A Comparative Analysis of Wax and Solid Residues From Plastic Wastes Pyrolysis by FTIR Spectroscopy

doi:10.21203/rs.3.rs-4870427/v1

Download PDF

Research Article

A Comparative Analysis of Wax and Solid Residues From Plastic Wastes Pyrolysis by FTIR Spectroscopy

https://doi.org/10.21203/rs.3.rs-4870427/v1

This work is licensed under a CC BY 4.0 License

Version 1

posted

You are reading this latest preprint version

Following the division of the PET-1 plastic samples (Azerbaijan-made, SIRAB brand noncarbonated beverage) used for the study into 1 cm² pieces, they were fired in quartz ampoules at temperatures of 350°C, 450°C, and 550°C for one hour. The FTIR spectroscopy method was applied in accordance with the objectives of the study. Since PET is thermally stable, separation of the volatiles occurs above 420°C. At 450°C, peaks characteristic of wax are observed in the wavenumber range of 2500–3062 cm^− 1, which may be due to the dispersion of the ether group in the PET macromolecule (these peaks are absent in the original sample). In our study, we observed a peak at approximately 1679 cm^− 1, which we believe may be characteristic of the ether (C = O) group. During the thermal destruction of the PET-1 samples at temperatures of 450 and 550°C, strong peaks appear in the regions of 1260, 1085, and 1020 cm-1 in the FT-IR spectra, which could be indicative of the presence of carboxylic acids.

Environmental Chemistry

Nuclear Chemistry

PET-1

pyrolysis

FTIR spectra

wax

solid residue

Comparison of wax and solid residues obtained from different combustion temperatures in PET-1 bottles (Azerbaijan-made,SIRAB brand noncarbonated beverage)
Contents of wax and volatile compounds obtained from the thermal degradation of PET-1 plastic bottle

A forecast of global trends in plastic waste recycling, incineration and disposal through 2050 suggests that 9000 million tons of plastic waste will be recycled, 12000 million tons incinerated, and another 12000 million tons disposed of in landfills or in the natural environment [1].

In the present study, various methods for processing plastic waste to obtain energy from plastic waste, including thermochemical processing methods such as incineration, gasification, plasma gasification, pyrolysis, glycolysis, hydrolysis, aminolysis, and hydrogenation, were developed. These methods involve the production of fuel products such as heat and power [2–15].

Among the methods of thermochemical decomposition, pyrolysis (without oxygen or air at elevated temperatures of 450–800°C) is one of the most reliable solutions to the problem of recycling plastic waste to produce fuel products. An additional advantage of pyrolysis is that the inorganic part present in secondary polymer raw materials is not subject to destruction and can be separated from organic substances, leaving a solid fraction, which makes it possible to extract it for further use. As a result of the pyrolysis of plastics, the product is formed in the form of a wide range of hydrocarbons with virtually no emission of toxic or harmful gases, as is the case with incineration of waste. In addition, no wastewater is produced from the gas purification system. This makes pyrolysis one of the main alternatives to conventional waste processing [16, 17]. The main products of the pyrolysis process are coke, pyrolysis oil and gas. The exact composition of the fuel fraction extracted by pyrolysis depends on the properties of the feedstock [18, 19] and the conditions under which the process is carried out: temperature [19–25], pressure and residence time in the reactor [26–29], and reactor design. The investigation of pyrolysis processes is conducted via various physicochemical methods, such as chromatography, mass spectrometry, and UV and FTIR spectroscopy [27–33].

In [34], the original PET and waxy products were analyzed via a Bruker alpha-P model Fourier transform infrared (FTIR) instrument equipped with a diamond attenuated total reflectance (ATR-DI) accessory and a deuterated triglycine sulfate (DTGS) detector. The wavenumber range was 375 cm^− 1-4000 cm^− 1. The IR spectrum (64 scans) was acquired via OPUS 6.5 software. The original PET and waxy product spectra were characterized by peaks corresponding to aromatic and ethylene groups. Despite the presence of various physicochemical methods, further studies of chemical changes are relevant.

The purpose of this study was to investigate the functional groups present in the products of the pyrolysis of PET-1 plastic waste at temperatures of 350, 450, and 550°C in nitrogen media via FTIR spectroscopy.

The PET-1 plastic samples used for the study were blue bottles from noncarbonated drinks of the SİRAB brand produced in Azerbaijan, which we use in daily lives. For analysis, we crushed samples with an area of approximately 1 cm² and incinerated them in a laboratory-adapted device. The experiments were conducted at 350°C, 450°C, and 550°C for one hour in quartz ampules, and a 10 g sample was added for each experiment.

FTIR spectroscopy and Raman microspectroscopy are the most effective methods for determining the type of polymer, as well as the number, size, and shape of particles. Therefore, the determination of organic functional groups in PET wax was carried out via Fourier transform infrared (FTIR) spectroscopy (Perkin-Elmer) in the range of 400–4000 cm-1. To obtain the emission spectra (T%), the powder samples were pressed in the spectrometer for 3 minutes via a press.

The pyrolysis process of the samples was carried out under flow conditions (nitrogen) in the facility, the scheme of which is given below:

1-nitrogen balloon, 2- monometer, 3- oven (I-heating zone, II-high heating zone), 4- termoregulator, 5- water cooler, 6- wax volume, 7- gas, 8- gas chromatography

The solid residues from the pyrolysis processes were removed after the wax was collected at a separated volume (6). The gas escaped to the atmosphere. FTIR spectra of the solid residues and wax.

Polyethylene terephthalate, also referred to as PET, is a thermoplastic polymer belonging to the polyester family. The formation of PET (polyethylene terephthalate) is achieved through a polycondensation reaction of the monomers, namely, terephthalic acid and ethyl glycol. The resulting material exhibits excellent chemical resistance and barrier properties, as well as good strength, stiffness, wear, and abrasion resistance. However, at high temperatures, PET displays notable sensitivity to moisture. PET has been observed to have rather high thermal stability, with the release of volatile substances beginning at temperatures above 300°C. Several authors have conducted studies on the thermal degradation products of PET Fig. 4\(\:\left[35\:\right].\:\) shows the structure of the polyethylene terephthalate molecule. The PET-1 polymer consists of terphthalate, ether, ethylene, phenyl, and carbonyl groups. Depending on the type of study and the purpose of the work, these groups undergo significant changes.

To understand the processes that occur during the burning of plastic, the following scheme is given (Fig. 4). The thermal degradation mechanism is primarily comprised of the degradation and separation of terephthalic acid and benzoic acid. Subsequently, benzoic acid undergoes a decarboxylation step, resulting in the formation of acetophenone. Definitively identified benzoic acid and acetylbenzoic acid as the most abundant thermal degradation products at 600°C. At higher temperatures, acetophenone yields increase.\(\:\left[37\right]\).

At 1713 (C = O in the carbonyl group),1408 and 1339 (C–O stretching modes in the alkanoate ester and alkoxy ether),1240 (C = C stretch of the phenyl ring),1093 and 1016 (C–O–C antisymmetric), 872 (phenyl ring γ(CH)), 723 cm^− 1 (trans configuration. γ-(CH2)) wavelength-identified peaks\(\:\:\left[40\right]\). The FTIR spectrum of the initial PET samples did not result in any discernible alterations to the existing C-H and O-H stretching vibrations of the various types of H-bonds present in PET. Furthermore, no alkyl group (3294 cm^− 1) was identified within the 3600 − 2500 cm^− 1 region.

It seems that (Fig. 6) as the wax is vaporized and the gaseous product is lost, the pyrolysis time and temperature increase, which in turn leads to a decrease in the yield of pyrolyzed wax \(\:\left[41\right]\). Therefore, as the temperature increased from 350\(\:℃\) to 550\(\:℃\), 92,6\(\:÷\)18,9% of the wax obtained

C-H and O-H stretching vibrations of the various types of H-bonds present in PET. Furthermore, no alkyl groups (3294 cm^− 1) were identified within the 3600–2500 cm^− 1 region (there were no peaks in this region in the initial samples).

The off-spectrum peaks were obtained at 350°C and were therefore not included in the FTIR spectrum results. The FTIR transmission spectra of black residue burning in sonicated quartz before thermal destruction at 450°C and the wax accumulated in the water tube were recorded according to the methodology.

The parameters at wavelengths of 1692.8, 1670, 1262, 755, 694 and 464.2 cm-1 appear only at 450°C. Moreover, the Abs parameters for the peaks at 2923.4, 1453.2, and 845.93 cm-1 observed in the initial samples are zero.

Table 1

Comparison of wax obtained without the thermal destruction of PET-1 bottle samples burned at 450⁰C and 550⁰C
X (cm-1)	initial	Abs 450⁰_C	Abs 550⁰_C
3062	A/O	0,13	0,12
2971	A/O	0,15	A/O
2824	A/O	0,17	0,15
2665	A/O	0,16	0,14
2547	A/O	0,17	A/O
1790	A/O	0,08	A/O
1679	A/O	0,91	0,83
1608	0,05	0,25	0,23
1574	A/O	0,22	0,23
1507	A/O	0,18	0,21
1451	A/O	0,14	0,11
1421	0,02	0,37	0,36
1317	A/O	0,29	A/O
1240	0,07	A/O	A/O
1260	A/O	0,73	0,76
1178	A/O	0,31	0,29
1128	A/O	0,43	0,41
1111	A/O	0,35	0,38
1094	0,07	0,44	0,47
1072	A/O	0,29	A/O
1017	0,06	0,33	0,35
928	A/O	0,42	A/O
876	0,04	0,39	A/O
802	A/O	0,23	0,44
780	A/O	0,31	0,44
756	A/O	0,22	A/O
726	0,09	0,66	0,44
707	A/O	0,65	0,44
684	A/O	0,37	A/O
666	A/O	0,29	0,44
609	A/O	0,15	A/O
550	A/O	0,35	A/O
525	A/O	0,34	A/O

The peaks observed in the 3062 − 2547 region suggest that the bonding configuration of the hydroxyl groups in the polymer chain remains relatively stable. Consequently, the content of hydroxyl groups appears to remain largely consistent with increasing polymer chain length \(\:\left[40\right]\).

The FT-IR absorption peak at 1710 cm^− 1, representing carbonyl C = O stretching, is one of the strongest absorption peaks in the FT-IR spectrum. This peak shows no significant change in intensity or position during thermal destruction. A strong peak at 1713 cm^− 1 is observed in the original PET plastic waste sample incinerated at 450°C, as opposed to the sample incinerated at 550°C. As shown in Fig. 1, the peak at 872 cm⁻1, which corresponds to out-of-plane phenyl ring γ(CH) groups, unequivocally indicates that the flexural mode of C-H PET completely disappears in the destructed samples.

In the FTIR spectra of the solid residues obtained by incinerating PET-1 plastic waste bottles at 450°C and 550°C, peaks corresponding to WAVE numbers 1710, 1601, 754, and 697 are observed, which correspond to C = O bonds.

The functional groups present in pyrolytic wax are determined on the bases of infrared light interacts with wax the chemical bonds will stretch, shrink, and absorb infrared radiation in a certain wavelength range regardless of the structure of the other molecules [12]. The functional groups of the PET waxes obtained in this study also agree with the data of previous studies [15, 34, 41]. \(\:\left[34\right]\:\) established that the original PET and waxy product spectra are characterized by peaks corresponding to aromatic and ethylene groups. The aromatic (C = C), (C–H) and (= C–H) bands are located at 1433, 3064 and 866 cm^− 1, respectively [42, 43]. The ethylene groups show two bands for (C–H) (at 2984 cm^− 1) and C–C (at 927 cm^− 1) [5, 34]. Importantly, the PET spectrum revealed the absence of a peak corresponding to the O–H band, which is characteristic of alcohols and carboxylic acids and is normally between 2500 and 3400 cm^− 1. Therefore, this may confirm that the PET chain does not contain any O–H terminations. In the waxy product spectrum, a very broad peak appears in the region between 2500 and 3064 cm^− 1, indicating the presence of carboxylic groups [43]. Furthermore, the ester bond (C–O), which is characterized by three peaks (1262, 1089 and 1021 cm^− 1), and the carbonyl group (C = O) (1680 cm^− 1) are more intense in the product spectrum [42, 44]. These results prove that the pyrolysis products are mainly carboxylic acids, ketones and esters. By comparing the different spectra at various temperatures, it can be seen that at 430°C, the OH peak of acids is more intense, and the spectrum is very close to the spectrum of benzoic acid. Therefore, there is a high production of benzoic acid and its derivatives at 430°C.

At low temperatures and low times, no significant change in product yield was observed. However, at a certain temperature, with increasing reaction time, the product yield decreased. On the other hand, a significant change in product yield was observed with increasing reaction time and temperature. When the PET-1 samples are subjected to temperatures of 450 and 550°C, pronounced peaks emerge in the FT-IR spectra within the 1260, 1085, and 1020 cm-1 regions, which may be indicative of the presence of carboxylic acids.

Acknowledgment

This work was supported by the “Framework of Research Plans of the Institute of Radiation Problems of Ministry of Science and Education of AR” and with support of the IAEA project [F23036] “Combined radiation‒thermal pyrolysis of polymer wastes”. FTIR spectroscopy was supported by the Department of French Azerbaijani University under Azerbaijan State Oil and Industry University.

Data availability

Data supporting the findings of this study are available from the corresponding author upon reasonable request.

CRediT author statement

M.A. Gurbanov: formal analysis, visualization, conceptualization, editing.

U.A. Guliyeva- Form performing calculations, writing, reviewing, methodology and editing.

E.V. Mirzazada- Research and collection of literature data, investigation, writing, and analysis

Declaration of interests

☒ The authors declare that they have no known competing financial interests or personal relationships that could have appeared to influence the work reported in this paper.

☐ The authors declare the following financial interests/personal relationships, which may be considered potential competing interests:

N. Yu. Kovaleva, E. G. Raevskaya, A. V. Roshchin. Pyrolysis of plastic waste. Review, Chemical Safety, Moscow, Russia, 2020, 4, (1), 48–79, DOI: https://doi.org/10.25514/CHS.2020.1.17004
Dong, J., Tang, Y., Nzihou, A., Chi, Y., Weiss-Hortala, E., Ni, M., & Zhou, Z. (2018). Comparison of waste-to-energy technologies of gasification and incineration using life cycle assessment: Case studies in Finland, France and China, J. Clean. Prod., 203, 287 - 300. https://doi.org/10.1016/j.jclepro.2018.08.139
Zhou, C., Fang, W., Xu, W., Cao, A., & Wang, R. (2014). Characteristics and the recovery potential of plastic wastes obtained from landfill mining. J. Clean. Prod., 80, 80 - 86. https://doi.org/10.1016/j.jclepro.2014.05.083
Bai, B., Liu, Y., Wang, G., Zou, J., Zhang, H., Jin, H., & Li, X. (2019. Experimental investigation on gasification characteristics of plastic wastes in supercritical water. Renew. Energy, 135, 32 - 40. https://doi.org/10.1016/j.renene.2018.11.092
Lee, U., Chung, J.N., & Ingley, H.A. (2014). High-Temperature Steam Gasification of Municipal Solid Waste, Rubber, Plastic and Wood. Energy & Fuels, 28, 4573 - 4587. https://doi.org/10.1021/ef500713j
Onwudili, J.A., & Williams, P.T. (2016). Catalytic supercritical water gasification of plastics with supported RuO2: A potential solution to hydrocarbons–water pollution problem. Process Saf. Environ. Prot., 102, 140 - 149. https://doi.org/10.1016/J.PSEP.2016.02.009
Sanlisoy, A., & Carpinlioglu, M.O. (2017). A review on plasma gasification for solid waste disposal. Int. J. Hydrogen Energy, 42, 1361 - 1365. https://doi.org/10.1016/j.ijhydene.2016.06.008
Munir, M.T., Mardon, I., Al-Zuhair, S., Shawabkeh, A., & Saqib, N.U. (2019). Plasma gasification of municipal solid waste for waste-to-value processing. Renew. Sustain. Energy Rev., 116, 109461. https://doi.org/10.1016/j.rser.2019.109461
Sharuddin, S.D.A., Abnisa, F., Daud, W.M.A.W., & Aroua, M.K. (2018). Pyrolysis of plastic waste for liquid fuel production as prospective energy resource. IOP Conf. Ser. Mater. Sci. Eng., 334(1). https://doi.org/10.1088/1757-899X/334/1/012001
Adrados, A., de Marco, I., Caballero, B.M., López, A., Laresgoiti, M.F., & Torres, A. (2012). Pyrolysis of plastic packaging waste: A comparison of plastic residuals from material recovery facilities with simulated plastic waste. Waste Manag., 32, 826 - 832. https://doi.org/10.1016/j.wasman.2011.06.016
S.D. Anuar Sharuddin et al./Energy Conversion and Management 115 (2016),P. 308–326http://dx.doi.org/10.1016/j.enconman.2016.02.037
Simón, D., Borreguero, A.M., de Lucas, A., & Rodríguez, J.F. (2014). Glycolysis of flexible polyurethane wastes containing polymeric polyols. Polym. Degrad. Stab., 109, 115 - 121. https://doi.org/10.1016/J.POLYMDEGRADSTAB.2014.07.009
Sharma, R., & Bansal, P.P. (2016). Use of different forms of waste plastic in concrete – a review. J. Clean. Prod., 112, 473 - 482. https://doi.org/10.1016/J.JCLEPRO.2015.08.042
Campanelli, J.R., Kamal, M.R., & Cooper, D.G. (1993). A kinetic study of the hydrolytic degradation of polyethylene terephthalate at high temperatures. J. Appl. Polym. Sci., 48, 443 - 451. https://doi.org/10.1002/app.1993.070480309
Onwudili JA, Insura N, Williams PT. Composition of products from the pyrolysis of polyethylene and polystyrene in a closed batch reactor: effects of temperature and residence time. J Anal Appl Pyrol 2009; 86:293–303. https://doi.org/10.1016/j.jaap.2009.07.008
Abbas-Abadi, M.S., Haghighi, M.N. & Yeganeh, H. (2012). The effect of temperature, catalyst, different carrier gases and stirrer on the produced transportation hydrocarbons of LLDPE degradation in a stirred reactor. Journal of Analytical and Applied Pyrolysis, 95, 198-204, https://doi.org/10.1016/j.jaap.2012.02.007
Lopez, G., Artetxe, M., Amutio, M., Bilbao, J. & Olazar, M. (2017). Thermochemical routes for the valorization of waste polyolefinic plastics to produce fuels and chemicals. A review. Renewable and Sustainable Energy Reviews, 73, 346-368, https://doi.org/10.1016/j.rser.2017.01.142
Lopez, A., Marco, D. I., Caballero, B.M., Laresgoiti, M.F., Adrados, A., & Torres, A. (2011). Pyrolysis of municipal plastic waste II: influence of raw material composition under catalytic conditions. Waste Management, 31, 1973 - 1983. https://doi.org/10.1016/j.wasman.2011.05.021.
Chin, B.L.F., Yusup, S., Al Shoaibi, A., Kannan, P., Srinivasakannan, C., & Sulaiman, S.A. (2014). Kinetic studies of copyrolysis of rubber seed shell with high density polyethylene. Energy Convers. Manag., 87, 746 - 753. https://doi.org/10.1016/j.enconman.2014.07.043.
Marcilla, A., Beltrán, M.I., & Navarro, R. (2009). Evolution of products during the degradation of polyethylene in a batch reactor. J. Anal. Appl. Pyrolysis, 86, 14 - 21. https://doi.org/10.1016/j.jaap.2009.03.004.
Diaz Silvarrey, L.S., & Phan, A.N. (2016). Kinetic study of municipal plastic waste. Int. J. Hydrogen Energy, 41, 16352 - 16364. https://doi.org/10.1016/j.ijhydene.2016.05.202.
Jana, R., Mukunda, P., & Nando, G. (2003). Thermogravimetric analysis of compatibilized blends of low density polyethylene and poly(dimethyl siloxane) rubber. Polym. Degrad. Stab., 80, 75 - 82. https://doi.org/10.1016/s0141-3910(02)00385-3.
Walendziewski, J. & Steininger, M. (2001). Thermal and catalytic conversion of waste polyolefines. Catal. Today, 65, 323 - 330. https://doi.org/10.1016/S0920-5861(00)00568-X.
Encinar, J.M., & González, J.F. (2008). Pyrolysis of synthetic polymers and plastic wastes. Kinetic study. Fuel Process. Technol., 89, 678 - 686. https://doi.org/10.1016/j.fuproc.2007.12.01170
Onwudili, J.A., Insura, N., & Williams, P.T. (2009). Composition of products from the pyrolysis of polyethylene and polystyrene in a closed batch reactor: Effects of temperature and residence time. J. Anal. Appl. Pyrolysis, 86, 293 - 303. https://doi.org/10.1016/j.jaap.2009.07.008
Murata, K., Sato, K., & Sakata, Y. (2004). Effect of pressure on thermal degradation of polyethylene. J. Anal. Appl. Pyrolysis, 71, 569 - 589. https://doi.org/10.1016/j.jaap.2003.08.010
Mastral, F., Esperanza, E., Garcı́a, P., & Juste, M. (2002). Pyrolysis of high-density polyethylene in a fluidized bed reactor. Influence of the temperature and residence time. J. Anal. Appl. Pyrolysis, 63, 1 - 15. https://doi.org/10.1016/S0165-2370(01)00137-1
Ludlow-Palafox, C., & Chase, H.A. (2001). Microwave-Induced Pyrolysis of Plastic Wastes. Ind. Eng. Chem. Res., 40, 4749 - 4756. https://doi.org/10.1021/ie010202j
Mastral, F.J., Esperanza, E., Berrueco, C., Juste, M., & Ceamanos, J. (2003). Fluidized bed thermal degradation products of HDPE in an inert atmosphere and in air–nitrogen mixtures. J. Anal. Appl. Pyrolysis, 70, 1 - 17, https://doi.org/10.1016/S0165-2370(02)00068-2
Natalia P. Ivleva.Chemical Analysis of Microplastics and Nanoplastics: Challenges, Advanced Methods, and Perspectives Chem. Rev. 2021, 121, 11886−11936, https://doi.org/10.1021/acs.chemrev.1c00178
Dazzi, A.; Prater, C. B. AFM-IR: Technology and Applications in Nanoscale Infrared Spectroscopy and Chemical Imaging. Chem. Rev. 2017, 117, 5146−5173. https://doi.org/10.1021/acs.chemrev.6b00448
Fischer, M.; Scholz-Boettcher, B. M. Simultaneous Trace Identification and Quantification of Common Types of Microplastics in Environmental Samples by Pyrolysis-Gas Chromatography‒Mass Spectrometry. Environ. Sci. Technol. 2017, 51, 5052−5060 https://doi.org/10.1021/acs.est.6b06362
Vágó Imre, Czinkota Imre, Simándi Péter, Rácz Istvánné, Tolner László. Analysis Of Pyrolysis Residues’ Uv-Vis Spectra. Analele Universităţii din Oradea, Fascicula Protecţia Mediului Vol. XXI, 2013, https://www.researchgate.net/publication/260289608
A. Dhahak, G. Hild,M. Rouaud,G. Mauviel and oth. Slow pyrolysis of polyethylene terephthalate: Online monitoring of gas production and quantitative analysis of waxy products. Journal of Analytical and Applied Pyrolysis,Vol.142,, 2019, 104664, https://doi.org/10.1016/j.jaap.2019.104664
Martı́n-Gullón, M. Esperanza, R. Font. Kinetic model for the pyrolysis and combustion of poly-(ethylene terephthalate) (PET). Journal of Analytical and Applied Pyrolysis,Volumes 58–59, 1 April 2001, P. 635-650, https://doi.org/10.1016/S0165-2370(00)00141-8
PET (Polyethylene terephthalate) https://www.plasticfinder.it/en/pet/pet-polietilen-tereftalato
Maite Artetxe, Gartzen Lopez, Maider Amutio, Gorka Elordi, Martin Olazar*, and Javier Bilbao, Operating Conditions for the Pyrolysis of Poly-(Ethylene Terephthalate) in a Conical Spouted-Bed Reactor, Industrial & Engineering Chemistry Research 49(5) 2010 https://doi.org/10.1021/ie900557c
Diaz-Silvarrey, L.S., McMahon, A., & Phan, A.N. (2018). Benzoic acid recovery via waste poly(ethylene terephthalate) (PET) catalytic pyrolysis using sulphated zirconia catalyst. Journal of Analytical and Applied Pyrolysis, 134(August), 621631. https://doi.org/10.1016/j.jaap.2018.08.014
Du, S., Valla, J.A., Parnas, R.S., & Bollas, G.M. (2016). Conversion of Polyethylene Terephthalate Based Waste Carpet to Benzene-Rich Oils through Thermal, Catalytic, and Catalytic Steam Pyrolysis. ACS Sustainable Chemistry and Engineering, 4(5), 2852–2860. https://doi.org/10.1021/acssuschemeng.6b00450
Shiv Govind Prasad, Abhijit De, and Udayan De. Structural and Optical Investigations of Radiation Damage in Transparent PET Polymer Films. Hindawi Publishing Corporation International Journal of Spectroscopy Volume 2011, Article ID 810936, 7 p. https://doi.org/10.1155/2011/810936
Arvind Kumar. Preparation of wax from waste plastic: a thesis submitted in the partial fulfillment of the requirements for the degree of m. tech. dual degree in chemical engineering, Department of Chemical Engineering National Institute of Technology Rourkela 2016,52 p
Anene, A.F., Fredriksen, S.B., Sætre, K.A., & Tokheim, L.A. (2018). Experimental study of thermal and catalytic pyrolysis of plastic waste components. Sustain., 10, 1 - 12. https://doi.org/10.3390/su10113979
Obeid, F., Zeaiter, J., Al-Muhtaseb, A.H., & Bouhadir, K. (2014). Thermocatalytic pyrolysis of waste polyethylene bottles in a packed bed reactor with different bed materials and catalysts. Energy Convers. Manag., 85, 1 - 6. https://doi.org/10.1016/j.enconman.2014.05.075
Akubo, K., Nahil, M.A., & Williams, P.T. (2017). Aromatic fuel oils are produced from the pyrolysis of polyethylene plastic with metal-impregnated zeolite catalysts. J. Energy Inst., 92,195 - 202. https://doi.org/10.1016/j.joei.2017.10.009

The authors declare no competing interests.

Download PDF

Version 1

posted

You are reading this latest preprint version

A Comparative Analysis of Wax and Solid Residues From Plastic Wastes Pyrolysis by FTIR Spectroscopy

Status:

Version 1

Abstract

Figures

Highlights

1. Introduction

2. Methods

3. Results and discussion

4. Conclusion

Declarations

References

Additional Declarations

Status:

Version 1