Waste Cooking Oil for Asphalt Modification: Comparison
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Waste cooking oil (WCO) is considered a potential bio-based waste material because it can lead to multiple topologies of the product. WCO is generated after frying activities, and the rising population has increased its quantity due to the increased demand for food. WCO is related to the vegetable oil family and mainly arises from the kitchen and food industry.

  • waste cooking oil
  • transesterification
  • sustainability
  • free fatty acid
  • asphalt binder
  • rheological properties

1. Introduction

Amongst many global issues, the rapid growth of cities and the increasing number of vehicles have dramatically enhanced the demand for pavement construction and maintenance [1]. Around 95% of the world’s roads are made of flexible pavement, and asphalt binder serves as a conventional material for pavement construction [2]. Asphalt binder is a byproduct of crude oil, which is well known as a non-renewable resource. A dramatic increase in the price of petroleum-based binders, due to the depletion of petroleum reserves, forces road authorities to explore alternative materials. Currently, the global practice is moving towards a sustainable, economical, and green environment. The scientific community is interested in optimizing bio resources for renewability, sustainability, and local production in the pavement industry, due to reduced costs and lower energy consumption.

Biomass is the primary source of bio material, whereas biomass refers to living things that store solar energy, such as plants, animals, and microorganisms [3]. Among various forms of biomaterial, bio-oil is a widely accessible material and is categorized as waste oil from the forest/agriculture industry, animal, and residual. Hence, modifying the asphalt binder with bio-oil significantly minimizes the issues regarding non-renewability and fluctuation of binder cost [4]. The compatibility and likelihood of bio-oil modified asphalt are somewhat satisfactory, and its quality differs with source and the content [5]. However, the addition of agricultural waste oil (5–10 wt.%) improves the bio asphalt viscosity and low-temperature properties, whereas there is marginal improvement in the high-temperature properties [6,7][6][7]. Similarly, the waste wood oil-based asphalt mixture improved the anti-fatigue and crack resistance properties [8]. Conversely, animal waste oil is commonly utilized less than 10 wt.% by asphalt to achieve better performance [9,10][9][10]. The addition of animal waste based bio-oil reduces the viscosity and stability of asphalt at higher temperatures and increases low-temperature crack resistance [1]. Yet the agriculture and animal-based oils are subjected to time-consuming and expensive refining procedures, such as pyrolysis and hydrothermal liquefaction [3,11][3][11]. In this way, the current implementation of bio-oil to modify asphalt binder is mainly focused on plant-based oil such as waste cooking oil/waste vegetable oil, as these soft oils are a ready substrate with lower production cost [3,12,13,14][3][12][13][14].

Waste cooking oil (WCO) is considered a potential bio-based waste material because it can lead to multiple topologies of the product [15]. WCO is generated after frying activities, and the rising population has increased its quantity due to the increased demand for food. WCO is related to the vegetable oil family and mainly arises from the kitchen and food industry. The global consumption of vegetable oil in 2021 has reached 209.14 million metric tons, and each year consumption has increased by 2% ( Figure 1 ). In contrast, a significant problem regarding the proper disposal and collection of WCO has still gone unsolved for a long time. The lack of awareness, facilities, and improper disposal of WCO are leading to environmental, ecological, and municipal problems [16,17][16][17]. Hence, by heavily consuming oil and fats, many countries face sewer blockage problems associated with an increased annual cost to remove blockage [18].

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Figure 1. Global vegetable oil consumption worldwide by oil type [19].

Azahar et al. [25][20] investigated the effect of acid value and water content on asphalt binder modification and revealed that chemically treated WCO with lower acid values and water content showed better high-temperature performance. Although, the physical performance of treated WCO was still below the control binder and compromised. To overcome the deficiencies encountered by the WCO-modified binder, researchers recently utilized additional modifiers such as waste polymers, palm oil fuel ash (POFA), and nano clay (NC). It was concluded that WCO-modified binder with other modifiers could withstand hot climate regions. Moreover, a higher percentage of WCO can be used along with additional modifiers to enhance the performance while ensuring a more sustainable environment [29,30,31][21][22][23].

2. Production of Waste Cooking Oil

The vegetable oils market is dominated by palm and soybean oils, which account for 36% and 28% of the market. Other vegetable oil fractions include sunflower (9.09%), rape (13.2%), peanut (2.95%), corn (2.1%), coconut (1.75%), olive (1.48%), and sesame (1.1%) [17]. Amongst all continents, Asia is on top of the list for highest production of vegetable oil. Domestically, edible oil is used for frying purposes, whereas food processing industries and fast food companies largely use oil [32][24]. Frying is a process in which food is fried at a temperature between 150–200 °C in the presence of moisture, anti-oxidants, and pro-oxidants [33][25]. During frying, various reactions occur, such as hydrolysis, polymerization, isomerization, and oil decomposition. After a frying operation, the leftover oil is considered waste material and named waste cooking oil or used cooking oil [34][26]. The rapidly growing world’s population has dramatically increased the food demand that ultimately affects the production of WCO. Recent studies estimate that the generation of waste cooking oil is almost 20–32% of total edible oil consumption [17,35][17][27]. China and India are the most populated countries and produce the most WCO, around 5.6 million tons and 1.135 million tons per year. Canada, Demark, Spain, Italy, Japan, South Korea, Malaysia, and the United Kingdom have average generations, ranging from 0.1–0.5 million tons per year [36][28]. The other remaining countries produce no more than 0.1 million tons per year, and as per capita production of WCO, South Korea is on top of the list, followed by EU countries [17].

3. Free Fatty Acid in Waste Cooking Oil

Edible oil undergoes chemical and physical changes during frying activities, and the quality of the oil degrades. The steam generation during frying reacts with the oxygen and water in the food, initiates the hydrolysis process, and produces the FFA. The concentration of the FFA varies and depends on diverse conditions, such as heating temperature, moisture content, and storage time. Thus, during the additional reaction time the triglyceride bonds break down and produce FFA, including glycerol, diglyceride, and monoglycerides, as shown in Figure 2 . Furthermore, at a temperature above 150 °C, the glycerol accelerates the hydrolysis process, leading to further FFA production [44][29]. As the degradation process continues, the production of FFA accelerates, which ultimately decreases the unsaturation level of the cooking oil. Hence, the oil becomes no longer suitable for further frying and needs to be discarded as waste material [45][30]. The WCO quality can be monitored by the acid value parameter, which identifies the concentration of FFA and the amount of water content [19,46][19][31]. However, researchers have utilized the gas chromatography–mass spectrometry (GC–MS) technique to analyze the concentration of FFA in WCO. The acidic compounds of WCO are categorized as saturated, monounsaturated, and polyunsaturated compounds. The chemical composition of WCO studied by Azahar et al. [47][32] indicated that palmitic acid, stearic acid, and meristic acid are examples of saturated fatty acids, whereas monounsaturated fatty acids contain oleic acid and cis-11-eicosenoic acid. Table 1 indicates that the main components of WCO are oleic acid, palmitic acid, and linoleic acid, which account for 43.67%, 38.35%, and 11.39%, respectively [19,24][19][33].

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Figure 2. Chemical compositions of WCO [19,24,47][19][33][32].
Table 1. Hydrolysis of triglycerides.
Formulation of Fatty Acids Type of Free Fatty Acid Possible % in Waste Cooking Oil (WCO) Type of Saturation
C18:1 (Cis 9) Oleic Acid 43.67 Unsaturated
C16:0 Palmitic acid 38.35 Saturated
C18:2 (Cis) Linoleic acid 11.39 Unsaturated
C18:0 Stearic acid 4.33 Saturated
C14:0 Myristic acid 1.03 Saturated
C18:3 alpha ɣ- Linolenic acid 0.37 Unsaturated
C12:0 Lauric acid 0.34 Saturated
C18:2 t Linolenic acid 0.29 Unsaturated
C20:1 Cis-11-Eicosenoic acid 0.16 Unsaturated
C21:0 Heneicosanoic acid 0.08 Saturated
  TOTAL 100  

4. Available Technologies to Minimize FFA from Waste Cooking Oil

The simplicity of distillation deserves to be described, as it is the most used physical method. The method aims to reduce volatile compounds and water content by taking advantage of the fact that FFA has higher volatility than triglycerides. This process is carried out by simply heating filtered WCO in boiling kettles under vacuum conditions for about ≤90 min [35][27]. Table 2 summarizes key parameters for acidity and water reduction by means of the distillation process. Thus, this process purifies WCO of volatile compounds and water content up to the maximum level. Besides this, another consequence is eliminating other volatile compounds such as ketones, aldehydes, sulfur, and nitrogen. The removal of these undesirable compounds by distillation further improves the quality of WCO [35][27].

Table 2. Water content and acidity value reduction by distillation process.
Reference Temperature (°C) Reduction in Water Content (%) Reduction in FFA (%)
[53][34] 220 From 1.15% to 0.062% From 29% to 2%
[52][35] 200–280 From 5% to 0.1% Less than 0.5%

Transesterification is also known as alcoholysis, and it is the best conventional method for reducing the acid value of WCO by converting the triglycerides of an oil into ester by direct reaction with alcohols. A variety of alcohols can be used, such as methanol, ethanol, butanol, and propanol. Methanol is a more feasible option due to its wide availability, low cost, and quick reaction with triglycerides [59][36]. Generally, a 3:1 molar ratio of alcohol and oil is needed in the transesterification reaction to complete the reaction ( Figure 3 ). The kinetic analysis of the transesterification process is highly challenging, since the reaction is under an equilibrium process. Alcohol must be present in excess in the reaction mixture to shift the reaction towards the formation of the products [60][37]. However, to accelerate the transesterification reaction, commonly used catalysts are sodium hydroxide (NaOH) and potassium hydroxide (KOH). These catalysts are highly demanded for several reasons: cheap price, wide availability, and maximum yield at minimal time duration [61][38]. KOH catalyst reacts faster than NaOH due to strong bonding with alcohol. Tomasevic and Siler-Marinkovic [38][39] investigated the effect of KOH and NaOH as a catalyst; the result concluded that higher conversion of triglycerides was obtained at a 6:1 molar ratio of methanol to oil, a 90 min reaction time, 1% KOH, and 25 °C temperature. On the other hand, ester covers a wide range of end products and can be utilized in different applications, such as biodiesel production, asphalt industry, detergent, and cosmetics [25,41][20][40].

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Figure 3. Base-catalyzed transesterification [62][41].

However, the ultimate maximum ester application of the base catalyst in transesterification has certain limitations, as this process is susceptible to water content and FFA presence in WCO. A higher percentage of FFA reacts with the catalyst, whereas water content partially converts the reaction to saponification, and excessive soap may foam a semi-solid mixture at room temperature, which creates problems during the separation process [60,63][37][42]. Thus, the base catalyst cannot tolerate higher FFA content in WCO, and the desirable range is from less than 0.5 to 1%, as shown in Table 3 .

Table 3. Desirable ranges of FFA.
Author/Reference Recommended FFA (%)
[59][36] Less than 1
[64][43] Less than 0.5
[65][44] Less than 0.5
[66][45] Less than 2
[67][46] Less than 2
[25][20] Less than 1

In recent years, many researchers have been interested in electromagnetic waves utilization. Hence, microwaves are one example of accelerating chemical reactions, such as transesterification/esterification [70][47]. Microwaves can effectively transfer heat to the sample, and this energy completes the reaction. However, in conventional processes, heat is not distributed uniformly, resulting in more energy and time-consumption. Thus, the heat transfer mechanism is more effective than traditional heating [71][48]. Further advantages of microwave irradiation for treating waste oil include a lower alcohol to oil molar ratio, being environmentally friendly, water content removal, and an immediate decrease in FFA [63,72][42][49]. Microwave transesterification of WCO with a high FFA content indicated additional benefits in the separation and purification process between treated oil and residues compared to the conventional method [73][50]. Transesterification of WCO by sodium hydroxide as the catalyst (NaOH) was carried out in a domestic microwave (800 W) under varying parameters, such as molar to ethanol ratio and reaction time. The result indicated that the conversion time of FFA to reduce the acid value of the oil by microwaves is 10 times shorter than the conventional method [71][48].

References

  1. Fini, E.H.; Al-Qadi, I.; You, Z.; Zada, B.; Mills-Beale, J. Partial replacement of asphalt binder with bio-binder: Characterisation and modification. Int. J. Pavement Eng. 2012, 13, 515–522.
  2. Ansari, A.H.; Jakarni, F.M.; Muniandy, R.; Hassim, S.; Elahi, Z. Natural rubber as a renewable and sustainable bio-modifier for pavement applications: A review. J. Clean. Prod. 2021, 289, 125727.
  3. Zhang, X.; Zhang, K.; Wu, C.; Liu, K.; Jiang, K. Preparation of bio-oil and its application in asphalt modification and rejuvenation: A review of the properties, practical application and life cycle assessment. Constr. Build. Mater. 2020, 262, 120528.
  4. Wang, H.; Ma, Z.; Chen, X.; Hasan, M.R.M. Preparation process of bio-oil and bio-asphalt, their performance, and the application of bio-asphalt: A comprehensive review. J. Traffic Transp. Eng. 2020, 7, 137–151.
  5. Aziz, M.A.; Rahman, T.; Hainin, M.R.; Abu Bakar, W.A.W. An overview on alternative binders for flexible pavement. Constr. Build. Mater. 2015, 84, 315–319.
  6. Yang, X.; You, Z.; Dai, Q. Performance evaluation of asphalt binder modified by bio-oil generated from waste wood resources. Int. J. Pavement Res. Technol. 2013, 6, 431–439.
  7. Yang, X. The Laboratory Evaluation of Bio Oil Derived from Waste Resources as Extender for Asphalt Binder. Ph.D. Dissertation, Michigan Technological University, Houghton, MI, USA, 2013.
  8. Mohammad, L.N.; Elseifi, M.A.; Cooper, S.B.; Challa, H.; Naidoo, P. Laboratory Evaluation of Asphalt Mixtures that Contain Biobinder Technologies. Transp. Res. Rec. J. Transp. Res. Board 2013, 2371, 58–65.
  9. Fini, E.H.; Kalberer, E.W.; Shahbazi, A.; Basti, M.; You, Z.; Ozer, H.; Aurangzeb, Q. Chemical Characterization of Biobinder from Swine Manure: Sustainable Modifier for Asphalt Binder. J. Mater. Civ. Eng. 2011, 23, 1506–1513.
  10. Sun, D.; Sun, G.; Du, Y.; Zhu, X.; Lu, T.; Pang, Q.; Shi, S.; Dai, Z. Evaluation of optimized bio-asphalt containing high content waste cooking oil residues. Fuel 2017, 202, 529–540.
  11. Rogers, J.; Brammer, J. Estimation of the production cost of fast pyrolysis bio-oil. Biomass-Bioenergy 2012, 36, 208–217.
  12. Ramadhansyah, P.J.; Masri, K.A.; Azahar, W.N.A.W.; Mashros, N.; Norhidayah, A.H.; Warid, M.N.M.; Satar, M.K.I.M.; Yaacob, H. Waste Cooking Oil as Bio Asphalt Binder: A Critical Review. IOP Conf. Ser. Mater. Sci. Eng. 2020, 712, 012040.
  13. Wen, H.; Bhusal, S.; Wen, B. Laboratory Evaluation of Waste Cooking Oil-Based Bioasphalt as an Alternative Binder for Hot Mix Asphalt. J. Mater. Civ. Eng. 2013, 25, 1432–1437.
  14. Al-Sabaeei, A.M.; Napiah, M.B.; Sutanto, M.H.; Alaloul, W.S.; Usman, A. A systematic review of bio-asphalt for flexible pavement applications: Coherent taxonomy, motivations, challenges and future directions. J. Clean. Prod. 2020, 249, 119357.
  15. Mannu, A.; Garroni, S.; Porras, J.I.; Mele, A. Available Technologies and Materials for Waste Cooking Oil Recycling. Processes 2020, 8, 366.
  16. De Feo, G.; Di Domenico, A.; Ferrara, C.; Abate, S.; Osseo, L.S. Evolution of Waste Cooking Oil Collection in an Area with Long-Standing Waste Management Problems. Sustainability 2020, 12, 8578.
  17. Teixeira, M.R.; Nogueira, R.; Nunes, L.M. Quantitative assessment of the valorisation of used cooking oils in 23 countries. Waste Manag. 2018, 78, 611–620.
  18. Zhao, Y.; Wang, C.; Zhang, L.; Chang, Y.; Hao, Y. Converting waste cooking oil to biodiesel in China: Environmental impacts and economic feasibility. Renew. Sustain. Energy Rev. 2021, 140, 110661.
  19. Zahoor, M.; Nizamuddin, S.; Madapusi, S.; Giustozzi, F. Sustainable asphalt rejuvenation using waste cooking oil: A comprehensive review. J. Clean. Prod. 2021, 278, 123304.
  20. Azahar, W.N.A.W.; Jaya, R.P.; Hainin, M.R.; Bujang, M.; Ngadi, N. Chemical modification of waste cooking oil to improve the physical and rheological properties of asphalt binder. Constr. Build. Mater. 2016, 126, 218–226.
  21. Niu, D.; Xie, X.; Zhang, Z.; Niu, Y.; Yang, Z. Influence of binary waste mixtures on road performance of asphalt and asphalt mixture. J. Clean. Prod. 2021, 298, 126842.
  22. Khan, J.; Hussain, A.; Haq, F.; Ahmad, K.; Mushtaq, K. Performance Evaluation of Modified Bitumen with Replaced Percentage of Waste Cooking Oil & Tire Rubber with Bagasse Ash as Modifier. Civ. Eng. J. 2019, 5, 587.
  23. Adesina, P.A.; Dahunsi, B.I. Blended waste utilization in road construction: Physical characteristics of bitumen modified with waste cooking oil and high-density polyethylene. Int. J. Pavement Res. Technol. 2021, 14, 98–104.
  24. Jamil, F.; Al-Muhtaseb, A.; Myint, M.T.Z.; Al-Hinai, M.; Al-Haj, L.; Baawain, M.; Al-Abri, M.; Kumar, G.; Atabani, A. Biodiesel production by valorizing waste Phoenix dactylifera L. Kernel oil in the presence of synthesized heterogeneous metallic oxide catalyst ( 2). Energy Convers. Manag. 2018, 155, 128–137.
  25. Safari, A.; Salamat, R.; Baik, O.-D. A review on heat and mass transfer coefficients during deep-fat frying: Determination methods and influencing factors. J. Food Eng. 2018, 230, 114–123.
  26. Koh, E.; Surh, J. Food types and frying frequency affect the lipid oxidation of deep frying oil for the preparation of school meals in Korea. Food Chem. 2015, 174, 467–472.
  27. Cárdenas, J.; Orjuela, A.; Sánchez, D.L.; Narváez, P.C.; Katryniok, B.; Clark, J. Pre-treatment of used cooking oils for the production of green chemicals: A review. J. Clean. Prod. 2021, 289, 125129.
  28. Daud, M.S.M.; Ngadiman, N.I.; Suliman, M.S. The awareness of recycling the used of cooking oil. J. Crit. Rev. 2020, 7, 30–32.
  29. Naz, S.; Siddiqi, R.; Sheikh, H.; Sayeed, S.A. Deterioration of olive, corn and soybean oils due to air, light, heat and deep-frying. Food Res. Int. 2005, 38, 127–134.
  30. Zhang, Q.; Saleh, A.S.; Chen, J.; Shen, Q. Chemical alterations taken place during deep-fat frying based on certain reaction products: A review. Chem. Phys. Lipids 2012, 165, 662–681.
  31. Ahmed, R.B.; Hossain, K. Waste cooking oil as an asphalt rejuvenator: A state-of-the-art review. Constr. Build. Mater. 2020, 230, 116985.
  32. Azahar, W.N.A.W.; Jaya, R.P.; Hainin, M.R.; Bujang, M.; Ngadi, N. Mechanical performance of asphaltic concrete incorporating untreated and treated waste cooking oil. Constr. Build. Mater. 2017, 150, 653–663.
  33. Asli, H.; Ahmadinia, E.; Zargar, M.; Karim, M.R. Investigation on physical properties of waste cooking oil—Rejuvenated bitumen binder. Constr. Build. Mater. 2012, 37, 398–405.
  34. Yuan, X.; Liu, J.; Zeng, G.; Shi, J.; Tong, J.; Huang, G. Optimization of conversion of waste rapeseed oil with high FFA to biodiesel using response surface methodology. Renew. Energy 2008, 33, 1678–1684.
  35. Cvengroš, J.; Cvengrošová, Z. Used frying oils and fats and their utilization in the production of methyl esters of higher fatty acids. Biomass-Bioenergy 2004, 27, 173–181.
  36. Ma, F.; Hanna, M.A. Biodiesel production: A review. Bioresour. Technol. 1999, 70, 1–15.
  37. Enweremadu, C.; Mbarawa, M. Technical aspects of production and analysis of biodiesel from used cooking oil—A review. Renew. Sustain. Energy Rev. 2009, 13, 2205–2224.
  38. Atapour, M.; Kariminia, H.-R. Characterization and transesterification of Iranian bitter almond oil for biodiesel production. Appl. Energy 2011, 88, 2377–2381.
  39. Tomasevic, A.; Siler-Marinkovic, S. Methanolysis of used frying oil. Fuel Process. Technol. 2003, 81, 1–6.
  40. Phan, A.N.; Phan, T.M. Biodiesel production from waste cooking oils. Fuel 2008, 87, 3490–3496.
  41. Babcock, R.E.; Clausen, E.C.; Popp, M.P.; Schulte, W.B. Yield Characteristics of Biodiesel Produced from Chicken Fat-Tall Oil Blended Feedstocks. 2008. Available online: https://trid.trb.org/view/850767 (accessed on 14 October 2021).
  42. Talebian-Kiakalaieh, A.; Amin, N.A.S.; Mazaheri, H. A review on novel processes of biodiesel production from waste cooking oil. Appl. Energy 2013, 104, 683–710.
  43. Jeromin, L.; Peukert, E.; Wollmann, G. Process for the Pre-Esterification of Free Fatty Acds in Fats and Ols. U.S. Patent US4698186A, 6 October 1987.
  44. Zhang, Y.; Dubé, M.; McLean, D.; Kates, M. Biodiesel production from waste cooking oil: 1. Process design and technological assessment. Bioresour. Technol. 2003, 89, 1–16.
  45. Sahoo, P.; Das, L.; Babu, M.; Naik, S.N. Biodiesel development from high acid value polanga seed oil and performance evaluation in a CI engine. Fuel 2007, 86, 448–454.
  46. Crabbe, E.; Nolasco-Hipolito, C.; Kobayashi, G.; Sonomoto, K.; Ishizaki, A. Biodiesel production from crude palm oil and evaluation of butanol extraction and fuel properties. Process. Biochem. 2001, 37, 65–71.
  47. Zhang, H.; Ding, J.; Zhao, Z. Microwave assisted esterification of acidified oil from waste cooking oil by CERP/PES catalytic membrane for biodiesel production. Bioresour. Technol. 2012, 123, 72–77.
  48. Lertsathapornsuk, V.; Pairintra, R.; Aryusuk, K.; Krisnangkura, K. Microwave assisted in continuous biodiesel production from waste frying palm oil and its performance in a 100 kW diesel generator. Fuel Process. Technol. 2008, 89, 1330–1336.
  49. Supraja, K.V.; Behera, B.; Paramasivan, B. Optimization of process variables on two-step microwave-assisted transesterification of waste cooking oil. Environ. Sci. Pollut. Res. 2020, 27, 27244–27255.
  50. Refaat, A.A.; El Sheltawy, S.T.; Sadek, K.U. Optimum reaction time, performance and exhaust emissions of biodiesel produced by microwave irradiation. Int. J. Environ. Sci. Technol. 2008, 5, 315–322.
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