“…However, the intensity of this peak and maximum degradation temperature increased gradually from 448 to 476 °C. This shifting in the decomposition peak and increase in maximum degradation temperature were caused by increase in heating rates leading to increase in heat generation and heat flux transfers between the surroundings of the tested mask and their internal moroclaur, thus accelerating the degradation process and complete decomposition of all the mask’s compounds in short time [ 54 ]. Fig.…”
Section: Resultsmentioning
confidence: 99%
“…In case of this type of waste, treatments by heat are preferred to eliminate the virus and convert cotton into oil and gas [ [26] , [27] , [28] ]. Also, the pyrolysis process is classified as an eco-friendly approach with less emission and it may be addressed to the shortage of landfills and incineration disposal [ 29 ], where the medical waste can be converted into homogeneous energy products with high values in nitrogen atmosphere without need for pre-treatment in safe ambient [ 30 ]. The studies presented in the literature were focused on treatment of face mask using pyrolysis treatment [ 31 ].…”
In the times of Covid-19, face masks are considered to be the main source of protection against the virus that reduces its spread. These masks are classified as single-use medical products with a very short service life, estimated at few days, hence millions of contaminated masks are generated daily in the form of hazardous materials, what requires to develop a safe method to dispose of them, especially since some of them are loaded with viruses. 3-ply face masks (3PFM) represent the major fraction of this waste and are composed mainly from polypropylene and melt blown filter with high content of volatile substances (96.6 wt.%), what makes pyrolysis treatment an emerging technology that could be used to dispose of face masks and convert them into energy products. In this context, this work aims to study pyrolysis kinetic behaviour and TG-FTIR-GC–MS analysis of 3PFM. The research started with analysis of 3PFM using elemental analysis, proximate analysis, and compositional analyses. Afterwards, TG-FTIR system was used to study the thermal and chemical decomposition of 3PFM analyzed at different heating rates: 5, 10, 15, 20, 25, and 30 °C/min. The GC/MS system was used to observe the synthesized volatile products at the maximum decomposition temperatures. After that, isoconversional methods, the advanced nonlinear integral isoconversional method, and the iterative linear integral isoconversional method were used to determine the activation energies of mask pyrolysis, while the distributed activation energy model and the independent parallel reactions kinetic model were used to fit TGA and DTG curves with deviations below <1. The TGA-DTG results showed that 3PFM can decompose in three different periods with a total weight loss of 95 % and maximum decomposition in the range 405−510 °C, while the FTIR spectra and GC–MS analysis exhibited that – C—H (aromatic and aliphatic) and 2,4-Dimethyl-1-heptene (28–43 % based on heating rate) represented the major compounds in the released volatile components. Finally, Vyazovkin and the iterative linear integral isoconversional methods gave activation energies almost similar to that obtained by the KAS isoconversional method.
“…However, the intensity of this peak and maximum degradation temperature increased gradually from 448 to 476 °C. This shifting in the decomposition peak and increase in maximum degradation temperature were caused by increase in heating rates leading to increase in heat generation and heat flux transfers between the surroundings of the tested mask and their internal moroclaur, thus accelerating the degradation process and complete decomposition of all the mask’s compounds in short time [ 54 ]. Fig.…”
Section: Resultsmentioning
confidence: 99%
“…In case of this type of waste, treatments by heat are preferred to eliminate the virus and convert cotton into oil and gas [ [26] , [27] , [28] ]. Also, the pyrolysis process is classified as an eco-friendly approach with less emission and it may be addressed to the shortage of landfills and incineration disposal [ 29 ], where the medical waste can be converted into homogeneous energy products with high values in nitrogen atmosphere without need for pre-treatment in safe ambient [ 30 ]. The studies presented in the literature were focused on treatment of face mask using pyrolysis treatment [ 31 ].…”
In the times of Covid-19, face masks are considered to be the main source of protection against the virus that reduces its spread. These masks are classified as single-use medical products with a very short service life, estimated at few days, hence millions of contaminated masks are generated daily in the form of hazardous materials, what requires to develop a safe method to dispose of them, especially since some of them are loaded with viruses. 3-ply face masks (3PFM) represent the major fraction of this waste and are composed mainly from polypropylene and melt blown filter with high content of volatile substances (96.6 wt.%), what makes pyrolysis treatment an emerging technology that could be used to dispose of face masks and convert them into energy products. In this context, this work aims to study pyrolysis kinetic behaviour and TG-FTIR-GC–MS analysis of 3PFM. The research started with analysis of 3PFM using elemental analysis, proximate analysis, and compositional analyses. Afterwards, TG-FTIR system was used to study the thermal and chemical decomposition of 3PFM analyzed at different heating rates: 5, 10, 15, 20, 25, and 30 °C/min. The GC/MS system was used to observe the synthesized volatile products at the maximum decomposition temperatures. After that, isoconversional methods, the advanced nonlinear integral isoconversional method, and the iterative linear integral isoconversional method were used to determine the activation energies of mask pyrolysis, while the distributed activation energy model and the independent parallel reactions kinetic model were used to fit TGA and DTG curves with deviations below <1. The TGA-DTG results showed that 3PFM can decompose in three different periods with a total weight loss of 95 % and maximum decomposition in the range 405−510 °C, while the FTIR spectra and GC–MS analysis exhibited that – C—H (aromatic and aliphatic) and 2,4-Dimethyl-1-heptene (28–43 % based on heating rate) represented the major compounds in the released volatile components. Finally, Vyazovkin and the iterative linear integral isoconversional methods gave activation energies almost similar to that obtained by the KAS isoconversional method.
“…As revealed by the elemental analysis in the table, the nitrogen content (0.58%) was lower than that usually found in several other types of plastic wastes, such as: wheat PP (2.34%), PE (2.53%), and PH (2.64%) [ 39 ]. This low value of N 2 and S (0.01 wt %) is desirable in biofuels, which can contribute to the reduction of nitrogen oxides (NOx) and SO 2 toxic emissions during the conversion process [ 40 ]. Additionally, high content of C (81.56%) and O (3.91%) was observed in all the MFPW samples, which indicates that the MFPW samples are a very rich source of carbon precursor that facilitates the conversion process.…”
Section: Resultsmentioning
confidence: 99%
“…This means that all polymers and organic components degraded together in the form of a single reaction. Al is a metallic component that cannot decompose even at high temperatures; however, Al can react with the generated gases during the conversion process and some of them can be used as a catalyst (self-catalysts) to accelerate the reaction and to upgrade the obtained fuel [ 40 , 43 ]. Meanwhile, the excess fraction of Al can be kept (undecomposed Al) as a mixture with char devolatilization in the last phase in a wider range of temperatures (502–900 °C) with an average weight loss ~2 wt % for all samples.…”
Recently, a pyrolysis process has been adapted as an emerging technology to convert metalized food packaging plastics waste (MFPWs) into energy products with a high economic benefit. In order to upscale this technology, the knowledge of the pyrolysis kinetic of MFPWs is needed and studying these parameters using free methods is not sufficient to describe the last stages of pyrolysis. For a better understanding of MFPWs pyrolysis kinetics, independent parallel reactions (IPR) kinetic model and its modification model (MIPR) were used in the present research to describe the kinetic parameters of MFPWs pyrolysis at different heating rates (5–30 °C min−1). The IPR and MIPR models were built according to thermogravimetric (TG)-Fourier-transform infrared spectroscopy (FTIR)-gas chromatography−mass spectrometry (GC-MS) results of three different types of MFPWs (coffee, chips, and chocolate) and their mixture. The accuracy of the developed kinetic models was evaluated by comparing the conformity of the DTG experimental results to the data calculated using IPR and MIPR models. The results showed that the dependence of the pre-exponential factor on the heating rate (as in the case of MIPR model) led to better conformity results with high predictability of kinetic parameters with an average deviation of 2.35% (with an improvement of 73%, when compared to the IPR model). Additionally, the values of activation energy and pre-exponential factor were calculated using the MIPR model and estimated at 294 kJ mol−1 and 5.77 × 1017 kJ mol−1 (for the mixed MFPW sample), respectively. Finally, GC-MS results illustrated that pentane (13.8%) and 2,4-dimethyl-1-heptene isopropylcyclobutane (44.31%) represent the main compounds in the released volatile products at the maximum decomposition temperature.
“…As demand for natural gas has been growing enormously recently, many energy-conversion technologies (e.g., Pyrolysis, fermentation, etc.) were employed to generate biogas from different types of waste in order to compensate the shortage in production of natural gas, and to dispose such waste simultaneously [3][4][5]. Usually, biogas obtained using such technologies contains many components, particularly 60-70 wt.% of Methane (CH 4 ) as a main component, [30][31][32][33][34][35][36][37][38][39][40] wt.% of Carbon dioxide (CO 2 ) as a significant impurity in natural gas paths, and some trace elements (e.g., Nitrogen, ammonia, hydrogen sulphide, water vapor, etc.)…”
Polyether block amide (PEBA) nanocomposite membranes, including Graphene (GA)/PEBA membranes are considered to be a promising emerging technology for removing CO2 from natural gas and biogas. However, poor dispersion of GA in the produced membranes at industrial scale still forms the main barrier to commercialize. Within this frame, this research aims to develop a new industrial approach to produce GA/PEBA granules that could be used as a feedstock material for mass production of GA/PEBA membranes. The developed approach consists of three sequential phases. The first stage was concentrated on production of GA/PEBA granules using extrusion process (at 170–210 °C, depending on GA concentration) in the presence of Paraffin Liquid (PL) as an adhesive layer (between GA and PEBA) and assisted melting of PEBA. The second phase was devoted to production of GA/PEBA membranes using a solution casting method. The last phase was focused on evaluation of CO2/CH4 selectivity of the fabricated membranes at low and high temperatures (25 and 55 °C) at a constant feeding pressure (2 bar) using a test rig built especially for that purpose. The granules and membranes were prepared with different concentrations of GA in the range 0.05 to 0.5 wt.% and constant amount of PL (2 wt.%). Also, the morphology, physical, chemical, thermal, and mechanical behaviors of the synthesized membranes were analyzed with the help of SEM, TEM, XRD, FTIR, TGA-DTG, and universal testing machine. The results showed that incorporation of GA with PEBA using the developed approach resulted in significant improvements in dispersion, thermal, and mechanical properties (higher elasticity increased by ~10%). Also, ideal CO2/CH4 selectivity was improved by 29% at 25 °C and 32% at 55 °C.
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