Biosequestration of atmospheric CO2 and flue gas-containing CO2 by microalgae

Accepted Manuscript Review Biosequestration of atmospheric CO2 and flue gas-containing CO2 by microalgae Wai Yan Cheah, Pau Loke Show, Jo-Shu Chang, Tau Chuan Ling, Joon Ching Juan PII: DOI: Reference:

S0960-8524(14)01628-9 http://dx.doi.org/10.1016/j.biortech.2014.11.026 BITE 14232

To appear in:

Bioresource Technology

Received Date: Revised Date: Accepted Date:

30 August 2014 7 November 2014 9 November 2014

Please cite this article as: Cheah, W.Y., Show, P.L., Chang, J-S., Ling, T.C., Juan, J.C., Biosequestration of atmospheric CO2 and flue gas-containing CO2 by microalgae, Bioresource Technology (2014), doi: http://dx.doi.org/ 10.1016/j.biortech.2014.11.026

This is a PDF file of an unedited manuscript that has been accepted for publication. As a service to our customers we are providing this early version of the manuscript. The manuscript will undergo copyediting, typesetting, and review of the resulting proof before it is published in its final form. Please note that during the production process errors may be discovered which could affect the content, and all legal disclaimers that apply to the journal pertain.

A manuscript submitted to Bioresource Technology Special Issue on "Advances in Biofuels and Chemicals from Algae" Biosequestration of atmospheric CO2 and flue gas-containing CO2 by microalgae Wai Yan Cheaha, Pau Loke Showb,c, Jo-Shu Changd,e,f, Tau Chuan Linga, Joon Ching Juang*,h a

Institute of Biological Sciences, Faculty of Science, University of Malaya, 50603 Kuala Lumpur, Malaysia.

b

Department of Chemical and Environmental Engineering, Faculty of Engineering, University of Nottingham Malaysia Campus, Jalan Broga, 43500 Semenyih, Selangor Darul Ehsan, Malaysia.

c

Manufacturing and Industrial Processes Division, Faculty of Engineering, Centre for Food and Bioproduct Processing, University of Nottingham Malaysia Campus, Jalan Broga, 43500 Semenyih, Selangor Darul Ehsan, Malaysia.

d

University Center for Bioscience and Biotechnology, National Cheng Kung University, Tainan

701, Taiwan. e

Department of Chemical Engineering, National Cheng Kung University, Tainan 701, Taiwan

f

Research Center for Energy Technology and Strategy, National Cheng Kung University, Tainan

701, Taiwan. g

Nanotechnology & Catalyse Research Centre (NANOCAT), University of Malaya, 50603 Kuala Lumpur, Malaysia.

h

Laboratory of Advanced Catalysis and Environmental Technology, School of Science, Malayssia.

*Corresponding address: Joon Ching Juan Nanotechnology & Catalysis Research Centre (NANOCAT), University of Malaya, 50603 Kuala Lumpur, Malaysia Laboratory of Advanced Catalysis and Environmental Technology, School of Science, Malaysia Tel: +603-79676267 Email: [email protected] (J.C. Juan).

1

Abstract The unceasing rise of greenhouse gas emission has led to global warming and climate change. Global concern on this phenomenon has put forward the microalgal-based CO2 sequestration aiming to sequester carbon back to the biosphere, ultimately reducing greenhouse effects. Microalgae have recently gained enormous attention worldwide, to be the valuable feedstock for renewable energy production, due to their high growth rates, high lipid productivities and the ability to sequester carbon. The photosynthetic process of microalgae uses atmospheric CO2 and CO2 from flue gases, to synthesise nutrients for their growth. In this review article, we will primarily discuss the efficiency of CO2 biosequestration by microalgae species, factors influencing microalgal biomass productions, microalgal cultivation systems, the potential and limitations of using flue gas for microalgal cultivation as well as the bio-refinery approach of microalgal biomass. Keywords Biomass production, CO2 sequestration, Fixation efficiency, Flue gas, Microalgae 1. Introduction The anthropogenic activities such as burning of fossil fuel, deforestation and energy generation have caused intensive greenhouse gases emission. United States Environmental Protection Agency (USEPA) has stated that energy production and consumption, mainly from transportation, has contributed 71% of greenhouse gas emission world-wide in 2010. This emission has increased by 35% from 1990 to 2010 (Wilbanks & Fernandez, 2014). Carbon dioxide (CO2), which is a major greenhouse gas, has risen in its atmospheric concentration, which is from 280 to 390 ppm since pre-industrial revolution till 2013 (Rahaman et al., 2011; Singh & Ahluwalia, 2013). Though CO2 is essential for survival of photoautotrophs, however 2

this copious and unceasing rise concentration has contributed largely to global warming, as CO2 retains with atmospheric lifetime of 50 to 200 years (Van Den Hende et al., 2012). At present, CO2 is contributing approximately 52% in total global warming (Wilbanks & Fernandez, 2014). An example of effort can be seen under the Kyoto Protocol, 37 industrialised countries and European community have agreed to reduce the greenhouse gases emission by 18% below 1990 level within the period of 2013 to 2020 (Yoo & Al-Attiyah, 2013). Attempts have been made to mitigate the emissions, for instance, the carbon sequestration of biomass feedstock, microalgae. Microalgae have been long recognised as the promising alternatives for biofuel production, aiming to replace the utilisation of fossil fuel, and serves as the major feedstock towards greenhouse gases mitigation. This approach of using microalgae is predominantly due to their photosynthetic efficiency in bio-converting carbon dioxide (CO2), high biomass productivity, high lipid accumulation, and their valuable non-fuel co-products (Xie et al., 2014). The photosynthetic or autotrophic microalgae have high capabilities to fix CO2, which is 10-50 times more efficiently than terrestrial plants (Cheng et al., 2013; Lam et al., 2012). Terrestrial plants are only expected to contribute only 3-6% reduction in global CO2 emissions (Ho et al., 2011; Kao et al., 2014). During photosynthetic process, the CO2 is utilised as carbon source, to be converted into organic compounds by using solar energy. Carbon is the most important element for microalgae nutrition, followed by nitrogen and phosphorus (Lam & Lee, 2011). Dried microalgal biomass contains approximately 50% of carbon, which are all derived from CO2 (Lam et al., 2012). Approximately 1.83 kg of CO2 can be fixed in every 1 kg of microalgae biomass production (Jiang et al., 2013). These studies have revealed the fact that microalgae serve as the strong agent in CO2 biosequestration. There are many studies on the microalgalbased CO2 bio-mitigation presently but there is lacking of review literature on the latest

3

technologies on microalgal cultivation, which mainly towards successful CO2 bio-sequestration of atmospheric CO2 and flue gas-containing CO2. Therefore, this review attempts to summarise and discuss the CO2 bioconversion efficiency of microalgae species, factors influencing microalgal biomass productions, microalgal cultivation systems, the potential and limitation of flue gas utilisation for microalgae cultivation, and the bio-refinery of microalgal biomass. 2. Microalgae: The agent for carbon sequestration Microalgae are photosynthetic microorganisms, the basic plants present in abundance in the nature. Algae are divided into five main groups, namely Chlorophyceae, Rhodophyceae, Phaeophycea, Cynophyceae and Bacillariophyceae. Characteristics of each algae group are summarised in Table 1. Microalgae able to duplicate very rapidly of its cell biomass, and achieve 100 times faster than terrestrial plants (Lam et al., 2012). Microalgae though lacking in roots, stems and leaves, but has chlorophyll as their photosynthetic pigment. They are able convert the major carbon source which is the atmospheric CO2, to glucose for their growth (Ho et al., 2014a). As shown in Fig. 1, photosynthesis reaction is categorised into light dependent and light independent stage. The light dependent is the first stage whereby microalgae capture and store energy from sunlight, converting ADP and NADP+ into energy-carrying molecules ATP and NADPH. In the second stage of photosynthesis, which is the light independent reaction, microalgae will capture CO2 producing organic compounds by Calvin-Benson cycle, with the previously generated ATP and NADPH molecules (Zhao & Su, 2014). The high CO2 bioconversion efficiency and high growth rate of microalgae, allowing it to become the agent of carbon sequestration. 3. Perspectives of carbon dioxide capture for microalgae cultivation

4

Carbon dioxide is readily available in the atmosphere in concentration of 0.03-0.06% (v/v). Another elevated source of CO2 is originated from zero cost flue gas, which may give 615% (v/v) of CO2 (Rahaman et al., 2011). These are the major sources of CO2 used for microalgae cultivation, so as to continuously growing microalgae, for carbon sink production. Fig. 2 shows the relationship between microalgal-CO2 sequestration and biomass production. The CO2 fixation and biomass production vary distinctly depending on the characteristics of microalgae species, effects of physicochemical process and effects of cultivation systems. The following sections summaries the effects of microalgal species and growth conditions in relation to microalgal biomass production and bioconversion efficiency. 3.1 Biomass production – Effects of microalgal species Biomass production is the most significant indicator to observe when research into CO2 bio-sequestration by microalgae cultivation. The selection of appropriate microalgae species for microalgae cultivation, determines the success in CO2 bioconversion for biomass production. The ideal algal species should have high sinking capacity, high tolerance to CO2 concentration, toxic pollutants concentrations, temperature, nutrients limitation and pH effect. As stated by Singh and Ahluwalia (2013), microalgae species Scenedesmus obliquus, Botryococcus braunii, Chlorella vulgaris and Nannochloropsis oculata are the most promising species for carbon sequestration as well as for biofuel production. Chlorella sp. was identified as the species which possesses higher biomass production up to 1.06 g L-1 d-1 as compared to Cyanophytes and Chrysophyte species (Zhao & Su, 2014). As shown in Table 2, Chlorella sp., Scenedesmus sp. and Spirulina sp. (Table 2, no.5-20, 23-26 & 27-35) possess high biomass yield. It should be noted that the high performance of mentioned microalgae is obtained under different experimental conditions, such as light intensity, CO2 concentration and photobioreactor design.

5

This variation may affect the microalgal bio-fixation efficiency and biomass productions. Table 2 summarises literature survey on microalgal species that have been discussed in latest research on CO2 bioconversion and biomass production, rather than strict comparison on performance among these species. In exact, the comparative study among microalgae species is still lacking to date, due to the variation in parameters and cultivation conditions. The indication of best microalgae species is obtained by considering the tolerance level of the microalgae. For instance, a study reported that Scenedesmus dimorphus exhibited biomass of 4.51 and 3.82 g L-1 respectively under 10% (v/v) and 20% (v/v) of CO2, but achieved maximum biomass of 5.17 g L1

with 2% (v/v) CO2 (Jiang et al., 2013). This indicated that Scenedesmus sp. has high tolerance

level against CO2 concentration, making it able to grow within the range of 10-20% (v/v) although the best CO2 concentration is only 2% (v/v). 3.2 Biomass production – Effects of physicochemical process 3.2.1 Effects of CO2 concentrations Apart from typical microalgae species characteristics, the microalgae biomass production is greatly affected by cultivation conditions. Chlorella sp. was reported to be able to grow up in 40% (v/v) CO2, at pH 5.5-6.0, 30°C (Chen et al., 2014a; Rahaman et al., 2011). Conversely, Lam et al. (2012) stated that Chlorella sp. could only grow in less than 2% (v/v) of CO2 ; further increase of CO2 will inhibit their growth. These have shown that though the same microalgae species may has strong adaptation to tolerate, but the growth conditions determine the efficiency in CO2 bioconversion for biomass production. The growth rate Nannochloropsis sp. was increased for 58%, which is from 0.33 d-1 to 0.52 d-1 under cultivation of 15% (v/v) CO2 (Jiang et al., 2011). High concentration of CO2 promotes photosynthetic efficiency of microalgae to reproduce within a shorter time. Nevertheless, CO2 concentration above 5% (v/v) is considered

6

as toxic to microalgae growth (Ramanan et al., 2010; Zhao & Su, 2014). Microalgae growth was inhibited by continuous injection of increasing CO2-containing flue gas concentration to the medium (Lee et al., 2000). It was found that this flue gas inhibition is mainly occurred due to the presence of toxic pollutants NOx and SO2, which acidified the cultivation medium (Ho et al., 2014b; Ho et al., 2013; Rahaman et al., 2011; Zhao & Su, 2014). 3.2.2 Effects of nutrients Carbon, nitrogen and phosphorus are the three essential nutrients for biomass growth. Apart from carbon which can be obtained from atmospheric air or CO2 sparging, microalgae assimilate sufficient nitrogen and phosphorus from medium for their metabolic activities. Nitrogen present in the form ammonium is the primary nitrogen source for microalgae assimilation (Kumar et al., 2010; Razzak et al., 2013). Moreover, phosphorus is the element required for photosynthesis, metabolisms, formation of DNA, ATP and cell membrane. Phosphorus is available in the medium in the form phosphate and normally supplied in excess as it is not readily bioavailable. Other inorganic salts and trace element like metals and vitamins are usually added into the medium for effective photosynthetic activity. Microalgae serve as the important agent for bioremediation due to their ability to assimilate the organics and nutrients from wastewaters for their growth. They are the dominant biotics used in oxidation ponds in wastewater treatment plant and sewage treatment ponds. Algal pond could remove pollutants especially N and P, more efficiently compared to conventional activated sewage process (Zhou et al., 2014). Chlorella vulgaris, Pseudokirchneriella subcapitata, Synechocystis salina and Microcystis aeruginosa achieved nitrogen reduction percentage of 100% in wastewater, under high light supply condition (Gonçalves et al., 2014). Despite nutrient-rich wastewaters can be used as the medium, challenges are still present

7

including the C/N and N/P ratio. A suitable nutrients profile of wastewater is required for successful microalgae cultivation for CO2 biosequestration. Typically, Chlorella sp. and Scenedesmus sp. are the most notable microalgae in assimilating nutrients in the wastewaters, subsequently producing high biomass yield (Bhatt et al., 2014). 3.2.3 Effects of pH MoMicroalgae species grow well in optimal pH ranges. Synechococcus sp. and Spirulina platensis grow at optimal pH 6.8 and pH 9, respectively, meanwhile Chlorella sp. can tolerate to pH below 4 (Zeng et al., 2011; Zhao & Su, 2014). Flue gas usually contains high concentrations of NOx and SO2, which reduce the pH of culture medium. Dissolved NO from NOx is considered as an alternative nitrogen source for cell growth. It is expected that NOx in the flue gas will not bring significant negative impact to the microalgae growth. Conversely, flue gas with SO2 above 60 ppm is inappropriate to be used for microalgae cultivation (Lam et al., 2012). With the presence of 100-250 ppm of SO2 in flue gas, the pH may reduce to 2.5-3.5, due to the formation of bisulfite (HSO3-), sulfite (SO32-) and sulfate (SO42-) in the medium (Lam et al., 2012; Zhao & Su, 2014). Nevertheless, B. braunii was able to utilised S-source of bisulphite in medium with concentration of less than 104 ppm sodium bisulphite (Van Den Hende et al., 2012). This could be due to the high adaptatibilty of B. braunii species to grow in low pH medium. Furthermore, if 10-20% (v/v) of CO2 from flue gas is supplied, pH of medium can be reduced reaching 5.5 (Chen et al., 2014b; Zhao & Su, 2014). To certain extent, this can be counterbalanced by CO2 uptake of microalgae which will undoubtedly cause pH rising. Yet, some microalgae species are unable to withstand the acidic condition resulted from carbonic acid formed by CO2 dissolution in medium (Lam & Lee, 2011). Sodium hydroxide and calcium

8

carbonate are usually used to adjust pH reaching its optimal range, aiming to provide excellent CO2 bioconversion and biomass production (Rahaman et al., 2011). 3.2.4 Effects of temperature The optimal temperature for microalgae growth is ranging from 15 till 26 °C (Zhao & Su, 2014). Low temperature of culture medium is unfavourable for the enzyme activity of ribulose bisphosphate carboxylase oxygenase (RuBisCo), leading to reduction in photosynthesis rate. In contrast, high temperature inhibits microalgal metabolic rate and reduces the CO2 solubility (Rahaman et al., 2011; Zhao & Su, 2014). Low CO2 solubility causes photorespiration whereby the RuBisCo enzyme will bind with O2 rather than CO2, in consequence reducing carbon bioconversion rate by 20-30% (Zeng et al., 2011). The deviation of culture temperature from optimum range has resulted in lengthening of log phase. Flue gas in high temperature after the cooling and scrubber treatment is usually found to be suitable for cultivating thermo-tolerant microalgae like Chlorella sp. T-1 and Chlorella KR-1. They were able to grow at temperature of 35°C and 40°C, respectively (Zhao & Su, 2014). Chlorella sp. can survive and grow in hot springs at temperature 42°C with more than 40% (v/v) CO2 (Razzak et al., 2013). 3.2.5 Effects of light intensity The optimal light intensities used for microalgae cultivation is ranging from 10 to 30 mmol m2 s-1 (Razzak et al., 2013). Additionally, the metabolic rate of phototrophic microalgal cells can be enhanced by increasing the light intensity to 400 mmol m2 s-1 (Zeng et al., 2011). Algae with light-harvesting component (phycobilisomes) and most dinoflagellates prefer low (10 mmol m2 s-1) and high light intensities (60-100 mmol m2 s-1), respectively (Razzak et al., 2013). Chlorella and Scenedesmus sp. were grown under light intensity of 200 mmol m2 s-1. Light intensity is essential to be delivered to all the cells within the culture. High light intensity permits

9

light penetration to the high-density culture, allowing high photosynthetic rate due to less cell damage of photosynthetic components (photoinhibition) as the light-harvesting components absorb less light (Fernandes et al., 2014; Zeng et al., 2011). Conversely, excessive light intensity will cause photoinhibition. The highest photosynthetic efficiency is usually achieved by low and medium light intensity incorporated with appropriate temperature at a particular culturing stage. 3.3 Biomass production – Effects of cultivation strategies Microalgae cultivation is to date, applying open pond systems and closed systems. The cultivation system is designed according to the principle of achieving high surface area per volume ratio, so as to give more surface area for the light penetration and CO2 gaseous transfer. The design, scale up and the operation systems considering CO2 transfer, aeration system, and light provision are vital to maximise energy efficiency for biomass production. 3.3.1 Mixing and aeration CO2 has low solubility in the medium, meaning the mass transfer from gaseous to liquid phases is low. These resulted in lack of CO2 distribution in the medium, which may limit the microalgae growth. Optimal mixing is required to enhance CO2 distribution; simultaneously O2 stripping to eliminate O2 inhibition towards photosynthesis. Various cultivation associated with mixing strategies have applied (i) mechanical stirring systems like paddle wheel and baffles; (ii) gas injection like bubble diffuser; (iii) membrane-sparged device in order to (i) raise the gas and liquid interface areas; (ii) improve nutrients distribution; (iii) prevent self-shading area and phototoxicity for high density culture; (iv) control pH by ensuring CO2 dissolution; (v) stripping off dissolved O2 to reducing its toxicity to microalgae. With optimised aeration and stirring system, high performance Chlorella sp. achieved CO2 bioconversion efficiency of 58%, 27%, 20% and 16% under the CO2 concentration of 2%, 5%, 10% and 15% (v/v), respectively (Zhao

10

and Su, 2014). The mixing systems though contributing in CO2 gaseous transfer suffered some drawbacks. Drawbacks include (i) loss of CO2 to the atmosphere; (ii) bio-fouling of membrane and diffusers; (iii) shear damage to cells; (iv) large energy input and (v) poor mass transfer to relatively low interfacial surface area. The appropriate flow and mixing has to be determined, so as to elevate the CO2 fixation performance by maximising the pros and minimising the cons. 3.3.2 Light provision Effective utilisation of solar energy is vital towards economically viable microalgal cultivation for CO2 sequestration. Practically, sunlight and artificial light are the light sources used in current cultivation systems. The light penetration is expressed as percentage of irradiation invading on the culture surface. There are light zone and dark zone which describe the illuminated volume supplied with light and the non-illuminated dark volume without supporting photosynthesis, respectively (Razzak et al., 2013). In microalgae cultivation, the light supplied throughout the whole culturing process has to be regulated according to the changing algae population density. Neochloris oleobundans has shown doubling of its biomass in sequential change of light intensity comparing to a constant light supply (Pires et al., 2012). The higher the microalgal density, the smaller the light path, leads to limitation in light penetration and cell shading. Effective mixing can prevent cell shading, which resulted from less light supply to certain zone within the cultivation system. Moreover, light flux can be increased with decreasing distance from irradiated source and receiving surface, and increasing the surface area for light absorption (Ho et al., 2011; Pires et al., 2012). Optical fibers can also be used to guide sunlight into photobioreactor, enhancing illumination for microalgal cultivation (Pires et al., 2012). The photoperiods of light/dark periods required are typically ranging from 12/12 to 16/8 hours. These light/dark periods are important as the photo-induced damage caused by over-

11

illumination of excessive photon flux can be repaired during the dark period. Scenedesmus obliquus has shown high photosynthetic rate with increasing light/dark frequencies (Pires et al. (2012). The light/dark of 10 Hz frequency cycles for Spirulina platensis and Scenedesmus dimorphus cultivation resulted in microalgae productivity to increase by 43% and 38%, respectively (Razzak et al., 2013). Hence, high flow rate of medium can be incorporated as this provides shorter light/dark cycle, greater frequency fluctuations, subsequently improving light utilisation. Additionally, microalgae do not acclimate to a definite light/dark period. This is dependent on the nature of microalgae species, its acclimated state, frequency of changing light/dark period, and the duration of exposure (Fernandes et al., 2014; Pires et al., 2012). Genetic engineering can be incorporated by shortening the size of photosynthetic antenna, therefore boosting the microalgal photosynthetic efficiency (Ho et al., 2011). Placement of lighting device like LEDs or optical fiber inside the reactor can maximise light absorbance for microalgae utilisation (Kumar et al., 2010). The factors to be considered in bioreactor design and configurations include density of culture medium, optical depth of light, the amount of radiation being absorbed or scattered through medium, mixing efficiency, diameter of vessels to obtain increase illuminated surface area/volume of culture and integration with internal illumination. With these, light distribution can be enhanced to improve the microalgal photosynthetic efficiency and subsequently bringing effective CO2 sequestration. 3.4 Carbon dioxide fixation efficiency Photosynthesis is a natural way for CO2 recycling. Annually, 500 billion tonnes of CO2 is bio-mitigated by terrestrial vegetation worldwide yet this fixation is considered as inadequate (Xie et al., 2014). Microalgae have greater fixation ability than terrestrial plants, by biosequestration of atmospheric CO2 and CO2 from flue gas, into organic compounds. The

12

assimilation of CO2 is highly dependent on the five main factors namely (i) characteristics of the microalgae strain; (ii) CO2 concentration; (iii) cultivation system and photobioreactor design (iv) operating conditions (v) environmental factors (Ho et al., 2014c; Razzak et al., 2013). Biomass measurements and growth rate evaluations are crucial tools in evaluating the efficiency of microalgae in bio-sequestrating CO2. The latest data on CO2 fixation rate, removal percentage and biomass yield of various microalgae species are illustrated in Table 2. It has shown that microalgae species posed various CO2 fixation rates and removal percentages under different CO2 concentrations and cultivation methods. Closed photobioreactor cultivation has been studied widely due to the ease of regulating microalgal growth parameters. Several CO2 concentrations are usually supplied to evaluate the microalgal behavior in determining the CO2 sequestration efficiency. Some microalgae species require high CO2 concentration in the medium, indicating their ability to bio-convert high CO2 concentration. The CO2 removal efficiency by microalgae can be determined as the difference in CO2 concentration of the influent and effluent. This difference was due to the removal by microalgae. The removal efficiency (%) can be determined using the following formula: CO concentration of inluent − CO concentration of efluent × 100% CO concentration of inluent Carbon dioxide fixation rate can be determined by the carbon content in the algal cell. The CO2 fixation rate (g CO2 m-3 h-1) is estimated using the formula as follow: RCO = C × μ

MCO Mc

Where R CO2 and µ L are the CO2 fixation rate and the volumetric growth rate (g dry weight m-3 h-1) respectively, in the linear growth phase. MCO2 and MC represented the molar mass of CO2 and elemental carbon, respectively, CC is average carbon content of microalgal cells (% w/w).

13

The average carbon content measured by an elemental analyzer (CC measured by elemental analyzer) (CHNS-932, Leco), was 0.507 g carbon per g dry cell weight. The algal growth rate was determined in the linear growth phase because most of the algal growth occurred during this phase. (Anjos et al., 2013; Razzak et al., 2013). Chlorella sp., Scenedesmus sp. and Spirulina sp. have been identified as the favourable microalgae strains to bio-sequester CO2. This could be due to their high CO2 fixation ability, growth rate, tolerance level towards adverse environmental effects and rich in protein, carbohydrate and lipid. With refers to Table 2 (no. 16-20), the increase in CO2 concentration for Chlorella sp. cultivation led to increase in CO2 fixation rate, regardless of the cultivation systems applied which are either lab scale methods, photobioreactor or open pond system. Additionally, Chlorella KR-1 showed good growth rate at 10-50% CO2 (v/v) (Singh et al., 2014). Ho et al. (2011) and Li et al. (2011) (Table 2, no. 24-25) have worked on the CO2 sequestration by Scenedesmus obliquus using glass made vessel and air lift photobioreactor respectively. The decrease in CO2 concentration gave better growth rate and CO2 removal efficiency (Ho et al., 2011). Conversely, this was contradicted to the results obtained from Li et al. (2011). This could be due to the variation in cultivation system and growth conditions. The growth rate, bio-fixation rate and removal percentage of Spirulina sp. (Table 2, no.27-35) has shown inversely proportional to the CO2 concentration supplied (De Morais & Costa, 2007; Knudsen et al., 2009; Ramanan et al., 2010; Sydney et al., 2010). High CO2 concentration may increase the CO2 mass transfer; however pH reduction may also inhibit to the microalgae growth. The elevated CO2 concentration supplied may lead to the decrease of pH, subsequently causing lengthening in log phase and reduction in growth rate (Rinanti et al., 2014).

14

CO2 diffuses into liquid phase 104 times slower than through gaseous medium (McGinn et al., 2011). This has caused insufficient CO2 supply to the microalgae strains for growth, as atmospheric CO2 is only in approximately 360 ppm (Lam & Lee, 2011). Costly CO2 sparging like air-pumping is necessary to improve the retention time of CO2 in the medium. The CO2 flow rate of 5 L min-1 was significantly contributes to the effective CO2 distribution (Rinanti et al., 2014). Apart from CO2 sparging, emitted flue gases can be the carbon source to grow algae. Some researchers have found out the possibility of direct CO2 fixation of Chlorella KR-1, by using actual flue gases generated from combustion process (Singh et al., 2014). 4. Microalgae cultivation system Successful microalgae cultivation requires supply of adequate sunlight, CO2 and nutrients. Comprehensive design of cultivation system is aimed to provide the optimal growth conditions for microalgal growth, thus maximising the biomass production. The selection microalgal cultivation systems are still depending on these factors like (i) cost (ii) CO2 capture source (iii) type of target products and (iv) the nutrient sources. The types of microalgae cultivation systems used at present are summarised in the following sections. 4.1 Open pond system Open pond system is the most commonly applied for large scale microalgae cultivation due to its low cost and ease in operation and maintenance. It is commonly used for industrial application, to produce significant amount of products for commercial purposes at relatively low cost. The open pond is commonly designed as 0.25 m in width, with area of 0.2-0.5 hectares for commercial purpose microalgal productions (Zhao & Su, 2014). Open pond system possesses high surface area per volume ratio allowing the high CO2 mitigation. Additionally, if the nutrient sources used is wastewater, incorporated with CO2 supplied from flue gas, the open pond system is usually applied. It provides effective wastewater treatment concurrently. Nevertheless, open 15

pond system suffered some drawbacks whereby it requires significant land area, the culture is subjected to high risk of contamination or predators and the evaporative water lost can be significant due to the open structure. Thus, some ponds are covered with transparent material to promote growing period of microalgae, prevent evaporation loss and facilitate CO2 distribution. 4.1.1 Raceway ponds Raceway pond, an open pond system looks like race track, usually shallow with 15 to 25 cm in depth. It is equipped with paddle wheel agitation, so as to ensure good circulation and nutrients homogenisation. In addition, the flow of culture is controlled and guided with baffles placed in the flow channel (Ho et al., 2010; Lam & Lee, 2011). This promotes the liquid velocity of the ponds are to be operated with more than 30 cm per second (Razzak et al., 2013). Raceway ponds are presently the most commonly used large scale cultivation system for commercial scale. It is used for commercial culturing of Chlorella sp., Spirulina platensis, Hematococcis sp. and Dunaliella salina. If compared to closed photobioreactor system, raceway cultivation produced low biomass productivity of Chlorella sp. and Spirulina sp. due to carbon limitation, as only 5% of carbon is directly transferred by atmospheric air (De Godos et al., 2014). In order to achieve outstanding carbon sequestration, the microalgal farms can be placed surrounding the industrial plant, so as to utilise CO2 in the flue gas efficiently (McGinn et al., 2011). 4.1.2 Multi-layer bioreactor Multi-layer bioreactor system has been considered as feasible and cost-effective cultivation system in treating wastewater. It comprises of several tier of tanks, arranging one on top to the other. The pilot scale of multi-layer ponds has been achieved up to 2000 L to 40000 L capacity (Zhou et al., 2014). It has been successfully used for microalgae cultivation in centrate and animal manure wastewaters (Zhou et al., 2014). The medium are flowing from tank at the

16

top to the bottom tank by gravity, undergo mixing and pump up to circulate medium back to the top tank again. Apart from sunlight radiation, artificial light can also be installed at the top of every layer with tank, so as to ensure sufficient light supply. The benefits of the cultivation systems include less space requirement as it arrange in tiers, easy to scale up and cost-effective, while the limitations are similar to the other types of open pond systems. 4.2 Closed system Closed photobioreactors (PBR) have gained much interest by researchers due to better control of cultivation parameters and capability to satisfy carbon requirement. It was also evident that PBR cultivation has achieved high photosynthetic efficiency and biomass productions compared to open pond system (Chen et al., 2014a). These advantages are even more important if the desired microalgae are used for pharmaceutical purposes or highly selective products applications (Fernandes et al., 2014). PBRs are designed in configuration to maximise photosynthetic efficiency and CO2 mass transfer efficiency; minimise cultivation dark zone and power consumption (Ho et al., 2012). The PBRs used are summarised in the following sections. 4.2.1 Airlift photobioreactor In airlift PBR, the liquid volume in the vessel is separated into two connected zones by baffle. The liquid is moved in the circulatory flow caused by the CO2 supply at the bottom of the reactor (Razzak et al., 2013). It gave the most fixation efficiency due to its relatively better mass transfer and circulation (Ho et al., 2011). This provides the high cycling of medium with low surface area exposed for light radiation, thus resulting in minimum photoinhibition. With pressurised gas-liquid system incorporated to generate fine bubbles into the reactor, CO2 concentration can be regulated easily rather than using baffles as in open pond system. Additionally, in optimised PBR, generated microbubbles exert higher surface area to volume ratio, slow rising in the medium, leading to better dissolution of gas into liquid (Lam et al., 17

2012). The microbubbles can rising gradually and collapse in the medium, rather than macrobubbles rising rapidly and burst on the surface of medium to the atmosphere. Airlift PBR is effectively in gas hold-up, yet it is difficult to scale up as it possess high cell shear effect, difficult in temperature control, complex liquid flow pattern and high operation cost. In order to address these limitations, split column airlift PBR was introduced recently, by integrating temperature control system and light transport internally at the centre of the airlift PBR (Fernandes et al., 2014). This central flat plate provides illuminated surface in the medium, serves as the central baffle to prevent dark zone and functions as heat exchanger to ensure better temperature control. Fernandes et al. (2014) reported that the biomass productivity of microalgae cultivated in spit column airlift PBR was 15-36% higher than in conventional bubble column. 4.2.2 Tubular photobioreactor Tubular PBR system is the most noticeable system for large scale outdoor cultivation (Ho et al., 2011). Tubular PBRs are made up of transparent materials and placed in outdoors under sunlight radiation. The microalgae are cultivated in the vessel, permitting the addition of air, CO2, and nutrients into the medium; and O2 removal by reactor. The medium is circulated through tubes and back to reservoir in high turbulent flow, by using mechanical pump. The flow rate in the tube is ranging from 30 cm s-1 to 50 cm s-1, to ensure CO2 distribution, light/dark cycle and prevent cell deposition (Razzak et al., 2013). A portion of microalgae is usually harvested after it circulated through solar collection tubes. The tubes are generally 5-20 cm in diameter to enabling sunlight penetration, thus producing higher microalgal productivities (Razzak et al., 2013; Zhao & Su, 2014). Though it is often considered as the most suitable for microalgae cultivation, the reactor size and length are limited to parameter control, O2 removal and CO2 depletion (Ho et al., 2011). To date, the maximum capacity it can achieve is about 20 L. Further

18

increase in concentration culture has resulted in the increase tube length and diameter. Thus, it is difficultly to scale up and the only solution is to multiply the reactor units. 4.2.3 Flat plate photobioreactor Flat plate PBR has large surface area per volume ratio allowing large irradiated zone, cost effective, large volume culture and excellent biomass productivities. Flat plate PBR has achieved short light path and steep light gradients, and can be further enhanced by addition of baffles for aeration towards light gradient (Ho et al., 2011). The aeration rate using bubbling technique can be expressed in gas volumetric flow rate per unit volumetric culture medium (vvm). The optimum aeration rate of 0.023-1.000 vvm was proposed for 5% (v/v) or 10% (v/v) CO2 aeration and 0.05 vvm is appropriate for flat-plate PBR (Zhao & Su, 2014). Flat plate PBR is scalable, accommodating 1000 – 2000 L capacity. Limitations include difficulty in temperature control, limited degree of growth at the near wall region and hydrodynamic stress (Razzak et al., 2013). 4.2.4 Bag photobioreactor Bag PBR is a semi-continuous PBR, cultivating microalgae in transparent polyethylene bags. The bags are hung and placed in the cage with multiple partitions, located under the sunlight. The air is sparged from the bottom of the bags, together with sealing the bags in conical shape at the bottom, to prevent settling of cells (Razzak et al., 2013). This is commonly used in lab scale before proceeding to outdoor pilot plant. 4.2.5 Membrane photobioreactor Membrane PBR is basically the integration of membrane into the air lift or tubular PBR to produce fine bubbles for better CO2 mass transfer into the medium. The membrane exerts large surface area, with microspores that will generate fine bubbles with diameter 5.5-10.1 mm (Lam et al., 2012). An ideal membrane PBR should be (i) easy to install; (ii) good CO2

19

distribution while preventing O2 build up; (iii) membrane has to be resistance to alkaline and acidic conditions; (iv) less membrane fouling; (v) high durability. Hollow fiber membrane was integrated in airlift PBR to investigate the effects of membrane porosity on CO2 fixation rate. It was observed that low porosity of membrane provides better CO2 mass transfer, resulting in higher CO2 fixation rate (Lam et al., 2012). This is due to the generation of microbubbles by low porosity membrane were collapse in the medium, providing better CO2 mass transfer. With membrane system, lower CO2 gas pressures are sufficient to be implemented while producing same biomass productivity (Merriman et al., 2014). CO2 bubbling is less effective if compared with membrane PBR (Rahaman et al., 2011). Hydrophobic hollow fiber membrane even contributed better CO2 transfer and exerts lesser dissolved oxygen in the medium (Merriman et al., 2014). Yet, the dispersion of fine bubbles creating a cloudy condition inside the reactor reduces in light penetration. The solution to address this limitation is by separating the gas and light delivery systems into two individual systems (Lam et al., 2012; Rahaman et al., 2011). 4.2.6 Filtration photobioreactor Filtration PBR is developed recently whereby microalgal cells are attached and grow on the membrane in the cultivation tank. Apparently, the concept is originated by biofilm system, allowing microalgae and bacteria to attach on growth media, entrapped by extracellular polymeric substances excreted by themselves (Zhang et al., 2014). Filtration PBR comprises of a transparent cultivation tank and a recycle tank, separated by a membrane between them. The initial operation of filtration PBR requires inoculated microalgae cells suspended in the cultivation tank. As medium feeding through the membrane, the microalgae cells are filtered and attached on the membrane, forming biomass. Microalgal cells can be easily washed off by the flowing liquid medium, subsequently viable cells can be harvested. The liquid medium is then recycled from recycle tank and recirculated back to the cultivation tank continuously. This 20

system is easy to start up and enable elimination of the harvesting cost for the downstream processing biomass applications. However, the flow rate of medium has to be controlled, so as to create minimal disturbance to the even distribution and attachment of the microalgae. Chlorella sp. cultivated using filtration PBR showed highest productivity, 13.56 gm

-2

d-1 in 7.5% (v/v)

CO2, at 35°C (Zhang et al., 2014). Furthermore, majority of PBR employ degasser to release dissolved oxygen (DO). In order to ensure effective gas-liquid separation, the path to degasser is required to enable sufficient time for the release of small bubbles from the medium (Kumar et al., 2010). Additionally, gas bubbling in sodium sulfite solution before it return to the reactor is required, so as to prevent DO accumulation. Rahaman et al. (2011) also reported on the utilisation of selective polymer-membrane gas separation system to incorporate with the PBR, to capture the atmospheric CO2. Polyethylenimine and ionic liquids which can be switched to polymer form have shown good performance in CO2 capturing (Rahaman et al., 2011). Overall, excellent microalgae cultivation system should be universal for cultivating various microalgae species, able to supply permanent solar energy illumination, high CO2 mass transfer, prevent contamination, low energy and low cost of operation. The life cycle assessment is essential to address the energy consumption and CO2 balance for each process of the microalgal cultivation system. Table 3 summarises the variation in properties of different cultivation systems. Bag PBR (Table 3) seems to be the most potential cultivation system to be applied, whereby it achieves most of the listed criteria. It needs low cost and low energy consumption as in open pond systems, meanwhile retaining the advantages as in closed system. Additionally, bag PBR is made up of transparent polyethylene bags, enabling the cells to obtain light supply from all angles without any blockage that tends to cause cell shading. If to be

21

compared among the open pond systems which are more desirable for larger scale microalgal cultivation, the multi-stage bioreactor will be the best choice. Although it involves energy consumption for medium pumping and mixing, the land space used is very minimum compared to other open pond systems. Moreover, unlike raceway pond, artificial lights are installed on top of every tier of tanks allowing good light penetration into the medium. The flowing of medium from the top tank to the lower tank by energy-free gravity force is also contributing to the CO2 gas transfer and ensures liquid medium homogenisation. 5. Inhibition of toxic pollutants in flue gas Despite microalgae is efficient in CO2 bioconversion with cultivation strategies like costly and energy required CO2 sparging, treated flue gas can become the potential CO2 source for microalgal cultivation. The typical CO2 concentration in flue gas is at 15% (v/v), which is approximately 400 times more concentrated if compared to atmospheric CO2 (Lam & Lee, 2011; McGinn et al., 2011). This has resulted to the usage of flue gas for microalgae cultivation. Chlorella KR-1 was observed to be successfully fixing the actual flue gas discharged from boiler, without any treatment (Singh et al., 2014). This could be due to the characteristics of Chlorella sp. which has strong adaptability on high temperature and low pH of flue gas (Razzak et al., 2013; Zhao & Su, 2014). However, flue gas generated by combustion process of industrial plants generally contains inhibitory toxic pollutants SOx and NOx, which may affect most of the microalgal growth. The following sections describe the inhibition of these pollutants towards microalgae growth. 5.1 Effects of SO2 Flue gas typically comprise of 9.5-16.5% (v/v) CO2, 2-6.5% (v/v) O2, CO, 100-300 ppm NOx, 280-320 ppm SOX, heavy metals and particulate matter (Lam et al., 2012; Lee et al., 2000).

22

SO2 derived from SOx, hydrolysed in water forming hydrogen ions which tend to cause pH reduction of the culture medium. SO42- and HSO4- derived from SO2 hydrolysis are also the inhibition factors affecting microalgae growth. SO2 with concentration exceeding 100 ppm and 60 ppm, respectively, inhibit the growth of almost all kinds of microalgae species (Zhao and Su, 2014; Lam et al., 2012). The growth of Chlorella KR-1 were completely suppressed and inhibited in 150 ppm SO2 condition (Lee et al., 2000). Apart from pollutants concentration, the inhibition effect of SOx varies greatly depending on the source of flue gas. The flue gas generated from different industries; exert differences in toxicity level (Lam et al., 2012). In overall, the inhibition effects are depending on the characteristics of microalgae species, growth conditions and pollutants’ concentrations with its toxicity. Table 4 summarises the inhibition effects of microalgae species cultivated using flue gas with SOx and NOx compounds. The Chlorella sp. and Scenedesmus sp. listed in Table 4 (no.3-9) have shown to be the most prominent microalgae with only slight and no growth inhibition effect towards the CO2, SOx and NOx concentrations. The growth of Chlorella sp. MTF-15 was slightly inhibited by more than 24% (v/v) CO2 concentration (Kao et al., 2014). This was confirmed when the biomass production of Chlorella sp. MTF-15 was optimised when cultivated using diluted flue gas. In overall, this has proved that Chlorella sp. and Scenedesmus sp. are indeed efficient in mitigation of CO2, SOx and NOx pollutants from emission, provided that CO2 concentration in flue gas is not exceeding 24% (v/v). Mixed culture grown in high rate algal pond which is used for treating diluted swine manure, shown approximately 30% increase in biomass productions when flue gas was supplied (De Godos et al., 2010). Apparently, microalgal species are capable in bio-fixing CO2 and remove SO2, NO2 and VOC concurrently (Ho et al., 2011; Kao et al., 2014; Van Den Hende et al., 2012). This process could be considered as

23

phytoremediation in industrial plant with its cost-effective way of pretreating flue gas before direct emission. Nevertheless, there are also microalgae species especially isolates, which can withstand the inhibition of SO2 though undergoing longer lag phase for adaptability. Or else, pH adjustment can be made to neutralise the medium back to its optimal range. Alternately, desulfurisation unit can be installed to remove SO2 prior to flue gas supply for cultivation. There are dry and wet desulfurization processes, which involve uses of CaO sorbent and limestone-gypsum method, respectively (Lee et al., 2005). 5.2 Effects of NOX The NOx in flue gas emitted from industrial plant typically contains 5-10% (v/v) of NO2 and 90-95% (v/v) of NO (Zhao and Su, 2014). In general, microalgae can assimilate nitrogen in the form of NO3-, NO2-, NO, N2 and NH4+ (Van Den Hende et al., 2012). The major constituent in NOx which is NO is unlike SO2, as it hardly possesses direct impact to the microalgae growth. Tetraselmis sp. was able to grow under flue gases containing 185 ppm SOx, 125 ppm NOx and 14.1% (v/v) CO2 (Kumar et al., 2010). It can tolerate NO in high concentration which is up to 300 ppm because NO is not directly inhibiting the microalgal growth (Kumar et al., 2010). The growth of Chlorella sp. can be affected only with above 300 ppm of NO supply (Lee et al., 2000). In fact, the dissolved NO serves as an alternative nitrogen source, can easily being absorbed by culture medium for microalgae growth. Conversely, the positive effect of NO concentration is limited, whereby the increase in NO concentration may decrease the growth rate of most strains, but not to the extent of total inhibition. 5.3 Potential and limitation of using flue gas

24

Capturing CO2 from flue gas has been recognised mainly due to the low atmospheric CO2 concentration. CO2 concentration in the air though has been proven possible to be captured, but in very low concentration. However, as seen in Table 2 (no. 5), the atmospheric concentration of 0.03% (v/v) CO2 without capturing managed to achieve 92.2% removal efficiency compared to 5% (v/v) CO2-sparged conditions (Lam et al., 2012). This could be due to the low solubility of CO2, whereby most sparged CO2 was released back to atmosphere, before even dissolved in medium. Condition is worsening by the evaporative CO2 loss if microalgae were to be cultivated in open pond system (Chen et al., 2014b). The utilisation of flue gas-containing CO2 provides the solution to the mentioned problem, more importantly contribute in CO2 sequestration. Direct utilisation of flue gas serves as the alternatives for providing carbon source for biomass production. Nevertheless, till date, the in situ research on using flue gas from microalgae cultivation is still very limited. Though efforts have been made, yet there are multiple existing challenges and limitations waiting to be resolved, such as high temperature of the flue gas and presence of toxic pollutants. Microalgae species can be screened on their resistance towards toxic pollutants especially on site, as flue gas compositions may vary depending on the materials feed for combustion. High CO2 concentration in flue gas reduces pH of the medium, thus acidophilic microalgae, which are potentially effective in CO2 sequestration should have identified, especially under high loading rates of acidic flue gas compounds (Van Den Hende et al., 2012). Integration of desulfurisation unit can also be installed to minimise the SO2 inhibition effect. Alternative strategy will be encouraging the usage of low sulphur fuel for small scale industrial plants. Moreover, flue gas cooling system and gas distribution system have to be installed aiming to supply the optimal and homogenous CO2 to microalgae. 6. Genetic engineering of microalgae species

25

Apart from utilisation of elevated CO2 from flue gas to enhance microalgal cultivation, genetic engineering approach can be involved to genetically modify microalgae towards enhancing photosynthetic efficiency and CO2 fixation efficiency. There are researches developed for transgene expression and gene knockdown for microalgae which pose greater interest in industrial application (Zeng et al., 2011). Microalgae strains were modified by reducing the size of light-harvesting chlorophyll antenna, so as to absorb more light for photosynthesis and reduce photoinhibition (Lee et al., 2002; Ho et al., 2011; Zeng et al., 2011). As reported by Lee et al. (2002), antenna-deficient strain Chlamydomonas sp. was achieved greater CO2 photoassimilation if compared to a wild type species in a light saturated condition. Besides, the lipid synthesis gene overexpression may improve microalgal lipid synthesis, but may cause cell division reduction and lower biomass productions. Inducible promoter has to be activated at microalgal growth stationary phase aiming in controlling lipid anabolism in microalgal cells (Zeng et al., 2011). Additionally, knocking down of enzyme genes which causing lipid catabolism has been reported as effective in increasing lipid accumulation in cells. 7. Downstream biomass applications Successful microalgae cultivation systems, apart from CO2 sequestration, have also contributing to microalgae biomass productions which benefiting the people. This bio-refinery concept is introducing the application of microalgal biomass to produce biofuel, energy and value added products like human food supplement and medical drugs (Zhou et al., 2014). The utilisation of microalgae is mainly due to its cellular components which are rich in protein, lipids and carbohydrates. For instances, fatty acids and microalgae extracts are used in cosmetics, carotenoids used as dye pigments, poly-β-hydroxybutyrate used in plastics, polysaccharides used as food thickening agent, eicosapentanoic acid used as medical drugs, Omega-3 fatty acids for

26

nutritional supplement and glycerol used in food (Kumar et al., 2010). The microalgae species that commonly used for commercialised applications include Chlorella sp., Dunaliella salina, Botryococcus braunii, Spirulina plantensis, Haematococcus pluvialis, Arthrospira sp. and Nannochloropsis sp. (Ho et al., 2011). At present, thousand tons of biomass is produced yearly for commercial application by using open pond cultivation system. Nevertheless, the application of biomass produced by genetically modified microalgal species is greatly affected by the purpose of application. For instances, toxicity tests are required if biomass is used to produce cosmetic products and food supplement, but not necessarily required for biofuel production. Biofuel is undeniably the energy product mostly associated with microalgal research. Microalgae store significant amount of energy which can be converted into diesel, methane and ethanol via thermal-chemical and biological methods (Ho et al., 2011). Biofuel in-used presently are predicted to be insufficient to satisfy the world energy demand in the near future. The diminishment of natural resources, such as petroleum and coal, is soon to be occurred (Bhatt et al., 2014). Microalgae are known as the valuable feedstock for renewable energy production, due to their high growth rates and high lipid productivities (McGinn et al., 2011; Rogers et al., 2014). The cellular lipid contents of microalgae can reach up to 70% per cell (Pires et al., 2012). For instance, Scenedesmus sp. is the promising microalgae for CO2 sequestration, bio-oil production, carotenoids and pigments production for health food application (Ho et al., 2011). Additionally, microalgae are also the feedstock used for bioethanol production, as their carbohydrates and proteins serve as the carbon source for fermentation. Subsequently after the fermentation process, the remaining microalgae biomass can be further used for bio-methane generation via anaerobic digestion (Lam & Lee, 2011; Zhou et al., 2014).

27

Microalgae gain elevated the CO2 supply by utilising of flue gas which could contains significant amount of SOx and NOx pollutants. The production of biofuel using these microalgae is allowable with no effect on combustion. Conversely, bio-refinery approach on microalgal biomass produced from flue gas CO2 bio-conversion is still in a developing field especially for human nutritious supplement and pharmaceutical products. Further efforts like drug toxicity test and safety tests on animals are required to investigate the toxicity of microalgal biomass that could be probably brought by these flue gas pollutants. Notably, the microalgal applications have significantly improve the sustainability and economic feasibility of the microalgal cultivation systems for effective CO2 sequestration. 8. Conclusions Carbon sequestration through CO2 bioconversion is the natural mechanism for microalgae cultivation. Microalgae are able to bio-convert atmospheric CO2 and in particularly CO2 from flue gas, leading to reduction of greenhouse gas emission. This CO2 bio-mitigation will thus minimising the greenhouse effect, leading to ecosystem preservation. Moreover, microalgae contribute to renewable energy and valuables co-products production. Effective carbon sequestration and bio-refinery approach can be achieved towards environmental sustainability and economic feasibility. The innovation of microalgal-based CO2 bio-sequestration is required to bring significant advancement in CO2 bio-mitigation aiming towards global warming solution. Acknowledgments This work is supported financially by SATU Joint Research Scheme (RU022E-2014) from University of Malaya, Malaysia’s Fundamental Research Grant Scheme (FP054-2013B and FRGS/1/2013/SG05/UNIM/02/1), Malaysia’s Ministry of Science, Technology, Innovation (SF016-2013 and MOSTI-02-02-12-SF0256), Taiwan's Ministry of Science and Technology

28

(MOST 103-3113-E-006-006 and MOST 103-2221-E-006-190-MY3) and Taiwan's Ministry of Education on Top University Grants. References 1. Anjos, M., Fernandes, B.D., Vicente, A.A., Teixeira, J.A., Dragone, G. 2013. Optimization of CO2 bio-mitigation by Chlorella vulgaris. Bioresour Technol, 139, 149-54. 2. Bhatt, N.C., Panwar, A., Bisht, T.S., Tamta, S. 2014. Coupling of Algal Biofuel Production with Wastewater. The Scientific World Journal, 2014. 3. Chen, W.-H., Huang, M.-Y., Chang, J.-S., Chen, C.-Y. 2014a. Thermal decomposition dynamics and severity of microalgae residues in torrefaction. Bioresource technology, 169(0), 258-264. 4. Chen, W.-H., Wu, Z.-Y., Chang, J.-S. 2014b. Isothermal and non-isothermal torrefaction characteristics and kinetics of microalga Scenedesmus obliquus CNW-N. Bioresource technology, 155(0), 245-251. 5. Cheng, J., Huang, Y., Feng, J., Sun, J., Zhou, J., Cen, K. 2013. Improving CO2 fixation efficiency by optimizing Chlorella PY-ZU1 culture conditions in sequential bioreactors. Bioresource technology, 144, 321-327. 6. Chiang, C.-L., Lee, C.-M., Chen, P.-C., 2011. Utilization of the cyanobacteria Anabaena sp. CH1 in biological carbon dioxide mitigation processes. Bioresource Technology, 102, 5400–5405. 7. Chiu, S.-Y., Kao, C.-Y., Chen, C.-H., Kuan, T.-C., Ong, S.-C., Lin, C.-S. 2008. Reduction of CO2 by a high-density culture of Chlorella sp. in a semicontinuous photobioreactor. Bioresource technology, 99(9), 3389-3396. 8. Chiu, S.-Y., Kao, C.-Y., Tsai, M.-T., Ong, S.-C., Chen, C.-H., Lin, C.-S. 2009a. Lipid accumulation and CO2 utilization of Nannochloropsis oculata in response to CO2 aeration. Bioresource technology, 100(2), 833-838. 9. Chiu, S.-Y., Tsai, M.-T., Kao, C.-Y., Ong, S.-C., Lin, C.-S. 2009b. The air-lift photobioreactors with flow patterning for high-density cultures of microalgae and carbon dioxide removal. Engineering in life sciences, 9(3), 254-260. 10. Chiu, S.-Y., Kao, C.-Y., Huang, T.-T, Lin, C.-J., Ong, S.-C., Chen, C.-D., Chang, J.-S., Lin, C.-S. 2011. Microalgal biomass production and on-site bioremediation of carbon dioxide, nitrogen oxide and sulfur dioxide from flue gas using Chlorella sp. cultures. Bioresource technology, 102, 9135-9142. 11. De Godos, I., Blanco, S., Garcia-Encina, P.A., Becares, E., Munoz, R. 2010. Influence of flue gas sparging on the performance of high rate algae ponds treating agro-industrial wastewaters. J Hazard Mater, 179(1-3), 1049-54. 12. De Godos, I., Mendoza, J., Acién, F., Molina, E., Banks, C., Heaven, S., Rogalla, F. 2014. Evaluation of carbon dioxide mass transfer in raceway reactors for microalgae culture using flue gases. Bioresource technology, 153, 307-314. 13. De Morais, M.G., Costa, J.A.V. 2007. Biofixation of carbon dioxide by Spirulina sp. and Scenedesmus obliquus cultivated in a three-stage serial tubular photobioreactor. Journal of Biotechnology, 129(3), 439-445.

29

14. Doucha, J., Straka, F., Lívanský, K. 2005. Utilization of flue gas for cultivation of microalgae (Chlorella sp.) in an outdoor open thin-layer photobioreactor. Journal of Applied Phycology, 17, 403-412. 15. Fan, L.-H., Zhang, Y.-T., Zhang, L., Chen, H.-L. 2008. Evaluation of a membrane-sparged helical tubular photobioreactor for carbon dioxide biofixation by Chlorella vulgaris. Journal of Membrane Science, 325, 336-345. 16. Fernandes, B.D., Mota, A., Ferreira, A., Dragone, G., Teixeira, J.A., Vicente, A.A. 2014. Characterization of split cylinder airlift photobioreactors for efficient microalgae cultivation. Chemical Engineering Science, 117, 445-454. 17. Gonçalves, A.L., Simões, M., Pires, J.C.M. 2014. The effect of light supply on microalgal growth, CO2 uptake and nutrient removal from wastewater. Energy Conversion and Management, 85, 530-536. 18. Ho, S.-H., Chan, M.-C., Liu, C.-C., Chen, C.-Y., Lee, W.-L., Lee, D.-J., Chang, J.-S. 2014a. Enhancing lutein productivity of an indigenous microalga Scenedesmus obliquus FSP-3 using light-related strategies. Bioresource technology, 152(0), 275-282. 19. Ho, S.-H., Chang, J.-S., Lai, Y.-Y., Chen, C.-N.N. 2014b. Achieving high lipid productivity of a thermotolerant microalga Desmodesmus sp. F2 by optimizing environmental factors and nutrient conditions. Bioresource technology, 156(0), 108-116. 20. Ho, S.-H., Chen, C.-N.N., Lai, Y.-Y., Lu, W.-B., Chang, J.-S. 2014c. Exploring the high lipid production potential of a thermotolerant microalga using statistical optimization and semi-continuous cultivation. Bioresource technology, 163, 128-135. 21. Ho, S.-H., Chen, C.-Y., Chang, J.-S. 2012. Effect of light intensity and nitrogen starvation on CO2 fixation and lipid/carbohydrate production of an indigenous microalga Scenedesmus obliquus CNW-N. Bioresource technology, 113, 244-252. 22. Ho, S.-H., Chen, C.-Y., Lee, D.-J., Chang, J.-S. 2011. Perspectives on microalgal CO2emission mitigation systems—A review. Biotechnology Advances, 29(2), 189-198. 23. Ho, S.-H., Chen, W.-M., Chang, J.-S. 2010. Scenedesmus obliquus CNW-N as a potential candidate for CO2 mitigation and biodiesel production. Bioresource technology, 101(22), 8725-8730. 24. Ho, S.-H., Huang, S.-W., Chen, C.-Y., Hasunuma, T., Kondo, A., Chang, J.-S. 2013. Bioethanol production using carbohydrate-rich microalgae biomass as feedstock. Bioresource technology, 135, 191-198. 25. Jiang, L.-L., Luo, S.-J., Fan, X.-L., Yang, Z.-M., Guo, R.-B. 2011. Biomass and lipid production of marine microalgae using municipal wastewater and high concentration of CO2. Applied Energy, 88(10), 3336-3341. 26. Jiang, Y.-L., Zhang, W., Wang, J.-F., Chen, Y., Shen, S.-H., Liu, T.-Z. 2013. Utilization of simulated flue gas for cultivation of Scenedesmus dimorphus. Bioresource technology, 128, 359-364. 27. Kao, C.-Y., Chen, T.-Y., Chang, Y.-B., Chiu, T.-W., Lin, H.-Y., Chen, C.-D., Chang, J.-S., Lin, C.-S. 2014. Utilization of carbon dioxide in industrial flue gases for the cultivation of microalga Chlorella sp. Bioresource technology, 166(0), 485-493. 28. Kaštanek, F., Šabata, S., Šolcová, O., Maléterová, Y., Kaštanek, P., Brányiková, I., Kuthan, K., Zachleder, V. 2010. In-field experimental verification of cultivation of microalgae Chlorella sp. using the flue gas from a cogeneration unit as a source of carbon dioxide. Waste Management and Research, 28, 961-966. 30

29. Knudsen, J.N., Jensen, J.N., Vilhelmsen, P.J., Biede, O. 2009. Experience with CO2 capture from coal flue gas in pilot-scale: Testing of different amine solvents. Energy Procedia, 1(1), 783-790. 30. Kumar, A., Ergas, S., Yuan, X., Sahu, A., Zhang, Q., Dewulf, J., Malcata, F.X., Van Langenhove, H. 2010. Enhanced CO2 fixation and biofuel production via microalgae: recent developments and future directions. Trends in biotechnology, 28(7), 371-380. 31. Lam, M.K., Lee, K.T. 2011. Renewable and sustainable bioenergies production from palm oil mill effluent (POME): win–win strategies toward better environmental protection. Biotechnology Advances, 29(1), 124-141. 32. Lam, M.K., Lee, K.T., Mohamed, A.R. 2012. Current status and challenges on microalgaebased carbon capture. International Journal of Greenhouse Gas Control, 10, 456-469. 33. Lee, J.-N., Lee, J.-S., Shin, C.-S., Park, S.-C., Kim, S.-W. 2000. Methods to enhance tolerances of Chlorella KR-1 to toxic compounds in flue gas. Twenty-First Symposium on Biotechnology for Fuels and Chemicals. Springer. pp. 329-342. 34. Lee J.W., Mets, L., Blankinship, S.L., Greenbaum, E. 2002. Improvement of photosynthetic CO2 fixation at high light intensity through reduction of chlorophyll antenna size. Appl Biochem Biotechnol, 98, 37-48. 35. Lee, K.T., Bhatia, S., Mohamed, A.R. 2005. Preparation and characterization of sorbents prepared from ash (waste material) for sulfur dioxide (SO2) removal. Journal of material cycles and waste management, 7(1), 16-23. 36. Li, F.-F., Yang, Z.-H., Zeng, R., Yang, G., Chang, X., Yan, J.-B., Hou, Y.-L. 2011. Microalgae capture of CO2 from actual flue gas discharged from a combustion chamber. Industrial & Engineering Chemistry Research, 50(10), 6496-6502. 37. López, C.V.G., Fernández F.G.A., Sevilla, J.M.F., Fernández J.F.S., García M.C.C., Grima, E.M. 2009. Utilization of the cyanobacteria Anabaena sp ATCC 33047 in CO2 removal processes. Bioresource technology, 100, 5904-5910. 38. McGinn, P.J., Dickinson, K.E., Bhatti, S., Frigon, J.C., Guiot, S.R., O’Leary, S.J. 2011. Integration of microalgae cultivation with industrial waste remediation for biofuel and bioenergy production: opportunities and limitations. Photosynthesis research, 109(1-3), 231-247. 39. Merriman, L., Moix, A., Beitle, R., Hestekin, J. 2014. Carbon dioxide gas delivery to thinfilm aqueous systems via hollow fiber membranes. Chemical Engineering Journal, 253, 165-173. 40. Pires, J.C.M., Alvim-Ferraz, M.C.M., Martins, F.G., Simoes. 2012. Carbon-dioxide-capturefrom-flue-gases-using-microalgae-Engineering-aspects-and-biorefinery-concept. Renewable and Sustainable Energy Reviews, 16, 3043-3053. 41. Rahaman, M.S.A., Cheng, L.-H., Xu, X.-H., Zhang, L., Chen, H.-L. 2011. A review of carbon dioxide capture and utilization by membrane integrated microalgal cultivation processes. Renewable and Sustainable Energy Reviews, 15(8), 4002-4012. 42. Ramkrishnan, U., Bruno, B., Ramkrishnan, S.S. 2014. Sequestration of halotolerant algae. Journal of Environmental Health Science & Engineering, 12:81 http://www.ijehse.com/content/12/1/81 43. Ramanan, R., Kannan, K., Deshkar, A., Yadav, R., Chakrabarti, T. 2010. Enhanced algal CO2 sequestration through calcite deposition by Chlorella sp. and Spirulina platensis in a mini-raceway pond. Bioresource technology, 101(8), 2616-2622.

31

44. Razzak, S.A., Hossain, M.M., Lucky, R.A., Bassi, A.S., De Lasa, H. 2013. Integrated CO2 capture, wastewater treatment and biofuel production by microalgae culturing—A review. Renewable and Sustainable Energy Reviews, 27, 622-653. 45. Rinanti, A., Dewi, K., Kardena, E., Astuti, D.I. 2014. Biotechnology Carbon Capture and Storage (CCS) by Mix-culture Green Microalgae to Enhancing Carbon Uptake Rate and Carbon Dioxide Removal Efficiency with Variation Aeration Rates in Closed System Photobioreactor. Jurnal Teknologi, 69(6), 105-109. 46. Rogers, J.N., Rosenberg, J.N., Guzman, B.J., Oh, V.H., Mimbela, L.E., Ghassemi, A., Betenbaugh, M.J., Oyler, G.A., Donohue, M.D. 2014. A critical analysis of paddlewheeldriven raceway ponds for algal biofuel production at commercial scales. Algal Research, 4, 76-88. 47. Ronda, S.R., Kethineni, C., Parupudi, L.C.P., Thunuguntla, V.B.S., Vemula, S., Settaluri, V.S., Allu, P.R., Grande, S.K., Sharma, S., Kandala, C.V. 2014. A growth inhibitory model with SOx influenced effective growth rate for estimation of algal biomass concentration under flue gas atmosphere. Bioresource technology, 152, 283-291. 48. Ryu, H.J., Oh, K.K., Kim, Y.S. 2009. Optimization of influential factors for the improvement of CO2 utilization efficiency and CO2 mass transfer rate. Journal of Industrial and Engineering Chemistry, 15(4), 471-475. 49. Singh, S.P., Singh, P. 2014. Effect of CO2 concentration on algal growth: A review. Renewable and Sustainable Energy Reviews, 38, 172-179. 50. Singh, U.B., Ahluwalia, A. 2013. Microalgae: a promising tool for carbon sequestration. Mitigation and Adaptation Strategies for Global Change, 18(1), 73-95. 51. Sydney, E.B., Sturm, W., De Carvalho, J.C., Thomaz-Soccol, V., Larroche, C., Pandey, A., Soccol, C.R. 2010. Potential carbon dioxide fixation by industrially important microalgae. Bioresour Technol, 101(15), 5892-6. 52. Van Den Hende, S., Vervaeren, H., Boon, N. 2012. Flue gas compounds and microalgae:(Bio-) chemical interactions leading to biotechnological opportunities. Biotechnology Advances, 30(6), 1405-1424. 53. Wilbanks, T.J., Fernandez, S. 2014. Climate Change and Infrastructure, Urban Systems, and Vulnerabilities: Technical Report for the US Department of Energy in Support of the National Climate Assessment. Island Press. 54. Xie, Y.-P., Ho, S.-H., Chen, C.-Y., Chen, C.-N.N., Liu, C.-C., Ng, I.-S., Jing, K.-J., Yang, S.C., Chen, C.-H., Chang, J.-S., Lu, Y.-H. 2014. Simultaneous enhancement of CO2 fixation and lutein production with thermo-tolerant Desmodesmus sp. F51 using a repeated fed-batch cultivation strategy. Biochemical Engineering Journal, 86, 33-40. 55. Yeh, K.-L., Chang, J.-S. 2011. Nitrogen starvation strategies and photobioreactor design for enhancing lipid content and lipid production of a newly isolated microalga Chlorella vulgaris ESP-31: implication for biofuel. Biotechnology Journal, 6, 1358-1366. 56. Yoo, C., Jun, S.-Y., Lee, J.-Y., Ahn, C.-Y., Oh, H.-M. 2010. Selection of microalgae for lipid production under high levels carbon dioxide. Bioresource technology, 101(1), S71-S74. 57. Yoo, H.M., Al-Attiyah, H.M. 2013. United Nations Framework Convention on Climate Change. 58. Zeng, X.-H., Danquah, M.K., Chen, X.D., Lu, Y.-H. 2011. Microalgae bioengineering: From CO2 fixation to biofuel production. Renewable and Sustainable Energy Reviews, 15(6), 3252-3260. 32

59. Zhang, D., Fung, K.Y., Ng, K.M. 2014. Novel Filtration Photobioreactor for Efficient Biomass Production. Industrial & Engineering Chemistry Research, 53(33), 1292712934. 60. Zhao, B.-T., Su, Y.-X. 2014. Process effect of microalgal-carbon dioxide fixation and biomass production: A review. Renewable and Sustainable Energy Reviews, 31, 121-132. 61. Zhou, W.-G., Chen, P., Min, M., Ma, X.-C., Wang, J.-H., Griffith, R., Hussain, F., Peng, P., Xie, Q.-L., Li, Y., Shi, J., Meng, J.-Z., Ruan, R. 2014. Environment-enhancing algal biofuel production using wastewaters. Renewable and Sustainable Energy Reviews, 36, 256-269.

33

Caption of Figures Fig. 1

Light dependent and light independent stage during photosynthesis

Fig. 2

Flowchart relating microalgal-CO2 sequestration and biomass production

O2 CO2

NADPH Sunlight ATP Light dependent stage CalvinBenson cycle

Photosystem I & II Electron transport chain

Water

ADP

Light independent stage

NADP+

Glucose

Fig. 1. Light dependent and light independent stage during photosynthesis

34

CO2 Sequestration

Air

Atmospheric CO2 • CO2 Capture

Biomass Production

Microalgae Cultivation Photosynthesis

Microalgae biomass products •

•

Flue gas

CO2 separation and capture

• •

Microalgae species Physiochemical conditions Cultivation system

• •

Bioenergy and biofuel Biogas Co-products like food supplement

Toxic gas for treatment

Fig. 2. Flowchart relating microalgal-CO2 sequestration and biomass production

35

List of Tables Table 1: The characteristics of algae groups Table 2: Microalgae biomass yield and their CO2 fixation rate or removal percentage Table 3: The variation in properties of different cultivation systems Table 4: The inhibition effects of microalgae species cultivated using flue gas with SOx and NOx compounds

Table 1 The characteristics of algae groups Algae group

Common name Characteristics

Chlorophyceae

Green algae

(i) Estimated 6000 – 8000 species (ii) 90% live in freshwater rather than marine (iii) Ranging from tiny unicellular and colonial organisms to large macroscopic weeds (iv) In monophyletic group as the terrestrial plants

Rhodophyceae

Red algae

(i) Estimated 4000 – 5000 species (ii) 90% live in marine (iii) Ranging from unicellular to macroscopic algae often found on rocky shore (iv) In monophyletic group as the terrestrial plants

Phaeophyceae

Brown algae

(i) Estimated 1500 – 2000 species (ii) Almost all live in marine (iii) Ranging from giant kelps to smaller intertidal seaweeds (iv) Grow in rocky intertidal zone

Cyanophyceae

Blue-green algae

(i) Prokaryotic cell (ii) Present in almost all feasible habitats (iii) CO2 and nitrogen fixers since billion years ago

Bacillariophyceae Diatoms

(i) 12000 known species (ii) Single celled with microscopic in size (iii) Grow in seas, lakes and moist soils and out of glass (silicon dioxide or silicon)

1

Table 2 Microalgae biomass yield and their CO2 fixation rate or removal percentage No

Microalgae species

Initial CO2 (%)(v/v)

CO2 biofixation rate (g L-1 d-1)

Removal percentage (%)

Biomass yield (g L-1)

Cultivation system

References

1 2

Anabaena sp. Anabaena sp.

~ 0.03 (Air) 10

1.45 1.01

-

-

Bubble column Bubble column

3

Botryococcus braunii

5

0.5

-

3.11

Fermenter

4 5

Botryococcus braunii Chlorella vulgaris

10 0.03 (Air)

-

92.2

3.05 ~0.315

6

Chlorella vulgaris

0.09 (Air)

3.45

-

0.9

7

Chlorella vulgaris

2

0.43

-

2.03

8

Chlorella vulgaris

5

0.25

-

1.94

Bioreactor Sequential bioreactor Membranesparged helical tubular bioreactor Vertical tubular bioreactor Fermenter

(Lopez et al., 2009) (Chiang et al., 2011) (Sydney et al., 2010) (Yoo et al., 2010) (Lam et al., 2012)

9

Chlorella vulgaris

5

-

1.5

~0.73

10

Chlorella vulgaris

6

2.22

-

10.02

11

Chlorella sp.

0.038

-

60

0.4

Sequential bioreactor Glass bubble column Lab scale

(Fan et al., 2008)

(Yeh and Chang, 2011) (Sydney et al., 2010) (Lam et al., 2012) (Anjos et al., 2013) (Ramkrishan et al.,

2

12

Chlorella sp.

0.106

-

80

0.7

13

Chlorella sp.

1

-

59

-

14 15

Chlorella sp. Chlorella sp.

2 5

0.857 0.7

-

2.02

16

Chlorella sp.

5

-

51

-

17

Chlorella sp.

10

-

46

2.25

18

Chlorella sp.

10

-

63

5.15

19

Chlorella sp.

15

-

85.6

0.95

20

Chlorella sp.

10

-

46

2.25

21

Dunaliella tertiolecta

5

0.27

-

2.15

22

Nannochloropsis oculata

2-15

-

11-47

0.246-1.32 1

23

Scenedesmus obliquus

10

-

40.2

0.653

24

Scenedesmus obliquus

10

0.55

-

3.51

25

Scenedesmus obliquus

20

0.39

-

2.63

26

Geneticly modified Scenedesmus obliquus

20

-

61.8

0.948

photobioreactor Lab scale photobioreactor Lab scale flask method Bubble column Vertical tubular bioreactor Lab scale flask method Lab scale flask method Air lift photobioreactor Sequential bioreactor Open race-way pond Fermenter

2014) (Ramkrishan et al., 2014) (Ramanan et al., 2010) (Chiu et al., 2008) (Ryu et al., 2009) (Ramanan et al., 2010) (Ramanan et al., 2010) (Chiu et al., 2009a)

(Cheng et al., 2013) (Ramanan et al., 2010) (Sydney et al., 2010) Cylindrical glass (Chiu et al., 2009b) photobioreactor Air lift (Li et al., 2011) photobioreactor Glass-made (Ho et al., 2010) vessel Glass-made (Ho et al., 2010) vessel Air lift (Li et al., 2011) photobioreactor

3

27

Spirulina platensis

1

-

53

-

28

Spirulina platensis

5

-

41

-

29

Spirulina platensis

5

0.32

-

2.18

30

Spirulina platensis

10

-

39

2.91

31

Spirulina platensis

15

0.92

-

2.13

32

Spirulina sp.

6

-

53.29

3.40

33

Spirulina sp.

12

-

45.61

3.50

34

Spirulina obliquus

6

-

28.08

1.58

35

Spirulina obliquus

12

-

13.56

1.60

36

Mixed culture of Chlorella sp., Scenedesmus sp. and Ankistrodesmus sp. Mixed culture of Chlorella sp., Scenedesmus sp. and Ankistrodesmus sp.

5

0.98

59.80

10

0.85

63.10

37

1

Lab scale flask method Lab scale flask method Fermenter

(Ramanan et al., 2010) (Ramanan et al., 2010) (Sydney et al., 2010) (Ramanan et al., 2010) (Knudsen et al., 2009)

Lab scale flask method Hollow fiber membrane photobioreactor Serial tubular photobioreactor Serial tubular photobioreactor Serial tubular photobioreactor Serial tubular photobioreactor

(De Morais & Costa, 2007) (De Morais & Costa, 2007) (De Morais & Costa, 2007) (De Morais & Costa, 2007)

4.90

Vertical photobioreactor

(Rinanti et al., 2014)

5.80

Vertical photobioreactor

(Rinanti et al., 2014)

Data for 2% (v/v) CO2 concentration, growth inhibited for CO2 concentration of higher than 2% (v/v)

4

Table 3 The variation in properties of different cultivation systems

Cultivation system

Cost

Scale-up

Energy consumption

Space

Gas transfer

Light efficiency

Growth rate

Raceway pond Multi-layer bioreactor Airlift photobioreactor Tubular photobioreactor Flat plate photobioreactor Bag photobioreactor Membrane photobioreactor Filtration photobioreactor

Low Middle

Easy Easy

Low Low

High Low

Fair Fair

Low Middle

Low High

High

Difficult

Middle

Low

Good

High

High

High

Difficult

High

Low

Good

High

High

High

Middle

Middle

Low

Good

High

High

Low High

Middle Difficult

Middle Middle

Low Low

Good Good

High High

High High

High

Middle

Middle

Low

Good

High

High

5

Table 4 The inhibition effects of microalgae species cultivated using flue gas with SOx and NOx compounds

No

Microalgal species

CO2 %

NOx (ppm)

SOx (ppm)

Source

Inhibitory effect

Cultivation system

References

(v/v)

1

Nannochloropsis limnetica

10

-

25

Real flue gas from rice husk emission

Inhibited

Bubble column

(Ronda et al., 2014)

2

Nannochloropsis limnetica

3

-

11

Real flue gas from rice husk emission

Inhibited

Bubble column

(Ronda et al., 2014)

3

Chlorella sp.

8-10.2 38

3.8

Real flue gas from cogenerator units

No inhibition

Bubble column

(Kaštanek et al., 2010)

4

Chlorella sp.

6-8

37

-

Real flue gas from combustion of natural gas from boiler

No inhibition

Open thin layer PBR

(Doucha et al., 2005)

5

Chlorella sp.

23

78

87

Real flue gas from coke oven of steel plant

No inhibition

Double set PBR

(Chiu et al., 2011)

6

6

Chlorella sp.MTF-15

25

70-80

80-90

Real flue gas from coke oven of steel plant

Slight inhibition

Columntype glassfabricated PBR

(Kao et al., 2014)

7

Chlorella sp. MTF-15

26

8-10

15-20

Real flue gas from hot stove of steel plant

Slight inhibition

Columntype glassfabricated PBR

(Kao et al., 2014)

8

Chlorella sp. MTF-15

24

25-30

15-20

Real flue gas from power plant of steel plant

Slight inhibition

Columntype glassfabricated PBR

(Kao et al., 2014)

9

Scenesdemus sp.

18

150

200

Real flue gas from combustion chamber of coke oven

No inhibition

Airlift

(Li et al., 2011)

10

7.5 Mixed culture of Scenesdemus sp., Chlorella sp., Nitzschia sp., Chamydomonas sp., Oocystis sp. & Protoderma sp.

77

-

Real flue gas from combustion of natural gas in manure-drying motors

No inhibition

High rate algal pond

(De godos, et al., 2010)

7

Highlights

•

Microalgae are the agent for carbon biosequestration

•

CO2 from flue gas is potential carbon source for microalgae cultivation

•

The effect of inhibition derived by toxic pollutants in flue gas toward microalgae.

•

The advantages and disadvantages of microalgae cultivation system

44