with diverse of tolerance levels and the absence of pond crash;
  • the efficient use of resources (nutrients) by niche complementarity;
  • cheap and easy operation and maintenance.
The cultivaton of native algal communities has been effectively used for wastewater treatment in open ponds [16,17,18,19,20]. The Look Back at the US Department of Energy’s (DOE’s) Aquatic Species Program [21] recommended the development and demostration of microalgae biodiesel production as part of a wastewater treatment process. A subsequent model study in this field of research showed that when the primary process objective was wastewater treatment with biofuels as a byproduct, bio-oil production cost in 100 ha area was estimated to be approximately one-third of petroleum oil prices [3]. It was first reported that wastewater treatment by microalgae could reduce the cost of biofuel production. Therefore, it is necessary to demonstrate and verify this model at the scale of a conventional waterwater treatment plant.
The performance of the microalgae-based wastewater treatment process is mainly a function of algal production and wastewater treatment capacities. When using photosynthetic microalgae, the culture depth should be shorter to secure higher average irradiance for algal photosynthesis, resulting in high algal production and nutrient recovery. However, a shorter culture depth decreases the amount of wastewater treated per surface unit; thus, the algae-based wastewater treatment process requires a larger area than the conventional wastewater treatment process [22,23], resulting in a large land footprint. Therefore, it is necessary to propose a method to solve this dilemma.
This study reviews the R&D status of algae-based polyculture and biocrude oil production using wastewater with special reference to sewage treatment, which is attracting significant attention as it corresponds to most of the above ideal conditions. Sewage containing organic and inorganic pollutants, such as biological oxygen demand (BOD) components, nitrogen, and phosphorus, is an excellent source of nutrients for mixotrophic microalgae. Consequently, mixotrophic microalgae can be expected to purify the sewage to meet the quality standards of discharge water established in each country, resulting in high nutrient recovery. We also highlight the appropriate concentration and dewatering methods eligible for the subsequent HTL biocrude oil conversion and reasonable algal biofuel life cycle assessments. Since microalgae polyculture grown using sewage may sometimes be low in lipid content [14], an HTL method that converts the entire algae biomass into biocrude oil under high temperature and pressure should be employed. As HTL facilitates the conversion of the entire fraction of lipids, proteins, and carbohydrates to biocrude oil, it is unnecessary to promote lipid accumulation and extract the lipids. The essential factors for the efficient production of HTL biocrude oil are the need for stable and high algal biomass production. The overall economics for the HTL algal pathway are more strongly influenced by improvements in algae biomass productivity [24]. Therefore, the appropriate concentration and dewatering methods for the optimization of the conversion process and biocrude-oil quality should be considered.
This study proposes a considerable improvement on the upstream process, the best selection of an appropriate concentration, and the advantages and usefulness of biocrude-oil production through HTL from wastewater-grown algae polyculture. The realistic view of its amount of land use highlights the recent deep water-depth polyculture of mixotrophic microalgae combined with wastewater treatment process. This suggests that it is the most promising way to simultaneously increase capacities of algal biomass production, achieving wastewater treatment with high perturbation resilience and biocrude oil production, showing a high potential to meet the current demand of crude oil in Japan [14,25,26,27,28].

2. Wastewater in the World and Japan

Global freshwater withdrawals are estimated to be 3928 km3·year−1, 56% of which is released into the environment as wastewater as municipal and industrial effluent and agricultural drainage water [29]. On average, high-income countries treat 70% of wastewater; however, the ratio drops to 38%, 28%, and 8% in upper-middle-income, lower-middle-income, and low-income countries, respectively [30]. These estimates support the suggestion that more than 80% of wastewater is released into the environment without adequate treatment [31].
In Japan, the annual sewage treatment is 15.4 billion m3 in a total area of 1.37 million ha. Assuming three cases of 10,000, 50,000, and 100,000 m3 as the maximum daily inflow of sewage water, operation/maintenance costs and energy consumption per unit (m3) are estimated to be 27–13 JPY·m−3 and 3.02–1.76 MJ·m−3, respectively, using the conventional activated sludge process and 32–17 JPY·m−3 and 3.86–1.87 MJ·m−3, respectively, using the advanced anaerobic–anoxic–oxic process (Table 2) [32].
In the conventional activated sludge process, a 1 kg chemical oxygen demand (COD) reduction produces 0.3 to 0.5 kg of dry-weight secondary sludge, and 0.78 kg CO2-e·m−3 is discharged during the sludge treatment process [33]. The greenhouse gas (GHG) emissions during sewage treatment are estimated to be 3% of global GHG emissions [34]. In Japan, the annual GHG equivalent to 6.95 million tons of CO2 is emitted during the sewage treatment, accounting for approximately 0.5% of total CO2 emissions [35]. The blower used on the activated sludge treatment consumes most of power consumed during water treatment. Approximately 24% of excess sewage sludge is recovered for energy generation, such as methane production, and 10% is recovered as fertilizer on green farmland. The remaining sewage sludge is incinerated to generate N2O in the process, which accounts for 24% of GHG emissions in sewage treatment [36]. In addition, to avoid the worst scenario of phosphate ore depletion by 2060 [37], it is necessary to recover phosphorus from wastewater and waste. Approximately 10% of phosphorus imported in Japan flows into the sewerage system, of which only about 10% is used as compost [38]. The main commercial processes for removing and recovering phosphorus from wastewater effluents, such as chemical precipitation with iron, alum, or lime, is required. However, this process requires further refining, fine-tuning, and optimization. It renders the precipitates difficult, if not impossible, to recycle in an economical industrial manner [39]. Thus, the algal accumulation of phosphates has been extensively studied to evaluate their sustainable use of phosphates [39,40].
There are advancements in wastewater treatment, such as anaerobic treatment, membrane reactors, microbial fuel cells (MFCs), and anammox technology. However, they have advantages and disadvantages. Anaerobic treatment is used in the current wastewater treatment; however, it consumes twice as much energy as an aerobic treatment [41] and requires a prolonged hydraulic retention time [42,43]. Membrane reactors are fundamentally based on anaerobic technology, offering quicker start-up times, shorter retention times, and better COD removal; however, it causes the dissolution of methane in treated water and fouling in the reactor [33]. The COD removal efficiency of MFCs ranges above 50%; however, it is lower than anaerobic treatment [44,45]. Anammox treatment reduces the COD by 90% or more and CO2 emissions by 60% or more [46]. However, the anammox reaction requires further treatment to reduce the nitrogen due to the production of a certain amount of nitrate as a by-product. Optimal control technology for nitrate reduction by denitrifying bacteria (heterotrophic bacteria) and ammonia oxidation by anammox bacteria (autotrophic bacteria) is required for practical use. Overall, the above advanced technologies cannot treat and recover phosphorus. Considering the need for energy-efficient blowers, sludge reduction, and phosphorus recovery, as well as the ability of algae to purify sewage, which has been demonstrated in recent years, it is necessary to consider the introduction of algae for wastewater treatment.

3. Algae Biomass Production and Wastewater Treatment

Many authors have supported integrating wastewater treatment and algae biomass production [3,47,48]. Multiple benefits include the circular use of freshwater by purifying sewage, thus reducing the cost of biofuel production, creating and increasing market value for non-portable water supplies, and reducing the impact of contaminated water on the living environment and ecosystems [11]. According to model analysis, the algae oil production cost is less than USD 0.18·L−1 oil, significantly lower than that of fossil fuels; algae biomass production cost can be reduced to be less than EUR 1 kg−1 dry-algae by simultaneously achieving algae-based oil or algae biomass production and sewage purification [3,23]. Thus, research on optimal integrated technology for algal biomass production and sewage treatment have been extensively conducted to verify this model [43,49,50]. In this study, we focus on achieving the ideal algae fuel production as an alternative to fossil fuels.

3.1. Mixotrophic Algae

There are three nutritional modes in microalgae: photo-autotrophic (photosynthesis), heterotrophic, and mixotrophic, a combination of the first two modes. Thus, mixotrophic algae are less light restricted using organic matter and can grow well even in deep water-depth cultivation [14]. In the algae polyculture on wastewater, the mixotrophic microalgae community contributes exceedingly to the overall algae biomass production and sewage treatment and purification. Wastewater, containing organic and inorganic pollutants, such as BOD, nitrogen, and phosphorus, is an excellent source of nutrients for mixotrophic microalgae.
It has been emphasized that heterotrophic and mixotrophic microalgae can assimilate only low-molecular-weight compounds, such as glucose and glycerol; thus, it cannot be assumed that mixotrophic microalgae can degrade and use large organic compounds [23]. However, it has been revealed that marine coccolithophores and freshwater mixotrophic microalgae strains of Scenedesmus and Chlorella could use a wide range of organic substrates, such as carbohydrates, carboxylic acids, amino acids, amines, phenolic compounds, and polymers [51,52]. In addition, diverse organic substrates such as monosodium glutamate wastewater, cheese whey permeate, and fruit peel have been successfully used for mixotrophic microalgae growth [53,54,55,56]. Thus, mixotrophic microalgae play a significant role in reducing COD/BOD in wastewater such as heterotrophic microbes; they also have a high potential for biomass and biofuel production using organic wastewater, which is an anthropogenic GHG source.
A field experiment demonstrated that mixotrophic microalgae biomass productivity possibly exceeded the sum of potential photoautotrophic and heterotrophic productivities of the microalgae [14]. This suggests that the mixotrophic growth is not a simple combination of photoautotrophic and heterotrophic growth, as it has been extensively reported previously in laboratory studies [53,57,58]. Acetate can be metabolized by algal cells via acetyl-coA to produce 2CO2 in the tricarboxylic acid cycle [59], possibly stimulating photoautotrophic growth, as supposed in glucose-based mixotrophy [57]. Thus, the field investigation by Demura et al. [14] provided a feasible carbon mass balance to understand the roles of photosynthesis and organic compounds in mixotrophy.
Considering the need for a CO2 supply to enhance the photosynthetic algae, sourcing CO2 from co-located power plants and other sources introduces several technical, logistical, and scalable challenges. It could significantly hinder the practical deployment of algae culture farms in supporting fuel outputs. In addition, flue gas carbon capture and transport from point-source are very expensive and energy-intensive to enable either cost or sustainability goals for algae-based biofuel production [60]. Mixotrophic microalgae may have a high potential for solving the above bottlenecks of CO2 supply because they can utilize both atmospheric CO2 and organic carbon as a carbon source.

3.2. Polyculture

Numerous reports have demonstrated the importance of species or functional group diversity in terms of community stability and ecosystem function. Diverse communities in terrestrial and aquatic environments tend to be more resilient and resistant to perturbations due to different mechanisms, such as niche complementarity, niche differentiation, and functional redundancy [61,62,63,64,65,66]. Dzialowski and Smith [62] suggested that monocultures could be inherently unstable as many interactions are possible due to unoccupied niches. Polycultures are probably more robust to diverse perturbations because complex communities contain organisms with inherent resistance to specific optimization and various ranges of ecological and physiological resistances [67,68]. Behl et al. [69] found a positive correlation between species diversity and biomass yields in all phytoplankton. Considerable numbers of polyculture studies of microalgae have been conducted (Table 3). Most of the studies strongly suggested that polyculture outperforms the best mono-culture by performing multiple functions simultaneously, such as producing resilient communities, enabling efficient nutrient uptake and resisting population crashes and undesirable invaded species, and showing less tendency to trade-off between desirable functions [70,71,72,73,74,75], and only few reports indicated that polyculture does not outperfor m the most pro-ductive monoculture in producing biocrude oil [71] and biomass [72].
The polyculture of native algal communities has been used for algae biomass production and wastewater treatment in open ponds and bioreactors (Table 3) [14,16,17,18,19,26,27,28,76,77,78,79,80,81,82,83]. However, there is little information on the compositional dynamics of the native algal community in polyculture. Demura et al. [14] showed that, in most cases, polyculture biomass typically consists of 70–90% algae; however, the rest consists of bacteria, fungi, amoeba, ciliates, and some invertebrates. Species and taxa numbers decreased as the cultivation time increased, but productivities remained high in raceway ponds. They showed that species selection had occurred, with adapted algal species producing large amounts of biomass. In the period with decreased species and taxa diversity, “selected” native algal species may maintain stable and large biomass productivity. Desmodesmus sp. and Scenedesmus acuminatus were the dominant species. The authors provided several possible explanations for this dominance: (1) the bristles of Desmodesmus sp. cells may reduce predation pressure from small-sized predators; (2) various Scenedesmus species may inhibit the growth of other microalgae in mixed cultivations; (3) Scenedesmus and Desmodesmus show a short reproductive cycle of the coenobium, followed by the rapid formation and release of four-cell dominant coenobia over a wide temperature range, resulting in dominance over a wide temperature range. Complementary to Desmodesmus, the filamentous alga Klebsormidium sp. flourished at a cold temperature. Klebsormidium occasionally occurs in natural algal communities of wastewater ponds [84]. It has high species diversity, even in polar regions [85]. The adjustability of this genus to low temperatures may have contributed to the stable productivity of algal biomass during the winter season [14].
The performance of photosynthetic microalgae biomass production in the outdoor reactor system is mainly a function of solar radiation availability and culture depth of the reactor because light impinging on the reactor surface is attenuated along the culture depth due to an increase in algal cells in the culture [86]. Considering that fixation of nutrients by photosynthetic microalgae is a direct function of average irradiance, the shallower the culture depth, the higher the average irradiance, the higher the fixation rate of nitrogen and phosphorus, and the higher the biomass productivity. Thus, to maximize the photosynthetic microalgal biomass production and nutrient recovery from wastewater, the culture depth must be shallow, below 0.2 m [23]. This interrelationship applies for photosynthetic algae but not for mixotrophic microalgae.
Several studies have been conducted to optimize algal biomass production in polyculture with respect to depth [14,19,78]. When the seasonal algal performance in the polyculture high-rate algal ponds (HRAPs) using wastewater at three depths of 0.2, 0.3, and 0.4 m was evaluated, a 0.4 m deep HRAP resulted in 134% to 200% higher aerial productivity than a 0.2 m deep HRAP and was more efficient at NH4-N uptake [19]. However, the opposite results have been obtained [78]. The discrepancy may be caused by the differences in time, place, and algal components. Demura et al. [14] demonstrated in the mixotrophic microalgae-dominant polyculture induced by adding sodium acetate that the overall areal productivity increased significantly with increasing depth from 0.1 m to 0.8 m. Figure 1 shows that monthly algae biomass productivities in 0.8 m depth culture remained at a stable value of 24.4–32.8 g·m−2·day−1 (mean productivity 28.1 g·m−2·day−1) despite the seasonal fluctuation of temperature ranging from 7 °C in winter to 25 °C in summer and photon flux density ranging from 307 μmol·m−2·s−1 in December (winter solstice month) to 540 μmol·m−2·s−1 in May (one month before summer solstice).
However, with the biomass and biocrude-oil productivities of 0.8 m deep culture (Figure 1 and Table 3), the land area required to cover the imported amount (0.13 × 109 t) of crude oil in Japan is 3.7 million ha, which is 2.7 times larger than the total area (1.37 million ha) of the sewage treatment facility. To solve such a critical land issue, mixotrophic algae-based polyculture at a water depth of 1.4 m using primarily treated sewage has been conducted throughout the year [25]. A much higher biocrude oil productivity of more than 300 tons·ha−1·year−1 was obtained; thus, the land area required to fulfill the imported amount of crude oil is estimated to be less than 32% of the total area of sewage treatment facilities. Therefore, such a deep water-depth polyculture of mixotrophic algae combined with the wastewater treatment process can meet the current demand of crude oil in Japan.

3.3. Wastewater Treatment by Algae

The activated sludge treatment system used mostly in high-income countries has a high organic-matter removal from wastewater. The system efficiently purifies the sewage in a small area, but the operation/management costs and energy consumption are high. On the other hand, the conventional wastewater treatment pond system is cost-effective, requires little maintenance, and generally works well to remove organic solids in wastewater. However, the pond system needs a large area; it is not designed to optimize the recovery of natural resources from wastewater, such as nitrogen, phosphorus, and algae/bacterial biomass for biofuels.
HRAP systems were developed by Oswald and co-workers at the University of California, Berkeley [87]. HRAPs are shallow raceway ponds that circulate wastewater via a low-power paddle wheel. HRAPs are designed to maximize the breakdown of organic waste via algal and bacterial growth and inactivate pathogens through sunlight exposure. Based on a symbiotic relationship between bacteria and microalgae, they provided low-energy wastewater treatment and recovered nutrients as harvested algal biomass that could be used as a biofuel feedstock. Several systems are operating in northern cities in California State [3,88], Christchurch in New Zealand [17,89], and Spain [90]. Christchurch’s HRAP system of polyculture consists of a covered anaerobic pond (CAP), HRAP, algae settling and harvesting pond, mature pond (MP), and rock filter [18]. Depending on the climate, the maximum organic loading rate of HRAP is between 100 and 150 kg BOD5·ha−1·day−1. The HRAP depth depends on wastewater clarity (typically 0.2–0.6 m). In temperate climates, the hydraulic retention time varies seasonally (3–4 days in summer and 7–9 days in winter). The system was designed to treat wastewater to meet all discharge requirements for BOD, TSS, NH4-N, TN, and TP. CO2 addition doubled the biomass productivity to 16–20 g·m−2·day−1, improving effluent quality. In addition, a low level of chemical flocculants improved the effluent quality the most; for instance, the removal of TP was remarkable [18] (Table 4).
The HRAP polyculture system had high disinfection performance for fecal bacteria/viral indicator organisms and actual human pathogenic viruses from influent to final MP [89]; the removal of Escherichia coli from 106 to 102 order MPN·100 mL−1 in winter and summer; Enterococci from 107 to 102 order MPN·100 mL−1 in winter and from 107 to 104 order in summer, and fRNA from 105 to 101 order PFU·100 mL−1 in winter and summer; adenovirus from 105 to 104 order copies·100 mL−1 in winter and from 106 to 101 order copies·100 mL−1 in summer; enterovirus from 105 to 103 order copies·100 mL−1 in winter and from 105 to <101 order copies·100 mL−1 in summer; rotavirus from 105 to <101 order copies·100 mL−1 in summer. Only norovirus was not removed in winter and summer.
Thus, HRAP has a high performance in treating wastewater to meet discharge requirements, removing human pathogenic viruses and achieving high productivity of algae-dominant polyculture toward future algae-based biofuel production. However, a large area is required to treat a large amount of wastewater using the HRAP system. For example, most public sewage treatment plants in Japan treat 10,000 to 500,000 m3 of sewage daily. At least 5 ha–250 ha land areas are needed for a HRAP at a 0.2 m culture depth. Two-thirds of the islands of Japan consist of mountainous areas; the flat land is mostly occupied by cities, industrial zones, and agriculture, and it is extremely expensive to acquire. Thus, integrating wastewater treatment and algae biomass production should be developed using a system with a low land footprint in Japan and other countries with limited usable lands.
In the polyculture of the native algae community with 0.8 m water depth, BOD, TSS, TN, and TP of culture effluent without adding flocculants were reduced by 82.8%, 48.5%, 64.2%, and 32.1%, respectively. The addition of flocculants reduced these nutrients below the levels of the quality standard of discharge water based on the Sewage Act in Japan (Table 5) [26], suggesting that even 0.8 m deep algal culture efficiently purifies sewage in a small area. Developing a mixotrophic microalgae polyculture plant system with a low area-to-volume ratio would solve the above bottleneck by integrating sewage treatment and algae biomass production, resulting in low land-footprint algae-based fuel production.
Recently, numerous studies have been conducted on the performance of microalgae-activated sludge consortia treating synthetic wastewater under defined laboratory conditions [91,92,93,94,95,96,97,98,99]. Although there have been many differences in algae components, algae-activated sludge ratios, and experimental designs and conditions, the reduction rates shown under each optimal condition in these reports can be summarized as follows. The reduction efficiencies of COD, NH4-N, TN, and TP are 91.2 ± 5.0%, 95.3 ± 7.6%, 66.7 ± 27.5%, and 75.2 ± 30.5%, respectively. Despite great TN and TP removal variations due to different experimental designs and conditions, there is slight variation in the COD and NH4-N removal rates. These studies on activated sludge and algae consortium are similar to polycultures consisting of 70% to 90% algae, bacteria and other microorganisms and invertebrates. From the viewpoint of future applications to actual sewage treatment sites, these studies should be followed by an in situ pilot-scale demonstration experiment. It is worth noting that in situ pilot-scale investigations are being conducted by the Environmental Engineering team at New Mexico State University [100] and by the technology entity led by MicroBio Engineering Inc.-California Polytechnic State University [88]

4. Harvesting and Dewatering

The conversion of algal biomass from ponds or bioreactors into liquid biofuel requires processing steps, such as harvesting/dewatering, and various pathways extraction of organic matter (e.g., carbohydrates, proteins, and lipids). Harvesting is the process of separating biomass (suspended solids) from a liquid culture medium. The algae biomass concentration significantly varies from that in diluted algal culture to that in dry algal powder. The combination of small cell size (2–40 µm) and low cell density (0.3 to 5.0 g·L−1 equivalent to 0.03 to 0.5 wt% solid content) creates a significant challenge for the biomass recovery process [101]. However, to remove large volumes of water and process great quantities of algal biomass, a suitable harvesting method requires multiple steps of physical, chemical, or biological methods to perform the desired solid–liquid separation. Table 6 presents an overview of the most common dewatering technology associated with biomass concentration and energy consumption.
The selection of the harvesting technique depends on the characteristics of microalgae, e.g., the cell size, density, and value of the target products. It is also crucial to the economic production of microalgae biomass. For large-scale algae biomass production, microalgae harvesting is mainly a two-stage process (Figure 2) and accounts for 20–30% of the total production costs, excluding drying costs [106]. Removing free bulk water from suspended solids at low solid concentrations requires less energy than the relatively small amount of the remaining water (sometimes refers to moisture content) after mechanical dewatering force (Figure 2). Thermal energy is required to remove moisture from the concentrated wet algae paste, and when derived from fossil fuels, the impact on GHG emissions is notably high.
The reduction of energy consumption to combine dewatering by flocculation and mechanical force (two-stage process) has been recognized as the most energy-efficient methodology [104]. It has been demonstrated that large-scale and effective methods for drying biomass incur prohibitive energy costs [111]. In contrast, with processing methods for wet biomass (up to about 20% solids), transport becomes prohibitively expensive, and on-site processing is required. The “Carnegie Project”, which was pioneered from the great achievements during the first conceptualization of algae mass culture, was the supplementation, or even replacement, of algae biomass to animal protein for direct consumption by humans [112]. Based on this project, the classic book edited by Burlew in 1953 [113] on microalgae mass cultivation was written, summarizing many early studies on microalgae. Since then, considerable efforts have been made to improve the efficiency of the economics of large-scale microalgae harvesting and processing. These achievements have been reported and discussed extensively in the literature [102,105,108,114,115]. In this section, we will focus on the processing methods eligible for subsequent HTL and reasonable algal biofuel life cycle assessments. The most common thickening and dewatering methods include sedimentation, filtration, and centrifugation.

4.1. Sedimentation

Sedimentation is the simplest step in liquid–solid separation by gravity, with low power consumption and a simple design but low solid concentration output and a large area footprint requirement. A large area is required for the lamellar settler, where the distance for settling particles is shortening. This method is suggested for separating algae cultures, and it is used in wastewater treatment [108]. However, sedimentation, as described by Stokes’ law, and sedimentation rates are affected by the cell size, cell density, cell motility, and water turbulence. For example, the average solid content of 1.6% with Coelastrum proboscideum was obtained, which is sufficient for pre-concentration [102]. Unlike filamentous algae, unicellular microalgae are small in size and do not settle naturally under normal growth conditions.
As mentioned above, flocculation is an essential step for microalgae-based wastewater treatment to meet discharge requirements [18,26]. Flocculation has been used as a step-in addition to or in combination with flocculation–flotation, to increase the particle size of microalgal cells and improve the efficiency of sedimentation, centrifugation, and filtration. The flocculation method is used to separate the biomass from the bulk suspension. The concentration factors for this method are typically 100–800 times to achieve 2–8% total solid matter [104]. Flocculation describes the formation of cells into aggregates to increase the effective particle size using various methods.
  • Flocculation by inorganic chemicals
  • Flocculation by organic chemicals
  • Bio-flocculation
  • Auto-flocculation
  • Ultrasound and Electro-flocculation/flotation
In this subsection, we consider the most proven techniques, such as flocculation, using inorganic and organic chemicals. Flocculation sometimes refers to the term coagulation, which describes the aggregation resulting from pH adjustment or electrolyte addition; however, aggregation because of polymer addition is termed flocculation [116]. As mentioned above, during algae biomass cultivation, the negative charge of microalgae cells prevents cell aggregation in a suspension. However, the surface charge can be neutralized or reduced by adding flocculants, such as multivalent cations and cationic polymers. The flocculants should be inexpensive, non-toxic, and effective at low concentrations; they should also be selected with no regard for downstream processes [106]. Metal ions, such as Al+3, Fe+3, and Mg+2, are used mainly as inorganic chemicals that form hydrates at suitable pH. Lime (Ca(OH)2) is commonly used in water and wastewater treatment for pH adjustment. The most effective metal salt was aluminum sulfate; however, it is expensive in large amounts [117].
Polymeric organic flocculants are an alternative to inorganic chemicals, such as metal salts (polyelectrolytes). Polyelectrolytes have the advantage of producing a three-dimensional matrix for more stable flocks because of their reduced surface charge and physically bridging algal cells and polymer chains. The efficiency is increased by high-molecular-weight polymers and a low pH [118,119]. The most well-known polyelectrolytes with a long history for commercial applications are chitosan, Zetag63, Zetag92, and N-100 [120]. Organic flocculants have a lower toxicity risk, which is a significant advantage. However, Udom et al. [121] found that ferric chloride and alum have significantly lower GHG emissions, with 10 kg CO2-e·ton−1 dry algae and 62 kg CO2 -e·ton−1 dry algae, respectively, than 110 kg CO2-e·ton−1 dry algae for polymers.

4.2. Filtration

Filtration is one of the most promising processes for solid–solid or liquid–solid separation. The filtration principle introduces particles into a filter mesh with a specific pore size [108]. Compared with the operating principle of a centrifuge, which relies mainly on centrifugal force and the specific gravity of the solid, filtration is based on the separation of solid from liquid through the pore size of the filter mesh, which is dictated by the particle size of the aggregated algae cells. Filtration systems have been developed with driving forces such as gravity, centrifugal, pressure, or vacuum [102]. A solid concentration of 27 wt% has been achieved using a chamber filter press with an estimated energy consumption of 0.88 kWh·m−3 and a micro strainer with the lowest energy consumption of 0.2 kWh·m−3 and a solid concentration of 1.5%. A pre-coated filter with potato starch for a vacuum drum filter achieved a solid concentration of 37% [102]. Recently, a research group in the Netherlands conducted a techno-economical evaluation of algae harvesting and dehydration considering a 100 ha scale [104]. Consequently, harvest and dehydration with the lowest cost and high energy efficiency combined coagulation precipitation with chitosan―pressure filtration. The cost and energy consumption were calculated to be EUR 0.36·kg−1 dry algae and 0.03 kWh·kg−1 dry algae, respectively. Similar results for GHG emissions have been reported by Udom et al. [121] with 5.0 kg CO2-e·ton−1 dry algae for belt press technology compared to 50 kg CO2-e·ton−1 dry algae for centrifugation. The combination of energy-efficient filtration technologies and high-efficiency sedimentation using flocculation will significantly reduce the carbon footprint for algae biofuel production.

4.3. Centrifugation

Centrifugation is a sedimentation process with enhanced gravitational force to increase the sedimentation rate within a chamber, allowing easier solid movement through a liquid [122]. The centrifugal separation process has been investigated for almost all types of microalgae, with high value metabolites and algae concentrate for hatcheries and nurseries in aquaculture [101,108]. Centrifugation is a rapid process whose biomass recovery depends on the slurry residence time in the centrifuge and settling distance. The different types of centrifuges cover a wide range of particle sizes (from 10−3 to 104 µm) [122]; however, not all types of centrifuges are suitable for continuous operation. A few centrifuges, e.g., nozzle centrifuge, screw centrifuge, and self-cleaning plate separator, are used at industrial scales; they can achieve a solid content of about 15 wt%. High energy demand and a high level of maintenance have been recognized as a disadvantage for centrifuge application. In contrast, decanter-type centrifuges are the most promising because they can operate continuously and have high capacity and lower maintenance requirements [123].

5. Conversion of Algae Biomass into Bio-Crude Oil through HTL

The following is a summary of the advantages of hydrothermal liquefaction technology:
  • Robust and reliable: can be applied to wide range of carbon rich feedstocks at similar processing conditions.
  • Conceptually simple (feed preparation, pump, heated pipe, separation of biocrude).
  • Wet feedstocks with 70–90% moisture such as microalgae biomass, agriculture residues, sludge, manure, and pulp mill residue can be processed.
  • The HTL biocrude oil is thermally stable and can be readily upgraded.
  • High carbon efficiency of product: greater than 50% carbon conversion from the feedstock to hydrocarbon fuel product.
  • Favorably comparable in economics with other biomass conversion technologies such as pyrolysis.
A large number of laboratory and pilot investigations on HTL have been reported trialing different feedstocks, reactor configurations, and catalysts to improve the product quality and yields [124,125,126,127,128,129]. Some HTL technologies have now matured and moved into commercial production by various companies in different countries such as Silva Green Fuel (Norway), Altaca Energy (Turkey), and Licella Pty Ltd. (Australia). The biocrude oils produced are used as fuel for heating or for co-processing in petroleum refineries. In most cases, co-products such as electricity, hydrocarbon gases, and green chemicals are also produced that improve the technology economics.
In this section, an availability of HTL methods for algal polycultures, including a deep water-depth polyculture of mixotrophic algae, is evaluated from the viewpoint of biocrude-oil yield and composition.
Developments on catalytic hydroprocessing technologies of biomass-derived liquefaction conversion products have usually been referred to as biocrude or bio-oil for almost four decades [130]. Over this period, the development of HTL has been broadened in subcritical conditions with and without catalysts, supercritical conditions, and a two-stage conversion process for the simultaneous extraction of value-added co-products such as carbohydrates and proteins [4]. The two-stage conversion process was mainly developed for macroalgae as a potential feedstock for biocrude-oil production. However, HTL is a promising technology widely used under subcritical reaction conditions of 250 °C to 374 °C and 5 to 25 MPa pressure at different reaction times between 5 and 60 min [131,132] to produce biocrude and bio-based chemicals [133,134].
HTL is a water-based process; it is therefore suitable for the carbon-rich matter at high moisture contents of about 80 wt%. The process replicates the formation of conventional hydrocarbons found in fossil crude oil by converting macromolecules to smaller molecules and reforming them to hydrocarbon products through a series of hydrolysis, depolymerization, and re-polymerization reactions [124,135]. Microalgae can be readily converted into transportation liquid fuels and chemicals using advanced thermal conversion technologies such as HTL [130]. The main products of the HTL process are categorized as follows [136]:
  • Biocrude oil―the primary product: it has properties similar to conventional petroleum.
  • Solid residues: it is used as a soil amendment for agricultural applications.
  • Aqueous phase: it contains essential nutrients including phosphorus that can be used to cultivate algae or other biomass resources. Alternatively, the remaining carbon content in the aqueous phase can produce synthetic natural gas by gasification or methane by anaerobic digestion.
  • Gas phase, which contains more than 90% of CO2 and trace amounts of hydrocarbon gases (CH4, C2H4, and C2H6).
It has been reported that the biocrude-oil yields and compositions obtained through HTL for numerous monoalgal-species are 18% to 87.2% in yield, 5.9% to 36.5% in ash content, 0.9% to 9.8% in N content, and 0.18% to 1.4% in sulfur content (except for Porphyridium, growing in high sulfur conditions at hot springs) [4,127]. Table 3 shows that polycultures of algae using sewage result in an HTL biocrude yield and quality [16,27,70,71,74,78,82,83] that matches the average monoculture. However, Goswami et al. [83] reported that the biocrude-oil yield obtained from algae–bacteria consortium is 39% lower than that of mixed microalgae culture [76]. They suggested that such an inferior yield might be due to the un-optimized process parameters and quality of the biomass stocks [83].
Importantly, HTL avoids the intensive energy required for drying feedstocks, as in the other thermochemical reaction technologies, such as gasification and pyrolysis [137,138]. It is worth noting that fossil crude oil is pumped from the ground at 10% oil and 90% water containing impurities, such as gases (CO2, H2S, and natural gas), minerals, and sand, requiring several pre-treatment steps before being transferred to the refinery. After removing gases and minerals, the water is removed through distillation, leaving only 2% of water in the fossil crude. Due to the limitation at the laboratory scale, few of these process steps have been applied for biocrude-oil production through HTL.
The energy efficiency of HTL technology is determined primarily by the thermodynamic properties of water, along with efficient heat recovery in a well-engineered reactor system and further process integration. The energy demand for the HTL process is dominated by the energy demand for heating the reactor with 6.51 MJ·kg−1 dry algae; this has been predicted to be slightly decreased at the industrial scale. The reasons for the slight decrease are the implementation of heat recovery and the combustion of process gases with the increased volume per unit and reduced heat transfer due to material thickness. The biocrude oils and gases produced through HTL were experimentally determined to have a high heating value of 34 and approximately 1.1 MJ·kg−1, respectively. However, one of the major challenges of the HTL process is the presence of undesirable heteroatoms in biocrude oil [124,139], such as nitrogen, oxygen, and sulfur, which are derived from proteins, carbohydrates, and lipids in the biomass feedstock. The presence of these hetero-atoms requires further upgrading/refining processes, such as hydrotreatment, followed by distillation, which significantly increases the GHG emission reported by Fortier et al. [140].
Furthermore, it is worth noting that, for more than half a century, oil refineries have been producing a wide range of chemicals from any quality of crude oil, including transportation fuels. These refineries can also remove oxygen, nitrogen, and sulfur from low quality crude oil using hydrogenation, hydro-denitrogenation, and hydro-sulfurization devices. The employed technology enables the refinement of various transportation fuels from crude oil of any quality. However, only crude oil cannot be created using them. It is required to reduce the biocrude-oil production cost so that the oil refineries can acquire it at economical feasible price.

6. Life-Cycle Assessment (LCA) of Microalgae-Based Biofuel Production

Currently, there are various pathways for biofuel production from biomass feedstock available. Three generations of biofuels such as bioethanol, biodiesel, and biocrude oil through HTL have been considered in this study. For adequate comparison of various biofuels, the well-to-wheel (WTW) perimeter was applied. WTW includes crop cultivation, harvesting, conditioning, transformation of the crop into biofuel, transportation, and its final use in a vehicle engine. However, the two other perimeters such as well-to-gate (WTG, including crop cultivation, harvesting, conditioning and transformation of the crop into biofuel) and well-to-tank (WTT, also known as well-to-pump, including crop cultivation, harvesting, conditioning, transformation of the crop into biofuel, and transportation to a gas station) have been widely used in the literature [141]. Frank et al. [142] presented a lipid extraction process model of hypothetical wet hexane extraction combined with anaerobic digestion for methane co-production and nutrient recovery. The GHG footprint outcome was 55,400 g CO2-e·mmBtu−1 (about 52.5 g CO2-e·MJ−1) renewable diesel output. These numbers were later updated [143] to 21,500 g CO2-e·mmBtu−1 (about 20.4 g CO2-e·MJ−1); however, an HTL pathway was also added to greenhouse gases, regulated emissions, and energy use in technologies (GREET) model at 31,000 g CO2-e·mmBtu−1 (about 29.4 g CO2-e·MJ−1). It is worth noting that these values represent hypothetical projections potentially achievable in optimized systems but have not been demonstrated to date. This is important as it indicates good potential for process improvements in the future. However, the modeled aspects used from GREET for resource acquisition, fuel conversion, and pump-to-wheel scenarios are based on mature technology and processes with values at a high level of confidence.
When comparing the major process steps between biodiesel production and biocrude oil production from microalgae (Table 7), there are differences in the biomass production process and downstream process. Biodiesel production from microalgae relies on monoculture cultivation and high lipid productivities. These conditions require the usage of fertilizer and shallow ponds at large area footprints. Both requirements have led to higher CO2 emission vales compared with the proposed deep-water polyculture system for wastewater treatment. Furthermore, the drying process of the biomass for the biodiesel production results in higher CO2 emissions compared with the downstream process required for the HTL conversion. Table 7 summaries the main process steps for the comparison between biodiesel production and biocrude oil production from microalgae, and the values clearly indicate the benefit of the application of HTL for biocrude oil production, producing lower CO2 emissions due to the unnecessity of the drying process and fertilizer.
Figure 3 summarizes the most dominant assessments for biofuel production from microalgae, illustrating the range of life cycle assessment (LCA) outcomes for GHG emission footprints prepared by various research groups [140,142,143,146,148,149,150]. This figure demonstrates that the conventional dry microalgae extraction models have excessively high energy consumption; thus, the drying is not part of the dewatering process. More modern systems are wet extraction, HTL, or secretion based, and whether focused on renewable diesel or jet fuel, they have favorable GHG emissions relative to conventional low-sulfur diesel (dotted line) at about 96 g CO2-e·MJ−1 fuel and about 88 g CO2-eq·MJ−1 (dashed line) for conventional jet fuel. However, the GHG emission value for refined jet fuel obtained from HTL biocrude oil increased to twice that of HTL biocrude oil due to removing undesirable heteroatoms.
Given that these values are based on hypothetical models instead of data from industrial production plants, there is a possibility that some values are reported with assumptions about the potential for promising results derived from theoretically optimized systems. However, except for the conventional dry extraction method, most renewable algae fuel production systems showed favorable GHG emissions that were lower than those of conventional diesel and jet fuel (also for ultra-low sulfur diesel). Large microalgae production systems with a massive area footprint should be located on land of low agricultural value (land of low carbon capture capacity), benefiting their potential for biofuel production. The reason is that the effects of land-use change on GHG emissions would be substantial. When land-use change is considered, there is a significant effect on the LCA outcomes of corn ethanol production in the United States of America, according to Tyner et al. [151]. For instance, the GHG footprint for renewable diesel from hydro-treated palm oil (about 30 g CO2-e·MJ−1) is almost as low as the best algae case without considering the land change. However, when the land-use change to areas such as peatland rainforest clearings in southeast Asia is considered, the value is dramatically higher (about 705 g CO2-e·MJ−1), almost an order of magnitude greater than conventional diesel from fossil sources [148].
The total net energy-gain value for biocrude oil and its co-products is higher than that for biodiesel and its co-products because the energy loss through the biodiesel production is higher compared to the biocrude oil production (Table 7). In addition, the reported high lipid content of microalgae for the potential production of biodiesel production represents the amount of total lipids but not the amount of FAME (C16 and C18) suitable for the transesterification process. Further loss of extracted lipids has been recognized for various cell lyses methods and large-scale extraction applications. These losses on extracted lipids will greatly impact the energy-gain value for the biodiesel pathway produced from 1 Kg microalgae biomass.
Figure 4 shows the comparison between EROIs of fossil fuels, first and second generation of biofuel pathway from biomass feedstocks, and HTL biocrude oil from algae. It was clearly demonstrated that EROI of algae HTL biocrude oil is much higher than fossil fuels and comparable to the other biodiesel and bioethanol plants.
Collectively, it is suggested that algae HTL biocrude oil has higher sustainability relative to the conventional liquid fuels and other biofuels, such as bioethanol and biodiesel, for combining GHG and EROI (Figure 3 and Figure 4, Table 7). Thus, in addition to the advantages of HTL of biomass to biofuel as mentioned in Section 1 and Section 5, HTL is advantageous also from the sustainability viewpoint.
Table 3 shows that polyculture outperforms the best monoculture by performing multiple functions simultaneously. A WTW-LCA that analyzed the impact of algal biodiversity on biofuel production showed that certain polycultures improved GHG and EROI by 16% and 20%, respectively, compared to the best monoculture [75]. It has also been suggested that in a 0.8 m depth polyculture of microalgae, based on 86% heat recovery in the HTL process previously reported, WTG-LCA of combining algae biomass/biocrude-oil production and wastewater treatment reduced the CO2 emissions of the conventional wastewater treatment system by 33% [8]. Thus, the benefits for reduced CO2 emission and increased net energy-gain are clearly demonstrated for the proposed biocrude oil production by HTL employing the polyculture system for wastewater treatment.
For the past few decades, especially since 2007, microalgae have been attracting significant attention as a promising source of sustainable biofuels. It tackled major challenges in optimizing upstream and downstream processes for algae fuel production and its practical application. In the harmonized model of the National Renewable Energy Laboratory (NERL), given annual productions of microalgae of 86.8 to 105.4 tons·ha−1 (freshwater algae: FA) and 87.8 to 100.1 tons·ha−1 (saltwater algae: SA) in the cultivation area of 5000 acres (=2025 ha) and 50% of biocrude oil conversion rate through HTL, the minimum fuel sales prices (MFSP) were calculated to be 3.48 to 3.68 $·GGE−1 (gallon gasoline equivalent) and 4.31 to 4.53 $·GGE−1, respectively. In addition, tax incentives have been expanded to include carbon credits for CO2 of $ 35 per ton in the US. Applying this credit to some CO2 incorporated into algal biomass, the MFSP would further reduce to 0.24 $·GGE−1 for FA and 0.23 $·GGE−1 for SA [60], much cheaper than that of fossil biocrude oil. This model suggests that algae fuel production is economically feasible combined with carbon credits that promote the realization of a low-carbon society. Ishizaki et al. [8] suggested that a 0.8- m depth polyculture-based wastewater treatment had the same cost-effectiveness as the conventional wastewater treatment, even though the resulting biocrude oil was sold at the same price as fossil crude oil. Thus, further reduction of MFST can be expected by introducing a combination of algae and sewage treatment to the NERL model. However, it has been suggested that algae fuel production alone is not economically feasible and must be combined with other useful by-products. Such a bio-refinery model seems attractive if the significant differences in the size of each market and production standards for feedstock produced for each product can be adjusted well.
It is widely acknowledged that LCA and techno-economic models of complex systems contain many uncertain aspects, as evidenced by the wide range of values observed in the literature when different assumptions are used. There are various scenarios for the economic feasibility of algal fuel and products. Nevertheless, not all of them have been demonstrated, which provide plausible paths to achieve future targets for cost and sustainability metrics. The model outputs still indicate a promising potential for algal biofuels to significantly contribute to the world fuel market. It is essential to accumulate and use real field data to properly validate these models in the future.

7. Conclusions

It is commonly recognized that integrating wastewater treatment and microalgae biomass production has multiple benefits, including the circular use of freshwater, reducing the biofuel production cost, and mitigating the impact of contaminated water on the living environment and ecosystems. To realize such benefits, it is necessary to consider how to increase the microalgae production and wastewater treatment capacities. This review highlighted the following:
  • Mixotrophic algae play a significant role in reducing COD/BOD in wastewater such as heterotrophic microbes.
  • Mixotrophic algae have a high potential for solving the bottlenecks of CO2 supply because they can utilize atmospheric CO2 and organic carbon as a carbon source.
  • Mixotrophic algae enable deep water culture, which significantly increases the capacities of aerial productivity of biomass/biocrude oil and wastewater treatment and reduces their land footprints.
  • Polyculture outperforms the best monoculture by performing multiple functions simultaneously, such as producing resilient communities, enabling efficient nutrient uptake, resisting population crashes and undesirable invasive species, and showing fewer tendencies to trade-off between desirable functions.
  • Energy-efficient filtration technologies combined with high-efficiency sedimentation through flocculation will significantly reduce the carbon footprint for algae biofuel production.
  • Algal polycultures using sewage have HTL biocrude oil with a yield and quality that match the average monoculture-derived biocrude oil; it is available for existing oil refineries.
  • HTL has bioavailability of the recycled nitrogen and phosphorus from the aqueous phase.
  • HTL biocrude oil is more sustainable than conventional liquid fuels and other biofuels for combining GHG and EROI.
  • Polyculture has the potential to improve the GHG and EROI significantly, compared with the best monoculture.
Thus, integrating mixotrophic algae polyculture and wastewater treatment processes simultaneously increase microalgae biomass production and wastewater treatment capacities with a low land footprint and high robustness to perturbations. The upgraded upstream process will bring about high efficiency and low carbon footprint in the downstream process. In particular, deep water-depth polyculture of mixotrophic microalgae using sewage has a high potential to produce sustainable biocrude oil within the land area of existing sewage treatment plants to fulfil of the Japanese crude oil demand. Figure 5 shows the diagram of the entire process.

8. Future Perspective

As mentioned in the Introduction section, the overall economics for the HTL algal pathway are more strongly influenced by improvements in algae biomass productivity [24]. Therefore, it is essential to secure stable and high algal biomass production for the efficient production of HTL biocrude oil. Deep water-depth polyculture of mixotrophic algae combined with wastewater treatment processing is the most promising way to fulfil this requirement.
It is worth noting that there are multiple approaches for selecting productive polycultures, ranging from synthetic polycultures using carefully selected laboratory strains to naturally occurring polycultures, as shown in Table 3. In the study of Demura et al. [14], the deep water-depth polyculture of mixotrophic algae was composed of native mixotrophic algae population. Thomas et al. [81] provided evidence that the native polyculture maintained higher diversity than the synthetic polyculture, enhancing the biomass productivity and nutrient removal. The differences became more pronounced under the grazing and resource stress conditions. However, they also suggested that the results should be interpreted as those of one pilot-scale empirical example; they could not infer whether natural or synthetic polycultures perform better in general. Various types of synthetic mixotrophic algae polycultures with functional complementarity should be constructed and tested on their capacities from various ecological aspects against native mixotrophic algae polycultures. This will be required for selecting more appropriate mixotrophic polycultures for biocrude-oil production.

Author Contributions

Writing—Section 1, Section 2 and Section 3, Section 7 and Section 8, and editing, M.M.W.; Writing―Section 4, Section 5 and Section 6, A.I. All authors have read and agreed to the published version of the manuscript.


This work was supported by “Next Generation Renewable Energy Technology Development Project” of Fukushima Prefecture, Japan (FY2013-FY2015), “R&D Project for Biofuel Production Using Algae” of Agency for Natural Resources and Energy, Ministry of Economy, Trade, and Industry, Japan (FY2016-FY2018), and “Low Carbon Technology Research, Development and Demonstration Program” of Ministry of Environment, Japan (FY2017-FY2020), each of which was conducted as a part of “Algae Biomass Energy R&D Program, Tsukuba International Strategic Zone” of the Cabinet Office, Japanese Government.

Institutional Review Board Statement

Not applicable.

Informed Consent Statement

Not applicable.

Data Availability Statement

Not applicable.

Conflicts of Interest

The authors declare no conflict of interest.


  1. Chisti, Y. Biodiesel from microalgae. Biotechnol. Adv. 2007, 25, 294–306. [Google Scholar] [CrossRef] [PubMed]
  2. Henry, R.J. Evaluation of plant biomass resources available for replacement of fossil oil. Plant Biotechnol. J. 2010, 8, 288–293. [Google Scholar] [CrossRef] [PubMed][Green Version]
  3. Lundquist, T.J.; Woertz, I.C.; Quinn, N.W.T.; Benemann, J.R. A Realistic Technology and Engineering Assessment of Algae Biofuel Production; Energy Biosciences Institute, University of California: Berkeley, CA, USA, 2010. [Google Scholar]
  4. Gu, X.; Martinez-Fernandez, J.S.; Pang, N.; Fu, X.; Chen, S. Recent development of hydrothermal liquefaction for algal biorefinery. Renew. Sustain. Energy Rev. 2020, 121, 109707. [Google Scholar] [CrossRef]
  5. Wibawa, D.S.; Nasition, M.A.; Noguchi, R.; Ahamed, T.; Demura, M.; Watanabe, M.M. Microalgae oil production: A downstream approach to energy requirements for the Minamisoma pilot plant. Energies 2018, 11, 521. [Google Scholar] [CrossRef][Green Version]
  6. Sasongko, N.A.; Noguchi, R.; Ito, J.; Demura, M.; Ichikawa, S.; Nakajima, M.; Watanabe, M.M. Engineering study of a pilot scale process plant for microalgae-oil production utilizing municipal wastewater and flue gases: Fukushima pilot plant. Energies 2018, 11, 1693. [Google Scholar] [CrossRef][Green Version]
  7. Ishizaki, R.; Noguchi, R.; Putra, A.S.; Ichikawa, S.; Ahamed, T.; Watanabe, M.M. Reduction in energy requirement and CO2 emission for microalgae oil production using wastewater. Energies 2020, 13, 1641. [Google Scholar] [CrossRef][Green Version]
  8. Ishizaki, R.; Putra, A.S.; Ichikawa, S.; Ahamed, T.; Watanabe, M.M.; Noguchi, R. Microalgae oil production using wastewater in Japan-Introducing operational cost function for sustainable management of WWTP. Energies 2020, 13, 5310. [Google Scholar] [CrossRef]
  9. Cui, Z.; Cheng, F.; Jarvis, J.M.; Brewer, C.E.; Jena, U. Roles of co-solvent in hydrothermal liqauefaction of low-lipid, high protein algae. Bioresour. Technol. 2020, 123454. [Google Scholar] [CrossRef]
  10. Lu, J.; Zhang, Z.; Zhang, L.; Fan, G.; Wu, Y. Catalytic hydrothermal liquefaction of microalgae over different biochars. Catal. Commun. 2021, 149, 106236. [Google Scholar] [CrossRef]
  11. Hamilton, C.E.; Rosmeissl, N. Exploring the Utilization of Complex Algal Communities to Address Algal Pond Crash and Increase Annual Biomass Production for Algal Biofuels; U.S. Department of Energy, Energy Efficiency & Renewable Energy: Washington, DC, USA, 2014.
  12. Lam, M.K.; Lee, K.T. Microalgae biofuels: A critical review of issues, problems and the way forward. Biotechnol. Adv. 2012, 30, 673–690. [Google Scholar] [CrossRef]
  13. Dalrymple, O.K.; Halfhide, T.; Udom, I.; Gilles, B.; Wolan, J.; Zhang, Q.; Ergas, S. Wastewater use in algae production for generation of renewable resources: A review and preliminary results. Aquat. Biosyst. 2013, 9, 2. [Google Scholar] [CrossRef][Green Version]
  14. Demura, M.; Yoshida, M.; Yokoyama, A.; Ito, J.; Kobayashi, H.; Kayano, S.; Tamangawa, T.; Watanobe, M.; Date, N.; Osada, M.; et al. Biomass productivity of native algal communities in Minamisoma city, Fukushima Prefecture, Japan. Algal Res. 2018, 29, 22–35. [Google Scholar] [CrossRef]
  15. Chen, G.; Zhao, L.; Qi, Y. Enhancing the productivity of microalgae cultivated in wastewater toward biofuel production: A critical review. Appl. Energy 2015, 137, 282–291. [Google Scholar] [CrossRef]
  16. Craggs, R.; Sutherland, D.; Campbell, H. Hectare-scale demonstration of high rate algal ponds for enhanced wastewater treatment and biofuel production. J. Appl. Phycol. 2012, 24, 329–337. [Google Scholar] [CrossRef]
  17. Craggs, R.J.; Lundqusit, T.J.; Benemann, J.R. Wastewater treatment and algal biofuel production. In Algae for Biofuels and Energy; Borowitzka, M.A., Moheimanii, N.R., Eds.; Springer: Dordrecht, The Netherlands, 2013; pp. 153–163. [Google Scholar]
  18. Craggs, R.; Park, J.; Heubeck, S.; Sutherland, D. High rate algal pond systems for low-energy wastewater treatment, nutrient recovery and energy production. N. Z. J. Bot. 2014, 52, 60–73. [Google Scholar] [CrossRef]
  19. Sutherland, D.L.; Turnbull, M.H.; Craggs, R.J. Increased pond depth improve algal productivity and nutrient removal in wastewater treatment high rate algal ponds. Water Res. 2014, 2014, 271–281. [Google Scholar] [CrossRef]
  20. Mehrabadi, A.; Craggs, R.; Farid, M.M. Wastewater treatment high rate algal ponds (WWT HRAP) for low-cost biofuel producton. Bioresour. Technol. 2015, 184, 202–214. [Google Scholar] [CrossRef]
  21. Sheehan, J.; Dunahay, T.; Benemann, J.; Roessler, P. A Look Back at the U.S. Department of Energy’s Aquatic Species Program-Biodiesel from Algae; NERL/TP-580-24190; National Renewable Energy Laboratory: Golden, CO, USA, 1998. [Google Scholar]
  22. Acién, F.G.; Gómez-Serrano, C.; Morales-Amaral, M.M.; Fernández-Sevilla, J.M.; Mollina-Grima, E. Wastewater treatment using microalgae: How realistic a contribution night it be to significant urban wastewater treatment? Appl. Microbiol. Botechnol. 2016, 100, 9013–9022. [Google Scholar] [CrossRef]
  23. Acién Fernández, F.G.; Gómez-Serrano, C.; Fernández-Sevilla, J.M. Recovery of nutrients from wastewaters using microalgae. Front. Sustain. Food Syst. 2018, 2, 59. [Google Scholar] [CrossRef][Green Version]
  24. Biddy, M.; Davis, R.; Jones, S.; Zhu, Y. Whole Algae Hydrothermal Liquefaction Technology Pathway; Technical Report NREL/TP-5100-58051, PNNL-22314; U.S. Department of Commerce National Technical Information Service: Springfield, VA, USA, 2013.
  25. Isdepsky, A.; Gotoh, H.A.; Watanabe, S.; Watanabe, M.M. Extraordinarily High Areal Production of Mixotrophic Microalgae in 1.4 m Water-Depth Culture Tank Using Primarily-Treated Wastewater. Partly in: Annual Report of Development of Low Carbon Technologies Based on Collaboration between Efficient Productions of Algae Biomass and Their Conversions to High Performance Plastics, Low Carbon Technology Research, Development and Demonstration Program, Ministry of Environment, Tokyo Japan. 2019. Available online: (accessed on 22 October 2021). (In Japanese)
  26. AIIC (Algae Industry Incubation Consortium Japan). Annual Report on R&D Project for Biofuel Production Using Algae; Agency for Natural Resources and Energy, Ministry of Economy, Trade, and Industry (METI): Tokyo, Japan, 2019; pp. 1–140. (In Japanese)
  27. AIIC (Algae Industry Incubation Consortium Japan). Annual Report on R&D Project for Biofuel Production Using Indigenous Algae; Next Generation Renewable Energy Technology Development Project: Fukushima, Japan, 2016. (In Japanese) [Google Scholar]
  28. Ichikawa, S.; Jain, A.; Gohara, T.; Matsumoto, S.; Aramaki, T.; Ito, J.; Noguchi, R.; Watanabe, M.M.; Nakajima, M. Continuous biocrude production from polycultured microalgae biomass using a bench-scale hydrothermal tubular reactor. In Proceedings of the 7th Conference of International Society for Applied Phycology (ISAP2020–2021 Virtual), Virtual, 14 May–13 August 2021. [Google Scholar]
  29. WWAP (World Water Assessment Program). The United Nations World Water Development Report 2017, Wastewater: The Untapped Resource; UNESCO: Paris, France, 2017. [Google Scholar]
  30. Sato, T.; Qadir, M.; Yamamoto, S.; Endo, T.; Zahoor, A. Global, reginal, and country level need for data on wastewater generation, treatment, and use. Agric. Water Manag. 2013, 130, 1–13. [Google Scholar] [CrossRef]
  31. WWAP (World Water Assessment Program). The United Nations World Water Development Report 2012, Managing Water under Uncertainty and Risk; UNESCO: Paris, France, 2012. [Google Scholar]
  32. Ministry of Land, Infrastructure, Transport and Tourism (MLIT). Survey for Formulating a Comprehensive Sewerage Development Plan. for Each Basin: Guideline and Commentary; MLIT: Tokyo, Japan, 2015. Available online: (accessed on 22 October 2021). (In Japanese)
  33. Daverey, A.; Pandey, D.; Verma, P.; Verma, S.; Shah, V.; Dutta, K.; Arunachalam, K. Recent advances in energy efficient biological treatment of municipal wastewater. Bioresour. Technol. Rep. 2019, 7, 100252. [Google Scholar] [CrossRef]
  34. Magill, B. Sewage Plants Overlooked Source of CO2. Researching and Reporting the Science and Impacts of Climate Change; Climate Central: Princeton, NJ, USA, 2016; Available online: (accessed on 22 October 2021).
  35. Sewage and Wastewater Management Department and National Institute for Land and Infrastructure Management, Ministry of Land, Infrastructure (MLIT), Transport and Tourism. Sewage Technology Vision. 2021. Available online: (accessed on 22 October 2021). (In Japanese)
  36. Ministry of Land, Infrastructure, Transport and Tourism (MLIT). About Global Warming Countermeasures in the Sewerage Field. 2019. Available online: (accessed on 22 October 2021). (In Japanese)
  37. Steen, I. Phosphorus availability in the 21st century: Management of a non-renewable resource. Phosphorus Potassium 1998, 217, 25–31. [Google Scholar]
  38. Ministry of Land, Infrastructure, Transport and Tourism (MLIT). Guide to the Recycling of Phosphorus in Sewerage. 2010. Available online: (accessed on 22 October 2021). (In Japanese)
  39. De-Bashan, L.E.; Bashan, Y. Recent advances in removing phosphorus from wastewater and its future use as fertilizer (1997–2003). Water Res. 2004, 38, 4222–4246. [Google Scholar] [CrossRef] [PubMed]
  40. Hashizume, M.; Yoshida, M.; Demura, M.; Watanabe, M.M. Culture study on utilization of phosphite by green microalgae. J. Appl. Phycol. 2020, 32, 889–899. [Google Scholar] [CrossRef]
  41. Liu, Y.-J.; Gu, J.; Liu, Y. Energy self-sufficient biological municipal wastewater reclamation: Present status, challenges and solutions forward. Bioresour. Technol. 2018, 269, 513–519. [Google Scholar] [CrossRef] [PubMed]
  42. Li, L.; Kong, Z.; Xue, Y.; Wang, T.; Kato, H.; Li, Y.-Y. A comparative long-term operation using up-flow anaerobic sludge blanket (UASB) and anaerobic membrane bioreactor (AnMBR) for the upgrading of anaerobic treatment of N, N-dimethylformamide-containing wastewater. Sci. Total Environ. 2020, 699, 134370. [Google Scholar] [CrossRef] [PubMed]
  43. Yadav, G.; Shanmugam, S.; Sivaramakrishnan, R.; Kumar, D.; Mathimani, T.; Brindhadevi, K.; Pugazhendhi, A.; Rajendran, K. Mechanism and challenges behind algae as a wastewater treatment choice for bioenergy production and beyond. Fuel 2021, 285, 119093. [Google Scholar] [CrossRef]
  44. Do, M.H.; Ngo, H.H.; Guo, W.S.; Liu, Y.; Chang, S.W.; Nguyen, D.D.; Nghiem, L.D.; Ni, B.J. Challenges in the application of microbial fuel cells to wastewater treatment and energy production: A mini review. Sci. Total Environ. 2018, 639, 910–920. [Google Scholar] [CrossRef]
  45. Goto, Y.; Yoshida, N. Scaling up microbial fuel cells for treating swine wastewater. Water 2019, 11, 1803. [Google Scholar] [CrossRef][Green Version]
  46. Ma, B.; Xu, X.; Wei, Y.; Ge, C.; Peng, Y. Recent advances in controlling denitritation for achieving denitratation/anamox in mainstream wastewater treatment plants. Bioresour. Technol. 2020, 299, 122697. [Google Scholar] [CrossRef]
  47. Yoshida, M.; Tanabe, Y.; Yonezawa, N.; Watanabe, M.M. Energy innovation potential of oleaginous microalgae. Bifuels 2012, 3, 761–781. [Google Scholar] [CrossRef]
  48. Carney, L.T.; Reinsch, S.S.; Lane, P.D.; Solberg, O.D.; Jansen, L.S.; Williams, K.P.; Trent, J.D.; Lane, T.W. Microbiome analysis of a microalgal mass culture growing in municipal wastewater in a prototype OMEGA photobioreactor. Algal Res. 2014, 4, 52–61. [Google Scholar] [CrossRef]
  49. Plöhn, M.; Spain, O.; Sirin, S.; Silva, M.; Escudero-Oñate, C.; Ferrando-Climent, L.; Allahverdiyeva, Y.; Funk, C. Wastewater treatment by microalgae. Physiol. Plant. 2021, 172, 568–578. [Google Scholar] [CrossRef]
  50. Bohutskyi, P.; Spiering, R.E.; Phan, D.; Kopachevsky, A.M.; Tang, Y.; Betenbaugh, M.J.; Bouwer, E.J.; Lundquist, T.J. Bioenergy from wastewater resurces: Nutrine removal, productivity and sttleabilitynof indigenous algal-bacteria polyculture, an effect of biomass composition variability on methane production kinetics and anaerobic digestion energy balance. Algal. Res. 2018, 36, 217–228. [Google Scholar] [CrossRef]
  51. Zhang, T.-U.; Wu, Y.-H.; Zhuang, L.-L.; Wang, X.-X.; Hu, H.-Y. Screening heterotrophic microalgal strains by using the Biolog method for biofuel production from organic wastewater. Algal Res. 2014, 6, 175–179. [Google Scholar]
  52. Godrijan, J.; Drapeau, D.; Balch, W.M. Mixotrophc uptake of organic compounds by coccolithophores. Limnol. Oceanogr. 2020, 65, 1410–1421. [Google Scholar] [CrossRef]
  53. Girard, J.-M.; Roy, M.-L.; Hafsa, M.B.; Gagnon, J.; Faucheux, N.; Heitz, M.; Tremblay, R.; Deschênes, J.-S. Mixotrophic cultivation of green microalgae Scenedesmus obliquus on cheese whey permeate for biodiesel production. Algal Res. 2014, 5, 241–248. [Google Scholar] [CrossRef]
  54. Ji, Y.; Hu, W.; Li, X.; Ma, G.; Song, M.; Pei, H. Mixotrophic growth and biochemical analysis of Chlorella vulgaris cultivated with diluted monosodium glutamate wastewater. Bioresour. Technol. 2014, 152, 471–476. [Google Scholar] [CrossRef]
  55. Park, W.-K.; Moon, M.; Kwak, M.-S.; Jeon, S.; Choi, G.-G.; Yang, J.-W.; Lee, B. Use of orange peel extract for mixotrophic cultivation of Chlorella vulgaris: Increased production of biomass and FAMEs. Bioresour. Technol. 2014, 171, 343–349. [Google Scholar] [CrossRef]
  56. Moreno-Garcia, L.; Adjallé, K.; Barnabé, S.; Raghavan, G.S.V. Microalgae biomass production for a biorefinery system: Recent advances and the way toward sustainability. Renew. Sustain. Energy Rev. 2017, 76, 493–506. [Google Scholar] [CrossRef]
  57. Villarejo, A.; Orús, M.I.; Martínez, F. Coordination of photosynthetic and respiratory metabolism in Chlorella vulgaris UAM 101 in the light. Physiol. Plant. 1995, 94, 680–686. [Google Scholar] [CrossRef]
  58. Liang, Y.; Sarkany, N.; Cui, Y. Biomass and lipid productivities of Chlorella vulgaris under autotrophic, heterotrophic and mixotrophic growth conditions. Biotechnol. Lett. 2009, 31, 1043–1049. [Google Scholar] [CrossRef]
  59. Perez-Garcia, O.; Escalante, F.M.E.; de-Bashan, L.E.; Bashan, Y. Heterotrophic cultures of microalgae: Metabolism and potential products. Water Res. 2011, 45, 11–36. [Google Scholar] [CrossRef]
  60. Davis, R.; Markham, J.N.; Kinchin, C.M.; Canter, C.; Han, J.; Li, Q.; Coleman, A.; Wigmosta, M.; Zhu, Y. 2017 Algae Harmonization Study: Evaluating the Potential for Future Algal Biofuel Costs, Sustainability, and Resource Assessment from Harmonized Modeling; Technical Report ANL-18/12; NREL/TP-5100-70715; PNNL-27547; National Renewable Energy Laboratory: Golden, CO, USA, 2018. [Google Scholar]
  61. Tilman, D. The ecological consequences of changes in biodiversity: A search for general principles. Ecology 1999, 80, 1455–1474. [Google Scholar] [CrossRef]
  62. Dzialowski, A.R.; Smith, V.H. Nutrient dependent effects of consumer identity and diversity on freshwater ecosystem function. Freshw. Biol. 2008, 53, 148–158. [Google Scholar] [CrossRef]
  63. Zeller, S.L.; Kalinina, O.; Flynn, D.F.B.; Schmid, B. Mixtures of genetically modified wheat lines outperform monocultures. Ecol. Appl. 2012, 22, 1817–1826. [Google Scholar] [CrossRef][Green Version]
  64. Cardinale, B.J.; Gross, K.; Fritschie, K.; Flombaum, P.; Fox, J.W.; Rixen, C.; van Ruijven, J.; Reich, P.B.; Scherer-Lorenzen, M.; Wilsey, B.J. Biodiversity simultaneously enhances the production and stability of community biomass, but the effects are independent. Ecology 2013, 94, 1697–1707. [Google Scholar] [CrossRef][Green Version]
  65. Hulot, F.D.; Lacroix, G.; Lescher-Moutoué, F.; Loreau, M. Functional diversity governs ecosystem response to nutrient enrichment. Nature 2000, 405, 340–344. [Google Scholar] [CrossRef]
  66. Worm, B.; Lotze, H.K.; Hillebrand, H.; Sommer, U. Consumer versus resource control of species diversity and ecosystem functioning, Nature 2002, 417, 848–851. Nature 2002, 417, 848–851. [Google Scholar] [CrossRef]
  67. Norberg, J. Biodiversity and ecosystem functioning: A complex adaptive systems approach. Limnol. Oceanogr. 2004, 49, 1269–1277. [Google Scholar] [CrossRef]
  68. Tylianakis, J.M.; Rand, T.A.; Kahmen, A.; Klein, A.-M.; Buchmann, N.; Perner, J.; Tscharntke, T. Resource heterogeneity moderates the biodiversity-function relationship in real world ecosystems. PLoS Biol. 2008, 6, e122. [Google Scholar] [CrossRef][Green Version]
  69. Behl, S.; de Schryver, V.; Diehl, S.; Stibor, H. Trophic transfer of biodiversity effects: Functional equivalence of prey diversity and enrichment? Ecol. Evol. 2012, 2, 3110–3122. [Google Scholar] [CrossRef] [PubMed]
  70. Novoveská, L.; Zaparta, A.K.M.; Zabolotney, J.B.; Atwood, M.C.; Sundstrom, E.R. Optimizing microalgae cultivation and wastewater treatment in large-scale offshore photobioreactors. Algal Res. 2016, 2016, 85–94. [Google Scholar] [CrossRef]
  71. Narwani, A.; Lashaway, A.R.; Hietala, D.C.; Savage, P.E.; Cardinale, B.J. Power of plankton: Effect of algal biodiversity on biocrude production and stability. Environ. Sci. Technol. 2016, 50, 13142–13150. [Google Scholar] [CrossRef][Green Version]
  72. Hietala, D.C.; Koss, C.K.; Narwani, A.; Lashaway, A.R.; Godwin, C.M.; Cardinale, B.J.; Savage, P.E. Influence of biodiversity, biochemical composition, and species identity on the quality of biomass and biocrude oil produced via hydrothermal liquefaction. Algal Res. 2017, 26, 203–217. [Google Scholar] [CrossRef]
  73. Godwin, C.M.; Hietala, D.C.; Lashaway, A.R.; Narwani, A.; Savage, P.E.; Cardinal, B.J. Ecological stoichiometry meets ecological engineering: Using polycultures to enhance the multifunctionality of algal biocrude system. Environ. Sci. Technol. 2017, 51, 11450–11458. [Google Scholar] [CrossRef]
  74. Godwin, C.M.; Lashaway, A.R.; Hietala, D.C.; Savage, P.E.; Cardinal, B.J. Biodiversity improves the ecological design of sustainable biofuel systems. GCB Bioenergy 2018, 10, 752–765. [Google Scholar] [CrossRef]
  75. Carruthers, D.N.; Godwin, C.M.; Hietala, D.C.; Cardinal, B.J.; Lin, X.N.; Savage, P.E. Biodiversity improves life cycle sustainability metrics in algal biofuel production. Environ. Sci. Technol. 2019, 53, 9279–9288. [Google Scholar] [CrossRef]
  76. Chen, W.-T.; Zhang, Y.; Zhang, J.; Yu, G.; Schdeman, L.C.; Zhang, P.; Minarick, M. Hydrothermal liquefaction of mixed-culture algal biomass from wastewater treatment system into bio-crude oil. Bioresour. Technol. 2014, 152, 130–139. [Google Scholar] [CrossRef]
  77. Thomas, P.K.; Dunn, G.P.; Coats, E.R.; Newby, D.T.; Feris, K.P. Algal diversity and traits predict biomass yield and grazing resistance in wastewater cultivation. J. Appl. Phycol. 2019, 31, 2323–2334. [Google Scholar] [CrossRef]
  78. Kim, B.-H.; Choi, J.-E.; Cho, K.; Kang, Z.; Ramanan, R.; Moon, D.-G.; Kim, H.-S. Influence of water depth on microalgal production, biomass harvest, and energy consumption in high rate algal pond using municipal wastewater. J. Microbiol. Biotechnol. 2018, 28, 630–637. [Google Scholar] [CrossRef]
  79. Audu, M.; Myint, M.T.; Cheng, F.; Mallick, K.; Jena, U.; Nirmalakhandan, N.; Brewer, C.E. Hydrothermal liquefaction of algae grown on brackish dairy wastewater. In Proceedings of the ASABE 2018 Annual International Meeting, Detroit, MI, USA, 29 July–1 August 2018. [Google Scholar] [CrossRef]
  80. Podkuiko, L.; Kasemets, M.-L.; Kikas, T.; Lips, I. Cultivation of algae polyculture in municipal wastewater with CO2 supply. Environ. Clim. Technol. 2020, 24, 188–200. [Google Scholar] [CrossRef]
  81. Thomas, P.K.; Dunn, G.P.; Good, A.R.; Callahan, M.P.; Coats, E.R.; Newby, D.T.; Feris, K.P. A natural algal polyculture outperforms an assembled polyculture in wastewater-based open pond biofuel production. Algal Res. 2019, 40, 101488. [Google Scholar] [CrossRef]
  82. Arashiro, L.T.; Ferrer, I.; Rousseau, D.P.L.; van Hulle, S.W.H.; Garfí, M. The effect of primary treatment of wastewater in high rate algal pond systems: Biomass and bioenergy recovery. Bioresour. Technol. 2019, 280, 27–36. [Google Scholar] [CrossRef][Green Version]
  83. Goswami, G.; Makut, B.B.; Das, D. Sustainable production of bio-crude oil via hydrothermal liquefaction of symbiotically grown biomass of microalgae-bacteria coupled with effective wastewater treatment. Sci. Rep. 2019, 9, 15016. [Google Scholar] [CrossRef][Green Version]
  84. Liu, J.; Danneels, B.; Vanormelingen, P.; Vyverman, W. Nutrient removal form horticultural wastewater by benthic filamentous algae Klebsormidium sp., Stigeoclonium spp. and their communities: From laboratory flask to outdoor Algal Turf Scrubber (ATS). Water Res. 2016, 92, 61–68. [Google Scholar] [CrossRef]
  85. Ryšánek, D.; Elster, J.; Kováčik, L.; Škaloud, P. Diversity and dispersal capacities of a terrestrial algal genus Klebsormidium (Streptophyta) in polar regions. FEMS Micobiol. Ecol. 2016, 92, fiw039. [Google Scholar] [CrossRef][Green Version]
  86. Molina Grima, E.; Femández Sevilla, J.M.; Sánchez Pérez, J.A.; García Camacho, F. A study on simultaneous photolimitation and photoinhibition in dense microalgal cultures taking into account incident and averaged irradiances. J. Biotechnol. 1996, 45, 59–69. [Google Scholar] [CrossRef]
  87. Benemann, J. Wastewater treatment with microalgae ponds. In Proceedings of the 7th Conference of International Society for Applied Phycology (ISAP2020–2021 Virtual), Virtual, 14 May–13 August 2021. [Google Scholar]
  88. Lundquist, T.J.; Blackwell, P.E.S.; Diego, E.; Coyne, J.; Benemann, J. Microalgae for water and nutrient recycling. In Proceedings of the 7th Conference of International Society for Applied Phycology (ISAP2020–2021 Virtual), Virtual, 14 May–13 August 2021. [Google Scholar]
  89. Craggs, R.J.; Park, J.B.K.; Weaver, L. Removal of faecal indicators and human viral pathogens in hectare-scale wastewater treatment high rate algal pond system. In Proceedings of the 7th Conference of International Society for Applied Phycology (ISAP2020–2021 Virtual), Virtual, 14 May–13 August 2021. [Google Scholar]
  90. Acién, F.G. Microalgae production coupled to wastewater treatment. In Proceedings of the 7th Conference of International Society for Applied Phycology (ISAP2020–2021 Virtual), Virtual, 14 May–13 August 2021. [Google Scholar]
  91. Sun, L.; Tian, Y.; Zhang, J.; Cui, H.; Zuo, W.; Li, J. A novel symbiotic system combining algae and sludge membrane bioreactor technology for wastewater treatment and membrane fouling mitigation: Performance and mechanism. Chem. Eng. J. 2018, 344, 246–253. [Google Scholar] [CrossRef]
  92. Ye, J.; Liang, J.; Wang, L.; Markou, G.; Jia, Q. Operation optimization of a photo-sequencing batch reactor for wastewater treatment: Study on influencing factors and impact on symbiotic microbial ecology. Bioresour.Technol. 2018, 252, 7–13. [Google Scholar] [CrossRef]
  93. Sun, L.; Tian, Y.; Zhang, J.; Li, H.; Tang, C.; Li, J. Wastewater treatment and membrane fouling with algae-activated sludge culture in a novel membrane bioreactor: Influence of inoculation ratios. Chem. Eng. J. 2018, 343, 455–459. [Google Scholar] [CrossRef]
  94. Tang, C.-C.; Tian, Y.; He, Z.-W.; Zuo, W.; Zhang, J. Performance and mechanism of a novel algal-bacterial symbiosis system based on sequencing catch suspended biofilm reactor treating domestic wastewater. Bioresour. Technol. 2018, 265, 422–431. [Google Scholar] [CrossRef]
  95. Mujtaba, G.; Rizwan, M.; Kim, G.; Lee, K. Removal of nutrients and COD through co-culturing activated sludge and immobilized Chlorella vulgaris. Chem. Eng. J. 2018, 343, 155–162. [Google Scholar] [CrossRef]
  96. Zhu, S.; Qin, L.; Feng, P.; Shang, C.; Wang, Z.; Yuan, Z. Treatment of low C/N ratio wastewater and biomass production using co-culture of Chlorella vulgaris and activated sludge in a batch photobioreactor. Bioresour. Technol. 2019, 274, 313–320. [Google Scholar] [CrossRef]
  97. Sepehri, A.; Sarrafzadeh, M.-H.; Avateffazeli, M. Interaction between Chlorella vulgaris and nitrifying-enriched activated sludge in the treatment of wastewater with low C/N ratio. J. Clean. Prod. 2020, 247, 119164. [Google Scholar] [CrossRef]
  98. Fan, J.; Chen, Y.; Zhang, T.C.; Ji, B.; Gao, L. Performance of Chlorella sorokiniana-activated sludge consortium treating wastewater under light-limited heterotrophic condition. Chem. Eng. J. 2020, 382, 122799. [Google Scholar] [CrossRef]
  99. Nugyen, T.-T.-D.; Niguyen, T.-T.; Binh, Q.A.; Bui, X.-T.; Ngo, H.H.; Vo, H.N.P.; Lin, K.-Y.A.; Vo, T.-D.-H.; Guo, W.; Lin, C.; et al. Co-culture of microalgae-activated sludge for wastewater treatment and biomass production: Exploring their role under different inoculation ratios. Bioresour. Technol. 2020, 314, 123754. [Google Scholar] [CrossRef]
  100. Randall, H. NMSU Environmental Engineers Examine New Method for Wasterwater Treatment, Reuse. 2019. Available online: (accessed on 21 October 2021).
  101. Brennan, L.; Owende, P. Biofuels from microalgae-a review of technologies for production, processing, and extractions of biofuels and co-products. Renew. Sustain. Energy Rev. 2010, 14, 557–577. [Google Scholar] [CrossRef]
  102. Mohn, F.H. Experiences and strategies in the recovery of biomass from mass cultures of microalgae. In Algae Biomass, Production and Use; Shelef, G., Soeder, C.J., Eds.; Elsevier/North-Holland Biomedical Press: Amsterdam, The Netherlands, 1980; pp. 547–571. [Google Scholar]
  103. Uduman, N.; Qi, Y.; Danquah, M.K.; Forde, G.M.; Hoadley, A. Dewatering of microalgal cultures: A major bottleneck to algae-based fuels. J. Renew. Sustain. Energy 2010, 2, 012701. [Google Scholar] [CrossRef]
  104. Fasaei, F.; Bitter, J.H.; Slegers, P.M.; van Boxtel, A.J.B. Techno-economic evaluation of microalgae harvesting and dewatering systems. Algal Res. 2018, 31, 347–362. [Google Scholar] [CrossRef]
  105. Pahl, S.L.; Lee, A.K.; Kalaitzidis, T.; Ashman, P.J.; Sathe, S.; Lewis, D.M. Harvesting, Thickening and Dewatering Microalgae Biomass. In Algae for Biofuels and Energy; Borowitzka, M.A., Moheimani, N.R., Eds.; Springer: Dordrecht, The Netherlands, 2013; pp. 165–185. [Google Scholar]
  106. Grima, E.M.; Belarbi, E.H.; Fernandez, F.G.A.; Medina, A.R.; Chisti, Y. Recovery of microalgal biomass and metabolites: Process options and economics. Biotechnol. Adv. 2003, 20, 491–515. [Google Scholar] [CrossRef]
  107. Danquah, M.K.; Ang, L.; Uduman, N.; Moheimani, N.; Fordea, G.M. Dewatering of microalgal culture for biodiesel production: Exploring polymer flocculation and tangential flow filtration. J. Chem. Technol. Biotechnol. 2009, 84, 1078–1083. [Google Scholar] [CrossRef]
  108. Shelef, G.; Sukenik, A.; Green, M. Microalgae Harvesting and Processing: A Literature Review; Report SERI/STR-231-2396; Technion Research and Development Foundation Ltd.: Haifa, Israel, 1984. Available online: (accessed on 22 October 2021).
  109. Becker, E.W.; Venkataraman, L.V. Biotechnology and Exploitation of Algae: The Indian Approach: A Comprehensive Report on the Cultivation and Utilization of Microalgae Performed at the Central Food Technological Research Institute, Mysore, India; German Agency for Technical Cooperation: Eschborn, Germany, 1982. [Google Scholar]
  110. O’Connell, D.; Savelski, M.; Slater, C.S. Life cycle assessment of dewatering routes for algae derived biodiesel processes. Clean Technol. Environ. Policy 2013, 15, 567–577. [Google Scholar] [CrossRef][Green Version]
  111. Lardon, L.; Hélias, A.; Sialve, B.; Steyer, J.-P.; Bernard, O. Life-cycle assessment of biodiesel production from microalgae. Environ. Sci. Technol. 2009, 43, 6475–6481. [Google Scholar] [CrossRef][Green Version]
  112. Shelef, G.; Soeder, C.J. (Eds.) Algae Biomass, Production and Use; Elsevier/North Holland Biomedical Press: Amsterdam, The Netherlands, 1980. [Google Scholar]
  113. Burlew, J.S. (Ed.) Current status of the large-scale culture of Algae 1. In Algal Culture from Laboratory to Pilot Plant; Carnegie Institution of Washington Publication: Washington, DC, USA, 1953; pp. 3–23. [Google Scholar]
  114. Muylaert, K.; Bastiaens, L.; Vandamme, D.; Gouveia, L. Harvesting of microalgae: Overview of process options and their strengths and drawbacks. In Microalgae-based Biofuels and Bioproducts; Gonzalez-Fernandez, C., Muñoz, R., Eds.; Woodhead Publishing: Oxford, UK, 2017; pp. 113–132. [Google Scholar]
  115. Singh, G.; Patidar, S.K. Microalgae Harvesting Techniques: A review. J. Environ. Manage. 2018, 217, 499–508. [Google Scholar] [CrossRef]
  116. Richmond, A. (Ed.) Biological principles of mass cultivation. In Handbook of Microalgal Culture: Biotechnology and Applied Phycology; Blackwell Publishing: Oxford, UK, 2003; pp. 125–177. [Google Scholar]
  117. Moraine, R.; Shelef, G.; Sandbank, E.; Bahr-Moshe, Z.; Shvartzburd, L. Recovery of sewage-borne algae: Flocculation, flotation, and centrifugation techniques. In Algae Biomass, Production and Use; Shelef, G., Soeder, C.J., Eds.; Elsevier/North-Holland Biomedical Press: Amsterdam, The Netherlands, 1980; pp. 531–545. [Google Scholar]
  118. Tenney, M.W.; Echelberger, W.F.; Schuessler, R.G.; Pavoni, J.L. Algal flocculation with synthetic organic polyelectrolytes. Appl. Microbiol. 1969, 18, 965–971. [Google Scholar] [CrossRef]
  119. Tilton, R.C.; Murphy, L.; Dixon, J.K. Flocculation of algae with synthetic polymeric flocculants. Water Res. 1972, 6, 155–164. [Google Scholar] [CrossRef]
  120. Bilanovic, D.; Shelef, G.; Sukenik, A. Flocculation of microalgae with cationic polymers—Effects of medium salinity. Biomass 1988, 17, 65–76. [Google Scholar] [CrossRef]
  121. Udom, I.; Zaribaf, B.H.; Halfhide, T.; Gillie, B.; Dalrymple, O.; Zhang, Q.; Ergas, S.J. Harvesting microalgae grown on wastewater. Bioresour. Technol. 2013, 139, 101–106. [Google Scholar] [CrossRef]
  122. Molina Grima, E.; Acien Fernandez, F.G.; Robles Medina, A. Downstream processing of cell-mass and products. In Handbook of Microalgal Culture: Biotechnology and Applied Phycology; Richmond, A., Ed.; Blackwell Publishing: Oxford, UK, 2003; pp. 215–251. [Google Scholar]
  123. Mohn, F.H.; Soeder, C.J. Improved technologies for the harvesting and processing of microalgae and their impact on production costs. Arch. Hydrobiol. Bech. Ergebn. Limnol. 1978, 11, 228–253. [Google Scholar]
  124. Biller, P.; Ross, A. Potential yields and properties of oil from the hydrothermal liquefaction of microalgae with different biochemical content. Bioresour. Technol. 2011, 102, 215–225. [Google Scholar] [CrossRef]
  125. Jazrawi, C.; Biller, P.; Ross, A.B.; Montoya, A.; Maschmeyer, T.; Haynes, B.S. Pilot Plant Testing of Continuous Hydrothermal Liquefaction of Microalgae. Algal Res. 2013, 2, 268–277. [Google Scholar] [CrossRef][Green Version]
  126. Wang, B.; Huang, Y.; Zhang, J. Hydrothermal liquefaction of lignite, wheat straw and plastic waste in sub-critical water for oil: Product distribution. J. Anal. Appl. Pyrolysis 2014, 110, 382–389. [Google Scholar] [CrossRef]
  127. Gollakota, A.R.K.; Kishore, N.; Gu, S. A review on hydrothermal liquefaction of biomass. Renew. Sustain. Energy Rev. 2018, 81, 1378–1392. [Google Scholar] [CrossRef]
  128. Kumar, M.; Oyedun, A.O.; Kumar, A. A review on the current status of various hydrothermal technologies on biomass feedstock. Renew. Sustain. Energy Rev. 2018, 81, 1742–1770. [Google Scholar] [CrossRef]
  129. Chen, P.H.; Quinn, J.C. Microalgae to biofuels through hydrothermal liquefaction: Open-source techno-economic analysis and life cycle assessment. Appl. Energy 2021, 289, 116613. [Google Scholar] [CrossRef]
  130. Elliott, D.C. Historical developments in hydroprocessing bio-oils. Energy Fuels 2007, 21, 1792–1815. [Google Scholar] [CrossRef]
  131. Jin, B.; Duan, P.; Xu, Y.; Wang, F.; Fan, Y. Co-liquefaction of micro-and macroalgae in subcritical water. Bioresour. Technol. 2013, 149, 103–110. [Google Scholar] [CrossRef]
  132. Elliott, D.C.; Biller, P.; Ross, A.B.; Schmidt, A.J.; Jones, S.B. Hydrothermal liquefaction of biomass: Developments from batch to continuous process. Bioresour. Technol. 2015, 178, 147–156. [Google Scholar] [CrossRef][Green Version]
  133. Toor, S.S.; Rosendahl, L.; Rudolf, A. Hydrothermal liquefaction of biomass: A review of subcritical water technologies. Energy 2011, 36, 2328–2342. [Google Scholar] [CrossRef]
  134. Palomino, A.; Godoy-Silva, R.D.; Raikova, S.; Chuck, C.J. The storage stability of biocrude obtained by the hydrothermal liquefaction of microalgae. Renew. Energy 2020, 145, 1720–1729. [Google Scholar] [CrossRef]
  135. Zhang, L.; Li, C.J.; Zhou, D.; Zhang, S.C.; Chen, J.M. Hydrothermal liquefaction of water hyacinth: Product distribution and identification. Energy Sources A: Recovery Util. Environ. Eff. 2013, 35, 1349–1357. [Google Scholar]
  136. Nallasivam, J.; Eboibi, B.E.; Isdepsky, A.; Lavanya, M.; Bhaskar, S.; Chinnasamy, S. Hydrothermal liquefaction of water hyacinth (Eichhorniacrassipes): Influence of reaction temperature on product yield, carbon and energy recovery, and hydrocarbon species distribution in biocrude. Biomass Convers. Biorefin. 2020. [Google Scholar] [CrossRef]
  137. Chen, X.; Peng, X.; Ma, X.; Wang, J. Investigation of Mannich reaction during co-liquefaction of microalgae and sweet potato waste. Bioresour. Technol. 2019, 284, 286–292. [Google Scholar] [CrossRef]
  138. Hietala, D.C.; Godwin, C.M.; Cardinale, B.J.; Savage, P.E. The independent and coupled effects of feedstock characteristics and reaction conditions on biocrude production by hydrothermal liquefaction. Appl. Energy 2019, 235, 714–728. [Google Scholar] [CrossRef]
  139. Eboibi, B.E. Impact of time on yield and properties of biocrude during downstream processing of product mixture derived from hydrothermal liquefaction of microalga. Biomass Convers. Biorefin. 2019, 9, 379–387. [Google Scholar] [CrossRef]
  140. Fortier, M.-O.P.; Roberts, G.W.; Stagg-Williams, S.M.; Sturm, B.S.M. Life cycle assessment of bio-jet fuel from hydrothermal liquefaction of microalgae. Appl. Energy 2014, 122, 73–82. [Google Scholar] [CrossRef]
  141. Carneiro, M.L.N.M.; Pradelle, F.; Braga, S.L.; Gomes, M.S.P.; Martins, A.R.F.A.; Turkovics, F.; Pradelle, R.N.C. Potential of biofuels from algae: Comparison with fossil fuels, ethanol and biodiesel in Europe and Brazil through life cycle assessment (LCA). Renew. Sustain. Energy Rev. 2017, 73, 632–653. [Google Scholar] [CrossRef]
  142. Frank, E.; Wang, M.; Han, J.; Elgowainy, A.; Palou-Rivera, I. Life-Cycle Analysis of Algal-Based Fuels with the GREET Model; Energy Systems Division, Argonne Laboratory: San Francisco, CA, USA, 2011. [Google Scholar]
  143. Frank, E.D.; Elgowainy, A.; Han, J.; Wang, Z. Life cycle comparison of hydrothermal liquefaction and lipid extraction pathways to renewable diesel from algae. Mitig. Adapt. Strateg. Glob. Chang. 2013, 18, 137–158. [Google Scholar] [CrossRef][Green Version]
  144. de Boer, K.; Moheimani, N.R.; Borowitzka, M.A.; Bahri, P.A. Extraction and conversion pathways for microalgae to biodiesel: A review focused on energy consumption. J. Appl. Phycol. 2012, 24, 1681–1698. [Google Scholar] [CrossRef]
  145. Flesch, A.; Beer, T.; Campbell, P.K.; Batten, D.; Grant, T. Greenhouse gas balance and algae-based biodiesel. In Algae for Biofuels and Energy; Springer: Berlin/Heidelberg, Germany, 2013; pp. 233–254. [Google Scholar]
  146. Woertz, I.C.; Benemann, J.R.; Du, N.; Unnasch, S.; Mendola, D.; Mitchell, B.G.; Lundquist, T.J. Life cycle GHG emissions from microalgal biodiesel- A CA-GREET model. Environ. Sci. Technol. 2014, 48, 6060–6068. [Google Scholar] [CrossRef] [PubMed]
  147. Ministry of Environment. Total Greenhouse Gas Emissions-Guidelines for Calculation Method 2017. Available online: (accessed on 22 October 2021). (In Japanese)
  148. Vasudevan, V.; Stratton, R.W.; Pearlson, M.N.; Jersey, G.R.; Beyene, A.G.; Weissman, J.C.; Rubino, M.; Hileman, J.I. Environmental performance of algal biofuel technology options. Environ. Sci. Technol. 2012, 46, 2451–2459. [Google Scholar] [CrossRef] [PubMed]
  149. Manganaro, J.L.; Lawal, A. CO2 life-cycle assessment of the production of algae-based liquid fuel compared to crude oil to diesel. Energy Fuels. 2016, 30, 3130–3139. [Google Scholar] [CrossRef]
  150. Bošnjakovíc, M.; Sinaga, N. The perspective of large-scale production of algae biodiesel. Appl. Sci. 2020, 8181. [Google Scholar] [CrossRef]
  151. Tyner, W.E.; Taheripour, F.; Zhuang, Q.; Birur, D.; Baldos, U.L. Land Use Changes and Consequent CO2 Emissions due to US Corn ethanol Production: A Comprehensive Analysis; Final Report; Department of Agricultural Economics at Purdue University: Lafayette, IN, USA, 2010. [Google Scholar]
  152. Liu, X.; Saydah, B.; Eranki, P.; Colosi, L.M.; Mitchell, B.G.; Rhodes, J.; Clarens, A.F. Pilot-scale data provide enhanced estimates of the life cycle energy and emissions profile of algae biofuels produced via hydrothermal liquefaction. Bioresour. Technol. 2013, 148, 163–171. [Google Scholar] [CrossRef]
  153. Yoo, G.; Park, M.S.; Yang, J.-W.; Choi, M. Lipid content in microalgae determines the quality of biocrude and Energy Return on Investment of hydrothermal liquefaction. Appl. Energy 2015, 156, 354–361. [Google Scholar] [CrossRef]
  154. Mehrabadi, A.; Craggs, R.; Farid, M.M. Wastewater treatment high rate algal pond biomass for bio-crude oil production. Bioresour. Technol. 2017, 224, 255–264. [Google Scholar] [CrossRef]
Figure 1. Biomass productivity in culture vessels with different water depths (September–December data added to Demura et al. [14] showing data from February to August. * September data missing due to flood damage.
Figure 1. Biomass productivity in culture vessels with different water depths (September–December data added to Demura et al. [14] showing data from February to August. * September data missing due to flood damage.
Energies 14 06992 g001
Figure 2. Relationship between volume and total suspended solids from harvesting of the determined volume algal culture, followed by thickening (I), dewatering (II), and drying (III), which was prepared based on the literature shown in Table 6.
Figure 2. Relationship between volume and total suspended solids from harvesting of the determined volume algal culture, followed by thickening (I), dewatering (II), and drying (III), which was prepared based on the literature shown in Table 6.
Energies 14 06992 g002
Figure 3. GHG emission footprint of various biofuel options from microalgae fuel models collected from scientific literature [140,142,143,146,148,149,150].
Figure 3. GHG emission footprint of various biofuel options from microalgae fuel models collected from scientific literature [140,142,143,146,148,149,150].
Energies 14 06992 g003
Figure 4. Energy in return of investment values for various pathways of biofuels from terrestrial plants and microalgae [152,153,154].
Figure 4. Energy in return of investment values for various pathways of biofuels from terrestrial plants and microalgae [152,153,154].
Energies 14 06992 g004
Figure 5. Diagram of biocrude oil production by deep-depth polyculture integrating mixotrophic algae community biomass production and wastewater treatment.
Figure 5. Diagram of biocrude oil production by deep-depth polyculture integrating mixotrophic algae community biomass production and wastewater treatment.
Energies 14 06992 g005
Table 1. Requirement for an ideal organism as an alternative feedstock to fossil fuels (prepared in reference of [1,2,3]).
Table 1. Requirement for an ideal organism as an alternative feedstock to fossil fuels (prepared in reference of [1,2,3]).
  • High fraction of biofuel component;
  • High biomass production;
  • Be able to be grown on marginal lands;
  • Adaptation to a wide range of water sources, such as fresh, brackish, saline, and wastewater;
  • Lower water footprint;
  • High potential to recycle nutrient waste streams as alternatives to fertilizers;
  • High ability of carbon capture;
  • Low-energy consumption throughout the biofuel production process;
  • Low production cost;
  • Greater scalability;
  • Lower land footprint;
  • Resilience to environmental fluctuations.
Table 2. Estimation of construction and operation/maintenance fees and unit energy consumption of conventional activated sludge process and advanced anaerobic–anoxic–oxic process (excluding incinerator) [32].
Table 2. Estimation of construction and operation/maintenance fees and unit energy consumption of conventional activated sludge process and advanced anaerobic–anoxic–oxic process (excluding incinerator) [32].
Daily Maximum Inflow of Sewage10,000 m3·day−150,000 m3·day−1100,000 m3·day−1
Conventional activated sludge process
Construction fee (million JPY)637416,21224,235
Unit construction fee (million JPY·m−3)0.640.320.24
Operation/maintenance fee (million JPY·year−1)100302488
Unit operation/maintenance fee (JPY·m−3·day−1)271713
Energy consumption (MJ·day−1)30,178106,960175,472
Unit energy consumption (MJ·m−3)
Anaerobic–anoxic–oxic (A2O) process
Construction fee (million JPY)732919,64229,979
Unit construction fee (million JPY·m−3)0.730.390.30
Operation/maintenance fee (million JPY·year−1)116371611
Unit operation/maintenance fee (JPY·m−3·day−1)322017
Energy consumption (MJ·day−1)38,582116,510187,180
Unit energy consumption (MJ·m−3)3.862.331.87
Table 3. Polyculture performances for biomass production, nutrient use and removal, and biocrude production.
Table 3. Polyculture performances for biomass production, nutrient use and removal, and biocrude production.
CultureConditionsResults HighlightedRef.
Natural algal polyculture5 ha demonstration HRAP system treating primary settled wastewater. 15 month operation.
  • ▪ Nutrient removal: about 87% removal of fBOD, about 65% removal of NH4-N, about 19% removal of DRP and about 2 log removal of Escherichia coli.
  • ▪ Algal/bacterial biomass productivity: about 8 g·m−2·day−1.
  • ▪ Conversion efficiency to biocrude oil: about 30%.
Natural algal polyculture 5 ha demonstration HRAP system treating primary settled wastewater.See Table 4 in the present paper[18]
Natural algal polyculture Three HRAP pond depths (20, 30 and 40 cm) treating primary settled wastewater.
  • ▪ Productivity: Areal productivity ranged from 134 to 200% higher in the 40 cm depth than that in the 20 cm depth.
  • ▪ Nutrient uptake: Microalgae in the 40 cm depth were more efficient at NH4-N uptake than those in the 20 cm depth.
Natural algal polyculture Offshore photobioreactor. Liquid (wastewater) depth ranged from 5 to 25 cm.
  • ▪ Species richness produces resilient communities, enabling efficient nutrient uptake due to niche complementarity.
  • ▪ Productivity: 3.5 to 22.7 g·m−2·day−1.
  • ▪ Resulting biomass: suitable for HTL fuel conversion due to consistent lipid content (13.0 ± 2.5), low ash content (12.0 ± 2.1%), and consistent elemental composition (C: 49.6 ± 1.1, H: 7.2 ± 0.2, N: 8.0 ± 1.0, S: 0.9 ± 0.1).
Monoculture: six microalgae species
Polyculture: two-species, four-species, and six-species
10 L tank. Temperture: constant (22 °C) and variable (17 °C to 27 °C).
  • ▪ Polycultures does not outperform the best species in biocrude production but has stabilizing effects on biocrude oil production over time in the variable temperature environment.
  • ▪ The two-species cultures produced biomass and biocrude of a quality that matched the average monoculture, while the four- and six-species cultures were worse on average.
  • ▪ The polycultures may offer potentially compelling advantages, including higher lipid content and lower biocrude N and O content, over their monoculture counterparts. However, such advantages, will likely be found only on a combination-specific basis.
Monoculture: five microalgae species
Polyculture: two-species, four-species, and six-species
9.5 L chemostat with 30% refresh of medium per week.
  • ▪ Some polycultures exhibit more balanced performance and maintain all three functions of nitrogen- and phosporus-nutrient-use efficiencies, and biocrude productivity at a high level simultaneously than any of monocultures.
Monoculture: five microalgae species
Polyculture: two-species and four species
1100 L outdoor pond.
  • ▪ Diversity potentially enhances the functions of biomass and biocrude-oil production and resistance against population crashes and invasions by unwanted species.
  • ▪ Most diverse polyculture (four species) forms more functions at higher levels than any of monocultures.
Monoculture: five microalgae species
Polyculture: two-species and four-species.
1100 L outdoor pond.
  • ▪ Some two-species cultures improved EROI and GHGs by 20% and 16%, respectively, compared to the best monoculture.
  • ▪ Bicultures outperformed monocultures by performing multiple functions simultaneously (e.g., improved stability, nutrient efficiency, biocrude characteristics)
Mixed-culture microalgae Directly harvested from wastewater treatment sysytemMaximum biocrude-oil yield: 49% of volatile matter (=25.7% of dry weight).
Elemental composition of C, H, N, and O: 65.7, 8.76, 3.93, and 21.7.
Monoculture: Five microalgae species
Polyculture: three-species, six-species, and a natural polyculture
Batch culture using flasks with anaerobic digester effluent.
  • ▪ No polyculture exceeded the biomass of the most productive monoculture, but higher grazing resistance is observed among polycultures when exposed to grazing pressure.
  • ▪ Polycultures may be less prone to trade-offs between desirable functions (like grazing resistance and growth rate).
Natural algal polyculture HRAP with different depths of 20, 30, and 40 cm.
  • ▪ The HRAP with 20 cm of water depth had about 38% higher biomass productivity per unit area (6.16 ± 0.33 g·m−2·day−1) and required lower nutrients and energy consumption than the other water depths.
Polyculture of microalgae isolatedPhotobioreactor with 37 L brackish dairy wastewater.
  • ▪ Ash content (dry wt.%): 20.5.
  • ▪ HTL biocrude oil productions (ash-free dry wt eq.): 11.7% to 30% of light oil and: 4% to 10% of heavy oil.
Monoculture: three microalgae species
Polyculture: three-species
300 mL conical flasks with primarily treated municipal wastewater.
  • ▪ Polyculture with CO2 supply reduces nitrogen and phosphorus concentration by the level allowed by the EU Council Directive.
Natural algal polyculture
An assembled polyculture of three-species
Open raceway pond with anaerobic digester effluent.
  • ▪ The natural polyculture: 25% higher biomass productivity and 19% higher N-removal efficiency than the assembled polyculture.
  • ▪ Differences became even more pronounced under grazing and resource stress conditions.
Natural algal polyculture HRAPs with and without primarily treated water.
  • ▪ The HRAP without primary treatment had higher biodiversity and productivity.
Consortium of two algae and two bacteria species7.5 L phtobioreactor wth wastewater from the paper indusry.
  • ▪ Biocrude oil yield: 15%.
  • ▪ Elemental composition of C,H,N,S and O: 63.16, 8.11, 5.37, 0.21 and 23.15, similar to HTL biocrude oil of the microalgae monocultures.
Natural algal polyculture Outdoor vessel-type reactor with water depth 0.8 m.
  • ▪ Areal productivity: 29.2 g·m−2·day−1.
  • ▪ Reduction of TN, TP, SS, and BOD below the levels of the quality standard of discharge water based on the Sewage Act in Japan.
  • ▪ Ash content: 15.4%, HTL biocrude oil yield: 43% of ash-free dry weight.
  • ▪ N and S contents of HTL biocrude oil: 5% and 0.3%, respectively.
  • ▪ Biocrude oil production: 1.3–1.7 times higher than lipid content
Table 4. Effluent quality of HRAP system compared with conventional wastewater treatment ponds in New Zealand (Integrated Table 1 and Table 2 in Craggs et al. [18]).
Table 4. Effluent quality of HRAP system compared with conventional wastewater treatment ponds in New Zealand (Integrated Table 1 and Table 2 in Craggs et al. [18]).
Water Quality Variables (ppm)Conventional WTP SystemHRAP SystemHRAP System with CO2 AdditionHRAP System with P Flocculation
Median95 PCTLMedian95 PCTLMedian95 PCTLMedian95 PCTL
E. coli
(MPN/100 mL)
Table 5. Nutrient removal in primarily treated sewage polyculture with 0.8 m culture depth (estimated from the figure of water quality test [26].
Table 5. Nutrient removal in primarily treated sewage polyculture with 0.8 m culture depth (estimated from the figure of water quality test [26].
Water Quality VariablesQuality Standard of Discharge Water Based on the Sewage Act in JapanInfluentEffluentEffluent after Flocculant Treatment
BOD (ppm)<15252.643.47.9
TSS (ppm)<40158.481.62.7
TN (ppm)<2038.813.97.3
TP (ppm)<
Table 6. Overview of most common dewatering technology associated with biomass concentration and energy consumption.
Table 6. Overview of most common dewatering technology associated with biomass concentration and energy consumption.
Dewatering TechnologyBiomass Concentration
(% TSS)
Energy Consumption
Gravity sedimentation1.50.10[103]
Filter basket 5.00.20[106]
Dissolved air flotation6.020.00[107]
Vibrating screen0.1–[102]
Filter thickener7.01.60[106]
Cylindrical sieve7.50.30[102]
Suction filter8.00.10[106]
Vacuum drum8.05.90[108]
Belt filter4.09.50.45[106]
Belt filter press0.518.00.50[102]
Chamber filter5.027.00.88[106]
Drum Dryer20>90.08.7[109]
Spray dryer[108]
Table 7. Comparison of energy balance and CO2 emission between conventional biodiesel production and biocrude oil production, which was prepared from the literature shown in Table 6 and [142,144,145,146].
Table 7. Comparison of energy balance and CO2 emission between conventional biodiesel production and biocrude oil production, which was prepared from the literature shown in Table 6 and [142,144,145,146].
Biofuel FeedstockUnit
MJ·kg−1 BM
Production ProcessEnergy Input
MJ·kg−1 BM
Accumulated Energy Input
MJ·kg−1 BM
Accumulated CO2 Emission *
kg-CO2·kg−1 BM
Dry Algae Biomass (BM)20
(polyculture using wastewater)
(monoculture of high lipid BM)
1. Cultivation (pumping, mixing)2.50 2.50 0.04875
2. Cultivation (Fertilizer use)5.43 7.93 0.15464
3. Harvesting/Dewatering (~80 wt% moisture1.99 9.92 0.19344
4. Drying (from ~80 wt% moisture to <10% moisture)9.00 18.92 0.36894
Net Energy in polyculture for HTL (MJ·kg−1 BM): process 1, 3)15.51
Net energy in monoculture of high lipid BM (MJ·kg−1 dry BM): process 1–45.08
Biodiesel (30 wt% of dry BM)12BM at <10 wt% moisture 18.920.36894
Dry BM extraction (40 wt% lipids)0.9319.850.38708
Glycerol (96 g·kg−1 BM)1.65Transesterification (Methanolysis)0.8720.720.40404
Remaining BM (60 wt%)8.15
Total output at 1 kg BM21.8
Net Energy (MJ·kg−1 BM)1.08
Biocrude oil (HTL) (50 wt% conversion rate)17.5BM at ~80 wt% moisture 4.490.08756
HTL conversion (MJ·kg−1 biocrude oil)3,257.740.15093
Solid/liquid separation (Tricanter)0.157.890.15386
Dewatering by sedimentation0.78.590.16751
Thermal water removal at ~50 wt% moisture1.8510.440.203580
Remaining solids (~35 wt%) for biogas10.6
Gas phase (10–15 wt%)0.11–0.165
Total HTL Output at 1 kg Biomass28.21
Net Energy (MJ·kg−1 BM)17.77
* CO2 emission was estimated based on the unit calorific value of heavy oil in accordance with the guideline of the Ministry of Environment, Japan [147].
Publisher’s Note: MDPI stays neutral with regard to jurisdictional claims in published maps and institutional affiliations.
Back to TopTop