Effects of Slow Pyrolysis Biochar on CO 2 Emissions from Two Soils under Anaerobic Conditions

: The amendment of sandy Haplic Arenosol and clayey loam Gleyic Fluvisol with two rates of biochar derived from the slow pyrolysis of wood feedstock was evaluated under anaerobic conditions in a 63-day laboratory experiment. The rates of biochar were 15 and 30 t ha − 1 . Both rates of biochar were applied either with or without 90 kg ha − 1 of nitrogen fertilizer (NH 4 NO 3 ). Soils with no amendments were used as control treatments. Our results showed that only the incorporation of 15 t ha − 1 of biochar, compared with the control treatment, led to a signiﬁcant ( p < 0.05) increase in volumetric water content of the sandy soil and a signiﬁcant ( p < 0.05) decrease in the parameters of the clayey loam soil. Increasing the biochar rate from 15 to 30 t ha − 1 did not result in signiﬁcant changes in volumetric water content in either type of soil. In the sandy soil, CO 2 emissions were signiﬁcantly ( p < 0.05) higher in the treatments of 15 and 30 t ha − 1 with N fertilizer compared with the control and N fertilizer treatment. In the clayey loam soil, the combined application of both rates of biochar with N fertilizer caused no signiﬁcant increase in CO 2 emissions compared with the control and N fertilizer treatment. The incorporation of 30 t ha − 1 of biochar into the sandy soil contributed to a signiﬁcant ( p < 0.01) increase in the cumulative CO 2 ﬂux compared with the control treatment. Application of 15 and 30 t ha − 1 of biochar into the clayey loam soil led, respectively, to a signiﬁcant ( p < 0.05) and a nonsigniﬁcant increase in the cumulative CO 2 ﬂuxes compared with the control treatment. Author Contributions: Conceptualization, J.H., E.B., N.B. and V.Š.; methodology, E.B. and J.H.; investigation E.B., N.B., V.Š. and J.H.; resources, E.B. and J.H.; data curation, E.B.; formal analysis E.B., N.B., V.Š. and J.H.; writing—original draft preparation, J.H., E.B. and V.Š.; writing—review and editing, N.B.; validation; visualization, E.B.; project administration, J.H.; funding acquisition J.H.


Introduction
One of the main challenges of modern agriculture is resource conservation, based on the principle of protecting the environment. By regulating the land-based placement of waste, we can enhance long-term carbon sequestration in the soil and mitigate the amounts of greenhouse gas emissions released into the atmosphere. An increase in the carbon sequestration in the soil is associated with changes in land use or with changes in agricultural management practices.
In recent decades, scientists have proposed converting renewable biomass, which is not suitable for direct use in the economy, into biochar. Biochar is a carbon-rich product that occurs when biomass (wood, manure, and crop residues) is heated in pyrolysis chambers (at temperatures up to 900 • C) with little or no available oxygen [1][2][3][4][5]. Biochar has the potential to enhance atmospheric carbon sequestration because of its high chemical stability [6][7][8].
Biochar sequestration can be carbon-negative and therefore contribute to CO 2 removal from the atmosphere, with implications for the mitigation of climate change. Biochar can be used in agriculture as its long-term stability in soils make it a useful soil conditioner [9][10][11].
The composition of initial feedstock for biochar production, pyrolysis temperature, and time of heating are crucial factors that can affect the properties of the final product. Biochars produced under different conditions can have different physical (bulk density and porosity), physico-chemical (pH, cation exchange capacity, surface area, and oxygencontaining functional groups), and chemical (total carbon, nitrogen, and hydrogen content) properties, which, in due course, can have positive, neutral, or negative effects on soil properties [1,[12][13][14].
Despite the positive feedback from the scientific community on the usage of biochar, there are critical knowledge gaps that exist in the literature. These include knowledge about the availability of plant nutrients in soil under the effect of biochar and the possibility of a priming effect of biochar application on soil organic matter [27]. Incorporation of fresh, non-oxidized biochar to soils can result in an increase in CO 2 emissions because of mineralization (priming effect), mainly of labile forms of soil organic matter. These forms of soil organic matter do not participate in the humification of the clay fraction of soil [28][29][30]. Nevertheless, the intensity of mineralization of labile organic compounds could decrease with an increasing degree of biochar oxidation, related to its long-term stay in the soil [31]. However, there remains a need for further research on changes in the degree of the slow or fast pyrolysis-induced aromatization of biochar, and mineralization of its aliphatic structures affected by soil biotic (microorganisms) and abiotic (moisture content, temperature, specific heat, thermal conductivity, and nitrogen availability) factors. These factors also affect the intensity of carbon sequestration in soils and CO 2 emissions from soils under different physical and physico-chemical conditions [32][33][34][35].
Slow pyrolysis biochars, in comparison with fast pyrolysis biochars, often demonstrate higher porosity, a higher content of nutrients and organic substances, and, as a result, a greater ability to improve soil aeration and microbial conditions to mitigate CO 2 emissions from soils [36]. However, an increase in soil bulk density and a decrease in aerated pore volume following heavy rains, for instance, can result in the formation of soil anaerobic conditions, which contribute to the increasing rate of CO 2 emissions from soils. The increase in the rate of CO 2 emissions from soils, even those amended with biochars and nitrogen fertilizers, can be induced by enhancing microbial mineralization of soil organic matter or the aliphatic structures of biochars [37][38][39]. On one hand, under anaerobic soil conditions, biochars have the potential to decrease anaerobiosis in coarse-textured soils, but not in fine-textured soils, which have a higher water retention capacity because of a higher content of clay particles and greater volume of micropores. On the other hand, water-saturated, porous biochars themselves can contribute to the formation of anaerobic conditions in soils. Therefore, the mechanisms behind the different effects of biochars on carbon transformation and CO 2 emissions from soils under anaerobic conditions remain obscure.
The objective of this study was to assess the effects of two rates of slow pyrolysis biochar on CO 2 emissions from sandy and clayey loam soils under anaerobic conditions. It was hypothesized that both rates of the biochar would be more effective in decreasing CO 2 emissions from the sandy soil than from the clayey loam soil, under similar anaerobic conditions.

Experimental Site
A 63-day laboratory experiment was carried out to fulfill the study objectives. The two studied soils were classified as Haplic Arenosol (sandy soil) and Gleyic Fluvisol (clayey loam soil) and were located in Rišňovce (48 • 21 788" N, 17 • 54 685" E) and Janíkovce (N48 • 6 933" N, 18 • 07 031" E), Slovakia, respectively. Disturbed soil samples were collected from the upper 0-20 cm layers. The sandy soil contained 924 g kg −1 of sand, 53 g kg −1 of silt, Agriculture 2022, 12, 1028 3 of 12 and 5 g kg −1 of clay, whereas the clayey loam soil contained 288 g kg −1 of sand, 417 g kg −1 of silt, and 295 g kg −1 of clay. Soil organic carbon content in the sandy soil ranged from 12.95 to 13.19 g C kg −1 soil and in the clayey loam soil, from 15.86 to 16.20 g C kg −1 soil. Values of soil pH (KCl) were equal to 6.83 (sandy soil) and 6.25 (clayey loam soil).
Biochar (BC) was produced from branch clippings of broad-leaved trees at a temperature of 500-600 • C in a Pyreg reactor (Pyreg GmbH, Dörth, Germany). The diameter of BC particles was ≤3 mm. The physico-chemical properties of BC included: a specific surface area of 123 m 2 g −1 , 6.20% oxygen, 0.63% hydrogen, 76.7% carbon, 0.64% nitrogen, and a pH (KCl) of 9.1. We used the Hekatech Euro EA elemental analyzer (Wegberg, Germany) to measure concentrations of the elements.

Experimental Design
The laboratory pot trial was conducted with the following treatments: 1.
Before the experiment, air-dried soil samples were mixed with the BC and N fertilizer and moistened to the field capacity. The field capacity of both soils was considered 50-55% of the full saturation. The full saturation of the sandy soil ranged from 50 to 58% (of weight) and of the clayey loam soil, from 62 to 66% (of weight). The moistened soil samples were placed into steel pots (95 cm 3 ). The amount of soil in every steel pot was equal to 120-125 g (dry weight). The specific surface area of the steel pot was 19.625 cm 2 . The selected rates of BC were 15 and 30 t ha −1 . These rates of the BC in t ha −1 were converted into rates in g cm −2 , and then into rates in g per pot, and were equal to 2.94 g and 5.88 g per pot, respectively. The recalculated rate of nitrogen fertilizer (90 kg N ha −1 ) was equal to 0.08 g per pot. The 63-day incubation of soil samples was conducted at room temperature. The soil samples in pots were regularly weighed to maintain the required moisture content in both soils for all treatments. The experiment was carried out in six replicates.
To measure CO 2 emissions, the soil pots were placed into plastic vessels (1000 cm 3 ) with airtight lids equipped with sealed rubber septa. For every air sampling, the plastic vessels were sealed for 20 min and air samples were collected from the headspaces with a syringe and transferred to pre-evacuated 12 mL glass vials (Labco Exetainer, Lampeter, UK). The collected air samples were analyzed for CO 2 concentration using a gas chromatograph (GC-2010 Plus Shimadzu, WTW SPECTRIOLEX, 6100, Weilheim, Germany) equipped with a thermal conductivity detector. The GC was calibrated using three certified standard gas mixtures of CO 2 in the expected concentration range. Helium was used as a carrier gas (30 mL min −1 ).
The volumetric water content in the soils was calculated by multiplying the soil water content (% of weight) by the soil bulk density. The soil water content (% of weight) was measured by a common thermogravimetric method using an oven at a temperature of 105 • C. Bulk density (g cm −3 ) of the soil was calculated using the soil volume and the weight of the dry soil.

Statistical Analysis
Statistical assessment of the results included the calculation of means, standard deviations, and standard errors. A one-way ANOVA was applied to evaluate the significance of differences between means of data (https://www.socscistatistics.com (accessed on 18 April 2022). Mann-Whitney U test (https://www.socscistatistics.com/tests/mannwhitney/ default2.aspx (accessed on 18 April 2022) was applied to assess the significance of differences in means (at p ≤ 0.05) if the distribution was not normal according to the Kolmogorov-Smirnov test of normality (https://www.socscistatistics.com/tests/kolmogorov/default. aspx (accessed on 18 April 2022).

Soil Water Content
In studies of soil CO 2 emissions, the volumetric soil water content (VSWC) is an important indicator of soil moisture conditions, which can be favorable or unfavorable for microbial processes of soil organic matter transformation. According to the results of the one-way analysis of variance (ANOVA), there were mostly nonsignificant differences in the VSWC between the treatments of the sandy soil. Only the incorporation of 15 t ha −1 of BC into this soil resulted in a significant (p < 0.05) increase in the VSWC compared with that of the control treatment. The sandy soil demonstrated anaerobic conditions under all the studied treatments. Biochar is a porous organic substance that contains a large volume of macroporosity in the 1 to 10 µm range [40,41]. It can significantly increase the volume of soil macropores, which, in due course, could be saturated by water; consequently, there would be no improvement in soil aeration under anaerobic conditions [42][43][44]. Moreover, pores inside biochar particles provide extra water storage space beyond soil interpore compartments [45]. Therefore, in specific circumstances, biochar can be an additional source of soil anaerobiosis. According to Hardie et al. [25], biocharamended soils have a significantly higher near saturated hydraulic conductivity (at water potentials of −0.25 and −0.10 kPa), total porosity, and soil water retention at the water potential of −0.1 kPa, resulting from the presence of large macropores >∼1200 µm. In the clayey loam soil, there was also no significant difference in the VSWC between most of the treatments. Compared with the VSWC of the control treatment, only the BC rate of 15 t ha −1 resulted in a significant (p < 0.05) decrease in the VSWC of the clayey loam soil. This rate of biochar significantly improved aeration of the soil. The degree of biochar-induced changes in the VSWC depends on soil texture and the rates of biochar [46]. The mean values of VSWC of the clayey loam soil were significantly (p < 0.001) higher than those of the sandy soil in all treatments. The greater amounts of silt and clay particles in the clayey loam soil, compared with the sandy soil, were the main reasons for the significant difference in water retention capacity.

CO 2 Emissions
The dynamics of CO 2 emissions from the sandy and clayey loam soils with different treatments is shown in Figures 1 and 2. The results showed a high variability in daily CO 2 emissions from the sandy soil over the incubation period ( Figure 1A,B). The CO 2 emissions from the sandy soil in the control treatment with N fertilizer were often equal to zero and sometimes even negative (from −1.5 to −180.7 mg CO 2 -C m −2 h −1 ). Therefore, the lowest average daily CO 2 emissions were recorded in this treatment: 10.9 ± 49.5 mg CO 2 -C m −2 h −1 , whereas in the control treatment with no N fertilizer, the average values of daily CO 2 emissions were 41.2 ± 58.5 mg CO 2 -C m −2 h −1 (the difference was not significant). The application of biochar to soils can result in either positive or negative priming [47][48][49]. The proposed mechanism of positive priming after biochar application involves the growth of so-called 'r-strategist' microbes that are adapted to quickly respond to newly available C sources, re-mineralizing soil nutrients, and co-metabolizing more refractory organic matter, such as soil humic substances in the carbon mineralization process. Positive priming can occur at an early stage of the mineralization of the labile organic matter of biochar [30]. Negative priming (i.e., the repression of soil organic carbon mineralization) is caused by soil organic matter sorption to the biochar surface, either within biochar pores or onto external biochar surfaces [50]. These processes can induce a decrease in activity of soil microbial communities [51].
can occur at an early stage of the mineralization of the labile organic matter of bioch [30]. Negative priming (i.e., the repression of soil organic carbon mineralization) is cause by soil organic matter sorption to the biochar surface, either within biochar pores or on external biochar surfaces [50]. These processes can induce a decrease in activity of so microbial communities [51].  The results demonstrated that, in the sandy soil, the incorporation of 15 t ha −1 of BC did not cause a significant increase in daily CO2 emissions, compared with those in the control treatment ( Figure 1A). However, incorporation of 30 t ha −1 of BC resulted in a sig nificant (p < 0.001) increase in CO2 emissions, compared with the control treatment. The rate of 30 t ha −1 of BC could contribute to an enhanced release of available and weakly protected organic substances from organo-mineral complexes of the sandy soil. Applica tion of N fertilizer did not significantly affect the daily CO2 emissions, probably because of a negligible effect of nitrogen on the activity of 'r-strategist' microbes participating in The results demonstrated that, in the sandy soil, the incorporation of 15 t ha −1 of BC did not cause a significant increase in daily CO 2 emissions, compared with those in the control treatment ( Figure 1A). However, incorporation of 30 t ha −1 of BC resulted in a significant (p < 0.001) increase in CO 2 emissions, compared with the control treatment. The rate of 30 t ha −1 of BC could contribute to an enhanced release of available and weakly protected organic substances from organo-mineral complexes of the sandy soil. Application of N fertilizer did not significantly affect the daily CO 2 emissions, probably because of a negligible effect of nitrogen on the activity of 'r-strategist' microbes participating in the positive priming of organic matter under anaerobic conditions. There was a gradual decline in CO 2 emissions over the entire incubation period, which may have been a result of the declining content of microbial biomass carbon [51]. If the available sources of carbon and nitrogen for microorganisms are gradually reduced, the CO 2 emission rates slow down and finally become stabilized. Biochar with N fertilizer could provide an additional source of available carbon and nitrogen to stimulate CO 2 emissions from microorganisms. CO 2 emission could increase with increasing soil porosity and promotion of CO 2 diffusion [52,53]. This was probably the reason why CO 2 emissions were significantly (p < 0.05) higher in the treatments of 15 t ha −1 with N fertilizer and 30 t ha −1 with N fertilizer, compared with the control treatment of the sandy soil, as shown by the statistical results of the Mann-Whitney test ( Figure 1B). The CO 2 emissions from the soil, with the combined application of the biochar (both rates) and N fertilizer, were significantly (p < 0.01) higher than those in the treatment of only N fertilizer application. The statistical results of the Mann-Whitney test showed that the combined application of 15 t ha −1 and N fertilizer resulted in significantly (p < 0.05) higher CO 2 emissions from the sandy soil, compared with the treatment of 15 t ha −1 of BC. By the end of the incubation period, an increase in daily CO 2 emissions was observed in the sandy soil with the treatment of 30 t ha −1 , both with and without N fertilizer. This increase in CO 2 emissions may be due to the positive priming of the soil and biochar organic matter, even 63 days after the start of experiment. In the clayey loam soil, the emissions of CO 2 also showed high variability in all the treatments over the entire incubation period (Figure 2A). Changes in the content of microbial biomass carbon could result in such a pattern of CO 2 emissions from the clayey loam soil [51,52].
The application of 15 and 30 t ha −1 of BC resulted in no significant increase in CO 2 emissions from the clayey loam soil, compared with those in the control treatment (Figure 2A). Maximum CO 2 emissions occurred in both treatments with BC on the 55th day of incubation, and it was most likely related to the maximum activity of the soil microbial community. The daily CO 2 emissions were significantly (p < 0.001) higher from the clayey loam soil than from the sandy soil in the treatment with 15 t ha −1 of BC. In the treatments with 30 t ha −1 of BC, the CO 2 emissions from the clayey loam soil were not significantly higher than those from the sandy soil. These results are inconsistent with the findings of previous studies, which reported that biochar mitigated the mineralization of soil organic matter in clay soils, but strongly enhanced the mineralization of soil organic matter in sandy soils [53].
In the clayey loam soil, the incorporation of the N fertilizer had no significant effect on CO 2 emissions, probably due to the little impact the N fertilizer had on the activity of the microbial community under anaerobic conditions. Nevertheless, the application of N fertilizer on the clayey loam soil resulted in significantly (p < 0.01) higher CO 2 emissions than those from the sandy soil with the same treatment. This may be due to a nitrogen-induced formation of higher nutrient availability caused by a cation release that accelerates the microbial degradation of the soil organic matter in the clayey loam soil compared with the sandy soil. The combined application of either rate of BC with N fertilizer on the clayey loam soil resulted in no significant differences in CO 2 emissions compared with those in the control treatment and N fertilizer treatment. There was also no significant difference in CO 2 emissions between the sandy and clayey loam soils in the treatments where the BC (both rates) were combined with N fertilizer. The average CO 2 emissions from the clayey loam soil were higher than the average CO 2 emissions from the sandy soil in the treatments with 15 (p < 0.05) and 30 t ha −1 of BC (p < 0.001). Anaerobic conditions can contribute to an increased decomposition of soil organic matter and to enhanced CO 2 fluxes from soils [47,48]. Higher heterotrophic respiration rates in soils that encounter flooding and subsequent drainage could, therefore, experience a release of labile carbon from organo-mineral complexes directly caused by Fe reduction [47,49]. However, decomposition of soil organic matter may be sustained under anaerobic conditions due to compensatory mechanisms, such as the release and metabolism of mineral-associated carbon [50]. Overall, the clayey loam soil demonstrated no significant differences in CO 2 emissions between all the treatments under anaerobic conditions. In contrast, the sandy soil showed significant differences in CO 2 emissions between the studied treatments with BC under anaerobic conditions. These results indicate that sandy soil may be more suitable for biochar application.

Cumulative CO 2 Fluxes
By the end of the incubation period, the lowest cumulative CO 2 fluxes (kg CO 2 -C ha −1 ) were measured from the sandy soil with the treatment of N fertilizer ( Table 1). The CO 2 emissions from the sandy soil in this treatment were often equal to zero or even negative. As a result, the cumulative CO 2 fluxes showed the lowest values. The incorporation of 15 t ha −1 of BC into the sandy soil led to no significant changes in the cumulative CO 2 flux compared with the control treatment. However, incorporation of 30 t ha −1 of BC into the soil contributed to a significant (p < 0.01) increase in the cumulative CO 2 flux compared with the control treatment. There were also significant (p < 0.01) differences between the cumulative CO 2 fluxes from the soil with 15 and 30 t ha −1 of BC treatments. Table 1. Mean values of cumulative CO 2 fluxes (mean ± standard errors) from the sandy soil and the clayey loam soil with different treatments at the end of the incubation period. Letters a to e, and g and h within each column show significant differences between the mean values of cumulative CO 2 fluxes from the sandy soil and clayey loam soil, respectively, by one-way ANOVA (at p ≤ 0.05).

Treatment Sandy Soil Clayey Loam Soil
Incorporation of 15 t ha −1 of BC with N fertilizer and 30 t ha −1 of BC with N fertilizer into the sandy soil contributed to enhancing the mineralization (or positive priming) of the soil organic matter and, as a result, caused significantly higher cumulative CO 2 fluxes than those from the same soil with 15 t ha −1 (p < 0.01) and 30 t ha −1 of BC (p < 0.05) without N fertilizer treatments. Significant differences in the cumulative CO 2 fluxes were also observed between the sandy soil with the control treatment and the treatments with 15 t ha −1 of BC with N fertilizer (p < 0.001) and 30 t ha −1 of BC with N fertilizer (p < 0.001). Although the application of 30 t ha −1 of BC with N fertilizer led to the highest cumulative CO 2 flux, the flux was not significantly different (p = 0.63) from the cumulative CO 2 flux in the treatment of 15 t ha −1 of BC with N fertilizer (Table 1). In general, the cumulative CO 2 fluxes from the sandy soil increased with an increasing rate of BC without N fertilizer. The incorporation of N fertilizer together with the increasing rate of BC appeared to enhance the activity of the 'r-strategist' microorganisms and accordingly resulted in greater cumulative CO 2 fluxes due to the higher mineralization (positive priming) of soil and biochar organic matter compared with the treatments with BC without N fertilizer. In the clayey loam soil, the incorporation of 15 t ha −1 of BC led to a significant (p < 0.05) increase in the cumulative CO 2 flux, whereas incorporation of 30 t ha −1 of BC made no significant (p = 0.06) contribution to the cumulative CO 2 flux compared with the control treatment ( Table 1). The application of 30 t ha −1 of BC, compared with 15 t ha −1 of BC, resulted in a lower cumulative CO 2 flux, presumably due to the negative priming (or repression of mineralization) of organic matter. This could occur due to a decreasing availability of organic carbon adsorbed onto the external biochar surface or within the biochar or soil micropores.
The cumulative CO 2 fluxes from the clayey loam soil with the treatments of 15 t ha −1 of BC with N fertilizer and 30 t ha −1 of BC with N fertilizer were not significantly higher than those in the N fertilizer only treatment. Nevertheless, the application of N fertilizer with 15 t ha −1 of BC led to a significant (p < 0.05) decrease in the cumulative CO 2 flux from the clayey loam soil. However, the application of N fertilizer with 30 t ha −1 of BC only resulted in a nonsignificant increase in the cumulative CO 2 fluxes from this soil, compared with the treatments of 15 and 30 t ha −1 of BC without N fertilizer.
The economic feasibility of the application of biochar in agriculture depends on two aspects. First, we must demonstrate that biochar, at low and high rates, often contributes to an improvement in many soil quality indicators, an increase in carbon sequestration from the atmosphere, and a decrease in nitrous oxide emission from soils [2,[15][16][17][18][19][20][21][22][23][24][25][26]36,37]. This is an economical benefit of using biochar in the long term. Secondly, we must demonstrate that the application of high rates of biochar can be unprofitable for farmers because of the current high prices of biochar, high application costs, and operational prices of commodities under standard management practices [54]. Therefore, a detailed analysis of the economic feasibility of using biochar should include further studies on the best combination of soil quality and profit in new and standard management practices. Our results are important because they demonstrate both favorable and unfavorable possibilities of soil moisture content and CO 2 emission management using high rates of biochar incorporated into sandy and clayey loam soils under anaerobiosis. These findings can be used for further analysis of the positive or negative priming of organic matter in soils amended with biochar with or without nitrogen fertilizers.

Conclusions
The results of this study showed that biochar application at a rate of 15 t ha −1 to sandy soil led to a significant (p < 0.05) increase in the soil volumetric water content. This rate of biochar enhanced soil anaerobiosis due to an increased volume of water-holding soil macropores. Particles of biochar contain a high volume of water-holding macropores; therefore, they can be an additional source of anaerobiosis. The opposite effect was found for the clayey loam soil: 15 t ha −1 of BC significantly (p < 0.05) improved soil aeration, which was probably related to the increase in macropore volume.
Application of 15 t ha −1 of BC to the sandy soil did not result in a significant increase in daily or cumulative CO 2 emissions from the soil, probably because of the limited availability of carbon incorporated into the soil with the BC. However, application of 30 t ha −1 of BC led to significantly (p < 0.001) higher CO 2 emissions. The rate of 30 t ha −1 of BC may have enhanced the release of available and weakly protected organic substances from the organomineral complexes of the sandy soil. The CO 2 emissions from the sandy soil significantly (p < 0.05) increased when BC was applied together with N fertilizer (both rates). The N fertilizer probably contributed to the increasing availability of carbon and nitrogen because the 'r-strategist' microbes participated in positive priming.
The application of 15 and 30 t ha −1 of BC without N fertilizer did not significant affect the daily CO 2 emissions from the clayey loam soil, probably because the soil labile organic matter in this soil was more protected compared with those in the sandy soil. Compared with the sandy soil, cumulative CO 2 fluxes from the clayey loam soil did not change (30 t ha −1 ) or decreased (15 t ha −1 ) when the BC was combined with N fertilizer. This could have occurred due to the increased negative priming of organic carbon adsorbed onto the external biochar surface or within the biochar or soil micropores, which were unavailable for 'r-strategist' microorganisms in the clayey loam soil. Therefore, we may be able to control the cumulative CO 2 fluxes from clayey loam soil by combining the application of biochar with N fertilizer.
The higher content of adsorbed labile organic carbon in the clayey loam soil could be the reason for significantly greater daily and cumulative CO 2 emissions from this soil than from the sandy soil. Data Availability Statement: The datasets generated and/or analysed for the current study are available from the corresponding author on request.