Corn Cobs’ Biochar as Green Host of Salt Hydrates for Enhancing the Water Sorption Kinetics in Thermochemical Heat Storage Systems

Heat storage technologies are essential for increasing the use of solar energy in the household sector. Their development can be achieved by designing new storage materials; one way is to impregnate a porous matrix with hygroscopic salts. In this article, the possibility of using biochar-based composite sorbents to develop promising new heat storage materials for efficient thermal storage is explored. Biochar-based composites with defined salt loadings (5, 10, 15, and 20%) were produced by impregnating MgSO4 into a biochar matrix derived from corn cobs. The new materials demonstrated a high water sorption capacity of 0.24 g/g (20MgCC). After six successive charging-discharging cycles (dehydration/dehydration cycles), only a negligible variation of the heat released and the water uptake was measured, confirming the absence of deactivation of 20MgCC upon cycling. The new 20MgCC composite showed an energy storage density of 635 J/g (Tads = 30 °C and RH = 60%), higher than that of other composites containing a similar amount of hydrate salt. The macroporous nature of this biochar increases the available surface for salt deposition. During the hydration step, the water molecules effectively diffuse through a homogeneous layer of salt, as described by the intra-particle model applied in this work. The new efficient biochar-based composites open a low-carbon path for the production of sustainable thermal energy storage materials and applications.


Introduction
Thermochemical heat storage (TCHS) systems that are very broadly implanted in the areas of solar photo/thermal utilization, building insulation, and industrial applications are becoming increasingly important as a means to increase the energy efficiency [1]. TCHS systems have an important industrial application value to guarantee the adaptability and stability in renewable energy implementation. TCHS systems increase the utilization efficiency as a result of their high heat storage capacity, the possibility of achieving longlasting energy storage period, and the negligible energy loss during storage [2]. Salt hydratebased TCHS materials have emerged as the best candidate for storage materials due to the simple reaction involved (hydration), the non-toxicity, and the absence of side reactions [3,4]. Most TCHS operates on the principle of the reversible sorption reaction (generally water sorption), where heat is stored during desorption (charge) and released during adsorption at a later time (discharge). To convert the system into a practical residential application (space heating and domestic hot water generation), the TCHS material must be carefully selected. The selection criteria for salt hydrates [5][6][7] include a high energy density, a low charging temperature with a good mass and heat transfer [8], and an improved thermal conductivity [9]. The working pair MgSO 4 -H 2 O has gained attention [8,9] due to the high theoretical energy density (2.8 GJ/m 3 ) and the high deliquescence relative humidity (DRH) of 90%. However, overhydration, aggregate formation during rehydration, kinetic hindrance limiting mass and heat transfer, and poor cyclability [10] are the major drawbacks of salt hydrate-based TCHS. Consequently, the potential of the system has not yet been achieved, and due to these constraints, the energy storage capacity is still too low. Attempting to make composites by dispersing the salt in a porous matrix to prevent swelling and aggregation of the salt is one way to take advantage of MgSO 4 's great potential and overcome one of the main materials' drawbacks: mass and heat transfer limitations. To achieve the goal of efficient and low-temperature thermochemical heat storage, it is necessary to design and synthesize novel TCHS composites that not only present excellent storage capacity and hydration behavior, but also assure a long hydration/dehydration cycle reliability. The goal can be reached by finding suitable support for dispersing the salt hydrate to minimize the thickness of the salt deposit and consequently improve the water molecule diffusion. A promising candidate is biochar.
In contrast to its widespread application in other domains such as conversion and storage of energy [11], supercapacitors, and batteries [12,13], to the best of our knowledge, there is no study reporting on the application of biochar materials derived from biomass waste in the field of thermochemical heat storage by sorption.
Biomass is predominantly composed of biopolymers such as cellulose, hemicellulose, and lignin [14], which serve as a suitable carbon skeleton framework for the production of carbonaceous materials such as biochar. Bamboo bagasse [15], cotton rosewood [16], and pinewood [17] are some examples. A diverse spectrum of biomass precursors rich in biomolecules such as carbohydrates and proteins contributes to significant scientific progress in the development of functional biomass-based carbons [18]. A particularly renewable and sustainable source of biochar is woody biomass, such as agriculture's waste [19,20].
Pyrolysis is a sustainable method of converting biomass into biochar and biofuels. It consists of the thermal conversion of biomass in an oxygen-free or oxygen-poor conditions [21,22]. Due to its distinctive physicochemical characteristics, the biochar has a wide range of potential uses in a variety of fields, including energy production, soil conditioning, soil remediation, and catalysis [23][24][25][26][27]. The pyrolysis temperature is the most important property of the resulting biochar [28,29]. Biochar produced at high pyrolysis temperatures (>600 • C) has a high pH, a large surface area (porosity), and a high aromaticity. Lower process temperatures, on the other hand, result in higher char yield, a higher amount of volatiles (that recondense on the biochar surface), and oxygen-containing surface functions that provide higher electrical conductivity and cation-exchange capacity [25,30,31].
Moreover, it should be mentioned that biomass is an entirely renewable energy source because the CO 2 generated during its combustion and utilization processes does not account for the contribution to the atmospheric CO 2 (because of the neutral carbon balance due to its biogenic origin). In other words, plants utilize CO 2 , which is released into the environment as a result of other plants' decomposition processes for growth and metabolic functions [32]. Therefore, using biomass accelerates the release of CO 2 into the atmosphere but does not affect the global carbon balance; once released, CO 2 will be metabolized by plants to create new biomass [33].
Biochar derived from biomass waste has already displayed excellency in energy storage and catalysis due to its valuable advantages of a low carbon footprint [34], wide availability, and low cost [35,36]. Moreover, the annual production of biomass is around 130 billion tons worldwide [37]; this massive quantity assures the possibility of producing biochar in sufficient quantities for the eventual development of the TCHS sector. Converting the biomass waste into a support for producing TCHS materials is an interesting idea: such composites can store and convert renewable energy through a sustainable technology, thus applying a sustainable material and contributing to sustainable development [38].
In this study, MgSO 4 was incorporated into a porous biochar support derived from corncobs pyrolysis. The corresponding MgSO 4 TCHS composites were synthesized, carefully characterized, and examined to develop adsorbent materials that successfully disperse the salt over the support surface. Additionally, to gain a better understanding of the effect of MgSO 4 salt, studies on the hydration and energy release behavior of the materials have been detailed.

Composite Adsorbents' Structural and Textural Characteristics
The chemical composition determined by WDXRF (2nd column) is outlined in Table 1. The support was characterized by CO 2 manometric adsorption, and the isotherms were collected at 0 • C. Figure 1a,b display the CO 2 adsorption isotherm and the pore size distribution (PSD) of the biochar, respectively. PSD was obtained by applying the CO 2 -DFT model. The PSD clearly showed the microporous structure of the biochar and, in addition, the existence of ultramicroporosity (conventional for biomass-derived carbon materials). Three populations of pore size were detected: the first centered at 0.56 nm with a sharp and clear peak, and two others centered at 0.82 and 1.00 nm. The specific surface area S BET and the pore volume V p were then determined, and the result showed S BET = 175 m 2 /g and V p = 0.06 cm 3 /g due to the ultra-micro and microporosity. such composites can store and convert renewable energy through a sustainable technology, thus applying a sustainable material and contributing to sustainable development [38]. In this study, MgSO4 was incorporated into a porous biochar support derived from corncobs pyrolysis. The corresponding MgSO4 TCHS composites were synthesized, carefully characterized, and examined to develop adsorbent materials that successfully disperse the salt over the support surface. Additionally, to gain a better understanding of the effect of MgSO4 salt, studies on the hydration and energy release behavior of the materials have been detailed.

Composite Adsorbents' Structural and Textural Characteristics
The chemical composition determined by WDXRF (2nd column) is outlined in Table  1. The support was characterized by CO2 manometric adsorption, and the isotherms were collected at 0 °C. Figure 1a,b display the CO2 adsorption isotherm and the pore size distribution (PSD) of the biochar, respectively. PSD was obtained by applying the CO2-DFT model. The PSD clearly showed the microporous structure of the biochar and, in addition, the existence of ultramicroporosity (conventional for biomass-derived carbon materials). Three populations of pore size were detected: the first centered at 0.56 nm with a sharp and clear peak, and two others centered at 0.82 and 1.00 nm. The specific surface area SBET and the pore volume Vp were then determined, and the result showed SBET = 175 m 2 /g and Vp = 0.06 cm 3 /g due to the ultra-micro and microporosity.  The biochar support was also characterized by mercury intrusion porosimetry to probe the macroporosity. The estimated total pore area due to macrospores was 78.4 m 2 /g (this surface was estimated considering perfectly cylindrical pores). Figure 2 shows the  The biochar support was also characterized by mercury intrusion porosimetry to probe the macroporosity. The estimated total pore area due to macrospores was 78.4 m 2 /g (this surface was estimated considering perfectly cylindrical pores). Figure 2 shows the distribution of the macropores size from 300 µm to about 0.01 µm; three main pore size ranges were identified. The first was centered at 8 µm (in the 20 to 3 µm range), the second at 0.37 µm (characterized by a band in the 0.7 to 0.18 µm range), and the third at 0.07, with a band between 0.18 and 0.01 µm. The first two pore size populations, observed on the left side of Figure 2, correspond to the inter-particle filling between the granules. This result shows that the biochar supports possess a macroporosity network in addition to micropores. This can provide an accessible surface for the salt that can be homogeneously dispersed into the macropores. The possibility to charge into the support with a higher amount of salt allows for higher heat capacities. Moreover, if the salt can be efficiently dispersed on a larger, more accessible surface, the mass transfer is potentially ameliorated due to the thin layer of salt deposited. As a result, hydration kinetics can be improved. The other four composites were also characterized by Hg intrusion, and the results are shown in Figure 3. The pore size distribution of all four composites shows two main peaks located in the macropore range: 3 µm and 40 nm. A significant decrease in the 3 µm peak can be observed as the salt content increases. The decrease in the 3 µm peak also led to a reduction by 15% in terms of total porosity (from 70% to 55%) and more than 50% (from 1.89 to 0.81 cm 3 /g) in terms of pore volume.
Molecules 2023, 28, x FOR PEER REVIEW 4 o distribution of the macropores size from 300 μm to about 0.01 μm; three main pore s ranges were identified. The first was centered at 8 μm (in the 20 to 3 μm range), the seco at 0.37 μm (characterized by a band in the 0.7 to 0.18 μm range), and the third at 0.07, w a band between 0.18 and 0.01 μm. The first two pore size populations, observed on the side of Figure 2, correspond to the inter-particle filling between the granules. This res shows that the biochar supports possess a macroporosity network in addition to cropores. This can provide an accessible surface for the salt that can be homogeneou dispersed into the macropores. The possibility to charge into the support with a hig amount of salt allows for higher heat capacities. Moreover, if the salt can be efficien dispersed on a larger, more accessible surface, the mass transfer is potentially ameliora due to the thin layer of salt deposited. As a result, hydration kinetics can be improv The other four composites were also characterized by Hg intrusion, and the results shown in Figure 3. The pore size distribution of all four composites shows two main pe located in the macropore range: 3 μm and 40 nm. A significant decrease in the 3 μm pe can be observed as the salt content increases. The decrease in the 3 μm peak also led t reduction by 15% in terms of total porosity (from 70% to 55%) and more than 50% (fr 1.89 to 0.81 cm 3 /g) in terms of pore volume. XRD is a powerful method to investigate the eventual presence of crystalline impurities on the biochar and to identify the salt hydrate phases. The XRD patterns of all samples ( Figure 4) displays an amorphous graphite peak at 23 • 2θ. This peak is less visible in the most charged sample (20MgCC). Three tiny sharp peaks can be identified at 28, 30, and 40 • 2θ in the XRD pattern of the biochar support, which were assigned to Sylvite KCl. Prakongkep et al. [39] investigated 14 biochars made from agricultural wastes such as corn cobs and found that K-minerals are contained in most of them, including Sylvite KCl. However, those peaks were no longer present in the XRD patterns of the composites. KCl was probably removed or overlapped during the MgSO 4 impregnation procedure. According to the X'Pert HighScore Plus V4 software, the XRD patterns of the 15MgCC and 20MgCC samples showed sharp crystallinity diffraction peaks that were identified as MgSO 4 . 1.25H 2 O (Ref. Code: 00-028-0631), indicating that the dehydration at 150 • C was partial, as expected [40]. The intensity of the diffraction peaks indicates that more MgSO 4 . 1.25H 2 O crystallites were found in the 20MgCC sample. This can be explained by the fact that more salt was deposited on the surface of the biochar, resulting in clusters or thicker layers of MgSO 4 salt that are more difficult to dehydrate. It should be noted that, to our knowledge, no literature has illuminated the formation of XRD is a powerful method to investigate the eventual presence of crystalline imp rities on the biochar and to identify the salt hydrate phases. The XRD patterns of all sa ples ( Figure 4) displays an amorphous graphite peak at 23°2θ. This peak is less visible the most charged sample (20MgCC). Three tiny sharp peaks can be identified at 28, and 40°2θ in the XRD pattern of the biochar support, which were assigned to Sylvite K Prakongkep et al. [39] investigated 14 biochars made from agricultural wastes such as co cobs and found that K-minerals are contained in most of them, including Sylvite K However, those peaks were no longer present in the XRD patterns of the composites. K was probably removed or overlapped during the MgSO4 impregnation procedure. A cording to the X'Pert HighScore Plus V4 software, the XRD patterns of the 15MgCC a 20MgCC samples showed sharp crystallinity diffraction peaks that were identified MgSO4. 1.25H2O (Ref. Code: 00-028-0631), indicating that the dehydration at 150 °C w partial, as expected [40]. The intensity of the diffraction peaks indicates that more MgS 1.25H2O crystallites were found in the 20MgCC sample. This can be explained by the f that more salt was deposited on the surface of the biochar, resulting in clusters or thick layers of MgSO4 salt that are more difficult to dehydrate. It should be noted that, to o knowledge, no literature has illuminated the formation of MgSO4  SEM analyses were performed to examine the morphology and uniformity of salt deposition on the biochar surface. According to Figure 5, an irregular macropore network is observed, which confirms the results of Hg porosimetry. SEM analyses were also performed for the synthesized composites, and for further information, EDX mapping was conducted to analyze the salt distribution at the biochar surface. As shown in Figure 6, for the 5MgCC composite, the MgSO4 salt was deposited both on the external surface and inside the macropores. When the salt loading content started to increase, the macropore observed, which confirms the results of Hg porosimetry. SEM analyses were also performed for the synthesized composites, and for further information, EDX mapping was conducted to analyze the salt distribution at the biochar surface. As shown in Figure 6, for the 5MgCC composite, the MgSO 4 salt was deposited both on the external surface and inside the macropores. When the salt loading content started to increase, the macropore entrance became less and less accessible, as can be observed by the SEM picture in Figure 6 for the different composites with increasing salt content. EDX mapping showed, in each case, a homogeneous deposition of the salt on the external surface. Unfortunately, it is not possible to visualize the salt inside the pores; due to their depth, the electron beams cannot probe the internal surface (see Figures S1-S4 in the Supplementary Materials). SEM analyses were performed to examine the morphology and uniformity of s deposition on the biochar surface. According to Figure 5, an irregular macropore netwo is observed, which confirms the results of Hg porosimetry. SEM analyses were also p formed for the synthesized composites, and for further information, EDX mapping w conducted to analyze the salt distribution at the biochar surface. As shown in Figure 6, f the 5MgCC composite, the MgSO4 salt was deposited both on the external surface a inside the macropores. When the salt loading content started to increase, the macropo entrance became less and less accessible, as can be observed by the SEM picture in Figu  6 for the different composites with increasing salt content. EDX mapping showed, in ea case, a homogeneous deposition of the salt on the external surface. Unfortunately, it is n possible to visualize the salt inside the pores; due to their depth, the electron beams cann probe the internal surface (see Figures S1-S4 in the Supplementary Materials).

Hydration Performances
The variation of the heat flow and the mass of the sample in relation to time we employed to determine the heat of hydration (Figure 7a) and the water adsorption capa ity (labeled as "we" in Equation (1)

Hydration Performances
The variation of the heat flow and the mass of the sample in relation to time were employed to determine the heat of hydration (Figure 7a) and the water adsorption capacity (labeled as "w e " in Equation (1)) ( Figure 7b).
where m h (g) and m d (g) represent the final masses of the hydrated and the dehydrated composite, respectively, and w e is the water adsorption capacity (gH 2 O/g sample or g/g in short).  Table 2 reports the heat released by the biochar support and the four composites expressed as J/gcomp and J/gwater. The heat released by the biochar is close to the water condensation heat (vapor → liquid) at 30 °C, which is approximately 2400 J/gwater [41]. This means that the heat released by the biochar is related to the condensation of water vapor on the biochar surface. The heat released (in J/gwater) by the biochar and related composites is plotted as a function of the salt content in Figure 8a. The curve shows an increasing trend that tends to reach a value between 2900 and 3200 J/gwater [42] corresponding to the hydration of the salt from monohydrate to hexahydrate and from monohydrate to heptahydrate, respectively. From this observation, one can conclude that after the hydration process, the final hydration state is between six and seven molecules of water. Similar to the heat release behavior, the water adsorption has also been plotted as a function of the salt content, showing a linear increasing trend (Figure 8b). These results prove that all the The biochar support CC550 adsorbed 0.07 g of water per gram of dry composite, with a corresponding heat release of 183 J/g. The 5MgCC composite with 4.4% MgSO 4 released 360 J/g of energy (water adsorption 0.126 g/g). As the salt concentration increased up to 19.5% (20MgCC composite), the heat production and the water uptake of the composites continued to increase to over 635 J/g and 0.235 g/g in water adsorption capacity for the 20MgCC composite. By the observation of the hydration curves, it can be observed that the hydration process is relatively fast and the isotherms quickly reach a plateau after 2 and 3 h for the support and the 5MgCC composite, respectively. Differently, the beginning of the hydration process presents a lower rate (lower slope of the isotherm) for the other composites; even after 8 h of hydration, the plateau (complete hydration) was not attained. Table 2 reports the heat released by the biochar support and the four composites expressed as J/g comp and J/g water . The heat released by the biochar is close to the water condensation heat (vapor → liquid) at 30 • C, which is approximately 2400 J/g water [41]. This means that the heat released by the biochar is related to the condensation of water vapor on the biochar surface. The heat released (in J/g water ) by the biochar and related composites is plotted as a function of the salt content in Figure 8a. The curve shows an increasing trend that tends to reach a value between 2900 and 3200 J/g water [42] corresponding to the hydration of the salt from monohydrate to hexahydrate and from monohydrate to heptahydrate, respectively. From this observation, one can conclude that after the hydration process, the final hydration state is between six and seven molecules of water. Similar to the heat release behavior, the water adsorption has also been plotted as a function of the salt content, showing a linear increasing trend (Figure 8b). These results prove that all the composites adsorb water vapor similarly, regardless of the amount of salt deposited on the biochar support (no apparent mass transfer limitation).
Molecules 2023, 28, x FOR PEER REVIEW 9 of 17     Table 3 compares the performance of the 20MgCC sample with other composite storage materials (also impregnated with MgSO 4 ) reported in the literature. Supporting MgSO 4 on the corncob biochars seems to give origin to composites with a higher heat storage capacity than other composites previously reported (even when containing higher quantities of salt).

Hydration Kinetic Modeling
Various kinetic models are available in the literature and have been applied for the study of the kinetics of hydration of sorbent materials [48]. Among the models, the intra-particle diffusion model (Figure 9a), described by Equation (2) below, achieves good numerical approximations when applied to the hydration of biochar and related composites and better describes the physical phenomena involved during the water uptake.
with k i as the intra-particle diffusion rate constant (g/g 1 /h 0.5 ), t the hydration time (h), and C represents the material transfer resistance (g/g). This model assumes the diffusion of water on composites with a homogeneous dispersion of the salt. As shown in Figure 9b, the amount of water adsorbed is a linear function of the square root of the hydration time for all the materials. The intra-particle diffusion rate constant of each material was then deduced and showed a similar outcome between 0.09 and 0.11 for all samples. These results validate the model assumptions and confirm that the intra-particle model provides a good description of the hydration phenomena for these types of materials.

Cyclability Investigation
To test the cyclability of the best performing composite, the 20MgCC sample was submitted to six consecutive cycles of hydration (30 • C and an RH of 60%) and dehydration (150 • C). To determine whether the hydration behavior was consistent, the heat generated following each cycle was recorded and compared to the earlier ones. Figure 10 shows a negligible variation in the heat released and water uptake, confirming the good cyclability of the composite. Figure 11 shows the EDX images after six cycles of 20MgCC. The salt remained well dispersed on the support, confirming the stability of the synthesized 20MgCC composite.

Cyclability Investigation
To test the cyclability of the best performing composite, the 20MgCC sample was submitted to six consecutive cycles of hydration (30 °C and an RH of 60%) and dehydration (150 °C). To determine whether the hydration behavior was consistent, the heat generated following each cycle was recorded and compared to the earlier ones. Figure 10 shows a negligible variation in the heat released and water uptake, confirming the good cyclability of the composite. Figure 11 shows the EDX images after six cycles of 20MgCC. The salt remained well dispersed on the support, confirming the stability of the synthesized 20MgCC composite.

Preparation Method of Composites
The biochar was prepared in a pilot pyrolyzer at the RAPSODEE-UMR CNRS 5302 laboratory, following the procedure detailed in [19]. In the present case, the parent biomass was composed of corncobs collected in the Alsace region (to answer circular economy issues) and dried at 105 °C for 24 h. They were then pyrolyzed at 550 °C under an N2

Preparation Method of Composites
The biochar was prepared in a pilot pyrolyzer at the RAPSODEE-UMR CNRS 5302 laboratory, following the procedure detailed in [19]. In the present case, the parent biomass was composed of corncobs collected in the Alsace region (to answer circular economy issues) and dried at 105 • C for 24 h. They were then pyrolyzed at 550 • C under an N 2 flow rate of 100 mL/min. The pyrolysis temperature was reached with a heating rate of 4 • C/min and maintained for 1.5 h. The biochar obtained after the pyrolysis was sieved between 2.5-4 mm and labeled CC550. The obtained biochar was used as a porous support for MgSO 4 salt hydrate.
The impregnation method was used to deposit MgSO 4 (MgSO 4 . 7H 2 O, 99.9% from Sigma-Aldrich (Saint Quentin Fallavier, France) onto the CC550 porous support. The method consists of intimately mixing the porous support with a MgSO 4 solution. Prior to impregnation, to eliminate water from the pores, the biochar was dried in an oven at 150 • C. The aqueous solution of MgSO 4 was then added over the dried support. The mixture was subjected to constant mixing for 4 h to homogenize the impregnation. The obtained powders were then dried at 60 • C for 12 h and successively at 150 • C for 12 h more. Four composite adsorbents were synthesized and then designated as xMgCC (Table 1), with x is the theoretical content of MgSO 4 in the composites. The real salt content was then verified by X-ray fluorescence.

Techniques of Characterizations
The parameters and conditions used to characterize the composites by X-Ray Diffraction (XRD) analyses, X-Ray Fluorescence, CO 2 adsorption, and Scanning Electron Microscope (SEM) are detailed in our previously published papers [9,43,49].
Mercury porosimetry analysis on the biochar was subcontracted to a FiLAB provider that performed the analysis with an Autopore IV device from Micrometrics. The sample was degassed at ambient temperature and 50 µmHg pressure for 3 h. Mercury intrusion was performed at 22 • C with a contact angle of 130 • C and a pressure range of 0.52 to 60,000 psia (0.036 to 4137 bar), covering a pore range of 350 µm to 3 nm.

Heat Released and Water Adsorption Experiments
The apparatus and procedure employed to examine the performance of composites are reported in our previously published papers [9,43]. The samples (15-25 mg) were first dehydrated at 150 • C under a flow of dry air (30 mL/min) followed by 3 h in a 150 • C isotherm to perform the dehydration. The dehydration temperature was selected on the basis of the temperature that can be obtained in a real application by using flatplate solar heat collectors [47,50]. After the dehydration step, the sample was cooled to 30 • C. The sample was kept at this temperature in dry air until the DSC signal attained a stable baseline. Then the relative humidity (RH) of the air flow was augmented to 60% to begin the hydration phase. To reach a complete rehydration, the samples were hydrated for 8 h until the DSC signal went back to the baseline. The TG-DSC apparatus used in this study has inherent experimental errors, with an accuracy of ±0.01 • C for temperature measurements and ±10 −6 g for mass measurements. To ensure an accurate calculation of the dehydration/hydration heat, a standardized procedure was followed. The dehydration/hydration process was conducted after stabilizing the DSC and TGA signals. This procedure was carried out for both the empty crucible (blank experiment) and each sample. By subtracting the signals from the blank experiment, the dehydration/hydration heat (expressed in J/g sample ) was obtained. The estimation of the hydration heat values includes an error of approximately 15 kJ/kg sample , which takes into account systematic errors in heat flow acquisition, mass measurement obtained by the coupled balance, and the integration of the calorimetric peaks. To ensure the reliability and consistency of the results, all experiments were performed in duplicate. The obtained results from these duplicate experiments exhibited close agreement, indicating no significant modifications in heat and mass transfer. This enhances the reproducibility and reliability of our findings.

Conclusions
In conclusion, this work presents the synthesis and characterization of a novel series of composites based on corncob, an agricultural waste, for long-term heat storage applications. The composites were successfully synthesized by impregnating MgSO 4 onto corncob biochar and extensively characterized using XRD, BET, and SEM techniques. The CO 2 sorption results revealed that the corncob biochar support exhibited a small microporous surface area of 175 m 2 /g while displaying an enhanced macroporous structure. This unique feature allows for the homogeneous deposition of a large quantity of salt within the composites. Among the prepared series, the 20MgCC composite demonstrated the best performance, with an impressive energy storage density of 635 J/g at Tads = 30 • C and RH = 60%. This achievement highlights the superior energy storage capabilities of corncobbased composites developed in this work compared to the existing literature (please see Table 3). The hydration mechanism of the synthesized composites was well described by the intra-particle model, wherein water molecules diffuse through a homogeneous layer of salt deposited on the surface and inside the larger pores of the composites. The cyclability of the MgSO 4 /biochar composites was confirmed through six hydration/dehydration cycles, demonstrating the stability and durability of the 20MgCC composite. One of the significant achievements of this work is the utilization of biosourced materials, specifically corncob-derived biochar, as a constituent of heat storage composites. This accomplishment contributes to advancing green management practices in thermal energy applications. The use of biomass sources for biochar production offers opportunities for circular economy practices, reduced carbon footprint, and enhanced system sustainability. The abundance of biomass types available for biochar production opens up new avenues for the research and development of environmentally friendly heat storage materials. Overall, this study provides valuable insights into the synthesis and characterization of corncob-based composites for long-term heat storage, showcasing their potential for sustainable energy management.
The superior performance of the 20MgCC composite and the utilization of biosourced materials demonstrate the possibility of achieving more efficient and environmentally friendly heat storage solutions. Further research and comparative studies with a broader range of composites will be valuable for a comprehensive evaluation of the specific achievements and advantages of the developed materials over the existing literature.