Synergy effect of peroxidase enzymes and Fenton reactions greatly increase the anaerobic oxidation of soil organic matter

In temperate rainforest soils of southern Chile (38 °S), there are high rates of soil organic carbon (SOC) mineralization under oxygen (O2) limitation. We study the combined effects of Fenton reactions and the activity of two enzymes manganese peroxidase (MnP) and lignin peroxidase (LiP), which was hypothesised potentiate SOC mineralization under anoxic conditions leading to carbon dioxide (CO2) release. Both mechanisms produce free radicals when competing for SOC oxidation in the absence of microorganisms. We quantify the CO2 release by induced Fenton reactions in combination with MnP and LiP under aerobic and anaerobic conditions (20 °C, 36 h) in temperate rainforest soils. CO2 levels released by Fenton reactions and enzyme activity were eight times higher than those released by Fenton reaction and peroxidase enzymes in individual treatment. Approximately 31% of the CO2 released under aerobic soil incubation was found to be abiotic (sterilized), while 69% was biotic (non-sterilized soils), and respective values of 17% and 83% were recorded under anaerobic conditions. The relative fluorescence intensity clearly shows ·OH radicals production from Fenton reactions. In conclusion, levels of MnP and LiP coupled with Fenton reactions strongly increase SOC mineralization under long periods of O2 limitation in temperate rainforest soils.

Our current understanding of iron (Fe) as a driver of abiotic CO 2 release comes almost exclusively from tropical soils with high Fe content 1,2 . The effects of warm temperatures, high rainfall (> 3,000 mm year −1 ), topography, and vegetation on rapid soil organic matter (SOM) decomposition have been studied intensively in tropical soils [3][4][5] . Despite the importance of these studies, the contributions of combined mechanisms, Fenton reactions and the enzyme activity of manganese peroxidase (MnP) and lignin peroxidase (LiP) to CO 2 release from temperate rainforest soils have never been explored. MnP and LiP catalyse a variety of oxidative reactions 6 and can persist in anaerobic soil microsites 7,8 . Fenton reactions in combination with the activity of these enzymes can potentiate SOC mineralization due to the production of free radicals (strong oxidants of SOM) competing for soil organic matter (SOM) oxidation under anoxic conditions. This perspective challenges the traditional assumption that the soils of humid temperate rainforests, especially under high levels of precipitation, mineralize slowly due to a high proportion of anaerobic soils microsites. More and more evidence of abiotic mechanisms involving Fe redox processes that can lead to substantial C losses has been reported 3,4 . In anaerobic microsites, Fe transfers electrons during redox reactions, which can serve as an energy source to produce free radicals (e.g., hydroxyl radicals) for the abiotic oxidation of soil organic carbon (SOC) 1,9,10 . Hydroxyl radicals are strong non-selective oxidants that can attack similar to the lignin structures of SOM 6,11 . Thus, LiP and MnP combined with Fenton chemistry may accelerate C turnover in soils with high Fe content.
We hypothesize that Fenton reactions in combination with the activities of ligninolytic enzymes form a complementary mechanism of CO 2 release, enhancing the oxidation of SOC under O 2 limitation conditions in the absence of microorganisms. The objective of the present study was to quantify C release by Fenton reactions at different ratios of H 2 O 2 :Fe(II) in combination with MiP and LiP in temperate rainforest soils. To broaden the scope of our study, we evaluated three soil types differing in Fe content, pH, and parent material origin.

Results
Abiotic and biotic incubation. After 36 h of incubation, similar patterns of CO 2 release were recorded in all soils. The highest values were found during the aerobic incubation of non-sterilized soils (biotic). Volcanicallophanic soil showed the highest levels of CO 2 (172 mg C kg −1 ) followed by Metamorphic and Granitic soils ( Fig. 1A-C, Table S1, Supplementary Information). The lowest levels of C mineralization were recorded in sterilized soils (abiotic) under anaerobic incubation. These results are consistent with the consumption of hydrogen peroxide; Anaerobic abiotic, where Fenton reactions are assumed to occur, showed the highest levels of H 2 O 2 consumption while aerobic biotic incubation showed the lowest (Fig. 1D-F). However, Fenton reactions did not show the maximum Fe(II)-HCl extractable, it was higher for Anaerobic biotic (Fig. 1G-I). CO 2 from Aerobic abiotic and abiotic presented similar levels of H 2 O 2 consumptions and iron solubilisation. On average, 31% of all CO 2 released via aerobic incubation was purely abiotic and 69% was released through microbial respiration   2G-I) were higher for Anaerobic biotic followed by Anaerobic abiotic. Iron from the last incubation was not different than others treatments. All these results were expected and are discussed in the corresponding section.
Summing up the total CO 2 released from aerobic incubation, 31% was purely abiotic and 69% corresponded to biotic microbial respiration. While in anaerobic incubation, these values were 17% and 83%, respectively (Fig. 3).
Induced Fenton reactions and enzyme lignin peroxidase and manganese peroxidase. CO 2 released by Fenton reactions induced by the addition of various H 2 O 2 :Fe(II) ratios presented significant differences (p = 0.03) (Fig. 3, Table S2, Supplementary Information). The optimum Fenton reaction was found to present a H 2 O 2 :Fe(II) ratio of 10:1 for Metamorphic soil, showing the highest CO 2 value (25 mg kg −1 ) (Fig. 3A). Enzymatic activity. The enzyme concentration (soluble crude protein) obtained from the cultured filtrates of white rotted fungi grown after five days of incubation was 614 μg ml −1 . LiP varied between 5 and 25 μg g −1 , and MnP ranged from 6 to 75 μg g −1 (Fig. 4). Enzyme activity differed across the soils. LiP steadily increased in the following order: Granitic < Metamorphic < Volcanic-allophanic (Fig. 4A). For, MnP the opposite was found (Fig. 4B).
Relationships between variables measured. A positive and significant relationship was found between CO 2 and H 2 O 2 and between CO 2 and Fe(II)-HCl. Similar results were obtained for the correlation between and H 2 O 2 and Fe(II)-HCl (p < 0.01, R 2 > 0.86, Fig. 5) (Table S3, Supplementary Information). The regression slope for the Fenton + MnP + LiP treated soils was measured as eight times higher than those of the Fenton reaction and MnP + LiP experiment alone (Fig. 5).
Iron balance. After 36 h of incubation, the solubilization of Fe(II)-HCl averaged 5 g kg −1 . At the beginning of the incubation period, the average amount of Fe(II)-HCl extractable was 4.05 g kg −1 in the soil (Table 1). When we add the amount of Fe(II) (1.29 g kg −1 ) to the initial amount of Fe(II)-HCl, the total quantity of Fe(II)-HCl is 5.34 g kg −1 , which is close to the initial average of iron of soil. Thus, we assume that Fenton reaction reused Fe(III) produced as ferric oxyhydroxides in the range of pH found in the studied soils (3.6-5.1).
Fluorescence intensity. A significant relationship was found between the relative fluorescence intensity and the concentration of hexanol oxidized (Fig. 6). The highest regression slope was found for Metamorphic soils (446.4 a.u. mM −1 ) (Fig. 6B), coinciding with the highest Fe levels found in this soil (Table 1). Maximal hydroxyl radical production at a H 2 O 2 :Fe(II) ratio of 10:1 was found in Metamorphic soils as observed from Confocal images (Fig. 7H). All soils exhibited high levels of relative fluorescence intensity compared to the control soils without H 2 O 2 and Fe(II) additions (c.f. Fig. 7D-F with 7G-I).

Discussion
Under aerobic incubation, approximately 31% of all CO 2 released was abiotic and 69% was biotic. The lowest levels of organic C mineralization occurring during anaerobic and sterilized soil incubation correlate well with H 2 O 2 consumption (Fig. 1). These results are attributed to Fenton reactions, since Fe(II)-HCl extractable were accumulated in soil and H 2 O 2 was consumed to produce free radicals (Fig. 6). In the studied soils we found traces of H 2 O 2 ( Table 3) due to aeration and sample handling. We assumed that initial H 2 O 2 in Anaerobic-abiotic treatment prior to incubation, triggered Fenton's reactions, which proceed in two steps. First, by oxidizing Fe(II)-Fe(III)   2 17 . Reduced and precipitated iron is continuously reused by Fenton reactions under anaerobic conditions and this should be the reason for similar amounts of iron found at the beginning and end of incubation.
On the other hand, the highest cumulative Fe(II) HCl-extractable were found in Anaerobic biotic incubations (non-sterilized soils). This can be explained due to the presence of obligated anaerobic Fe reducing bacteria, which were found in abundance in the same soils studied here (Merino et al. personal communication). Microorganism for methane oxidation involving iron reduction is also well documented 18 . Biotic factors, other than microorganisms, for example, ligninolytic enzymes activity can be preserved by clay minerals, even in sterilized soil 19 (see discussion below). Abiotic mechanism, such as ferrous wheel, where SOM reduces Fe(III) to Fe(II), which is again oxidized in the presence of nitrate is also possible. This mechanism probably occurred in abiotic aerobic treatment 14 , that can explain the ferric iron release. Peroxidases enzymes activity could be well preserved in sterilized soils as well 19 .
Fenton reactions in combination with extracellular enzymes LiP and MnP mineralized eight times more CO 2 than what was recorded in separated experiments (Fig. 3). These results are in line with the hypothesis that both Fenton reactions and enzyme activity involving MnP and LiP contribute considerably to SOC oxidation in temperate rainforest soils (Fig. 3). From the linear relationship found it can be determined that one mole of H 2 O 2 yielded 0.5 mol of CO 2 or that one mole of Fe(II) is required to consume 0.08 mol of H 2 O 2 during www.nature.com/scientificreports/ Fenton + LiP + MnP treatment (Fig. 5). As previously indicated, this can be partially attributed to the potential preservation of enzyme activity in the soil matrix. This is an important and less widely considered mechanism where LiP and MnP are especially preserved in the clay minerals 7,8 . MnP and LiP remained active for extended periods of time, though they were sensitive to soil pH 20 . MnP and LiP activity in soil has been found to be 20-130 times higher than the activity of free enzymes in soil solution 8,21 . In our case, although the pH did not change throughout incubation, LiP was higher in Volcanic-allophanic soils (pH 5.1) and lower in Granitic soil (pH 3.6). In contrast, MnP activity increased as soil pH decreased (Fig. 4). Soil pH is an important regulator of enzyme stability, and this was notable in the case of LiP, which is less stable than MnP 20 . This mechanism can also explain the high potential oxidation capacity of the combined effects of Fenton reactions and enzymes on SOC mineralization. While LiP degrades lignin in soils with high pH levels, MnP does so in harsh environments with low pH levels. Our results are also supported by investigations of tropical soils, where Fe 2+ involved in Fenton reactions and likely enzymatic activity substantially increased the rate of SOM decomposition 1,11,22 . Direct evidence of Fenton reactions producing free radicals was also found from the relative fluorescence intensity and from the detection of free radicals by hexanol oxidation (Figs. 6, 7) 23,24 . The oxidation of DCFH 2 by hydroxyl radical is irrefutable 25 . Free radical-like ·OH produced from Fe 2+ and H 2 O 2 added to soil can mediate the oxidation of DCFH 2 through Fenton reactions. In the past it was believed that peroxidases similar to MnP and LiP interfered with DCFH 2 oxidation. Now is clear that neither H 2 O 2 nor Fe 2+ is directly involved in DCFH 2 oxidation while peroxidases and soluble Fe(II) may work as efficient catalysts 25 . Other oxidative mechanisms cannot be discarded. During anaerobic abiotic incubation, Fe(II) can react with nitrate present in soil solution, releasing CO 2 14 . Several chemical substances can serve as alternative electron acceptors (e.g. sulphates, semiquinones) for the oxidation of SOC. These mechanisms can be thermodynamically favourable depending on reducing substrates available and soil pH levels 26 . Under anaerobic biotic conditions, iron reducing bacteria (IRB) can solubilize Fe(II) from Fe(III) releasing CO 2 as well 27,28 .
In conclusion, when O 2 is removed from soil, SOC is vulnerable to intense abiotic oxidation. This is likely the case because abiotic-mediated Fenton reactions in combination with exoenzymes LiP and MnP activities compete for SOC oxidation. Both are able to produce free radicals to oxidize lignin-like compounds. Radical ·OH reacts rapidly with nearly all organic molecules, either by abstracting hydrogens from aliphatic structures or by adding as an electrophile to aromatic ones 29

Methods
Study sites and sampling. Three soil types were selected ( Table 2). The first was an Andisol 31 (Volcanicallophanic) formed from recent Volcanic ash deposited in the Andes. This was collected from a native temperate rainforest dominated by old growth Nothofagus betuloides (Mirb.) located in Puyehue National Park, where mean annual precipitation is typically > 8,000 mm year −112 . The soils are derived from basaltic scoria with high levels of allophane, imogolite, and ferrihydrite material 32 . The second soil type was an Ultisol (Metamorphic) sampled in Alerce Costero National Park in the coastal range. It is derived from Metamorphic-schist with high levels of illite-kaolinite 33 . Finally, an Inceptisol (Granitic) was selected from an ancient Araucaria araucana and Nothofagus pumilio forest in Nahuelbuta National Park. This soil type originates from intrusive Granitic rock parent materials. Mean annual precipitation in this ancient forest reaches > 1,491 mm and mean annual temperatures reach 13.3 °C 34 (Table 2). From each soil sample, four composite soil samples were taken from the Ah mineral horizon (5-10 cm) after removing litter and organic horizons. The samples were then transported to a laboratory under cold conditions. All soils were homogenized and sieved (< 2 mm). Hereafter, all derived soils are identified as Granitic, Volcanic-allophanic and Metamorphic.
Analytical procedure. pH and electrical conductivity were directly measured in an aliquot of soil in a 1:2.5 suspension of soil:water. Soil organic C was determined using TOC-VCSH (Shimadzu, Kyoto, Japan), and total N was determined by Kjeldahl distillation (VELP, Usmate, Italy). For the determination of Fe (Fe o ) and Mn (Mn o ), 0.2 M ammonium oxalate at pH 3 was used 35 . Iron and Mn complexed with SOM (Fe p and Mn p ) were obtained using a solution of 0.1 M sodium pyrophosphate 36 . Dithionite-citrate-bicarbonate (Fe d ) was used to identify exchangeable, crystalline, and complexed-SOM metals in the samples (see 36 for further details). Fe   ), and Si (Si o ) were also determined as described above. Cation exchange capacity (CEC) and nutrient characterization were conducted as indicated by Sadzawka et al. 35 ( Table 3). The total Fe concentration was determined from 100 mg of soil by adding 0.9 ml of 0.28 M hydroxylamine hydrochloride (2%) and 1 ml of 0.28 M HCl 26 . Approximately 100 μl of the extract was added to 4 ml of colour reagent (1 g ferrozine in a 6.5 M ammonium acetate solution). The amount of reduced iron Fe(II) (or Fe 2+ ) was quantified from 0.1 g of soil added to 1 ml of 0.5 M HCl (now on Fe(II)-HCl) 34 and shaken vigorously. Approximately 100 μl of this suspension was added to 4 ml of colour reagent (1 g ferrozine in 6.5 M ammonium acetate solution). The ferrozine complex standard was prepared with ferrous ethylene diammonium sulphate dissolved in 0.5 M HCl 37 . Fe 2+ was determined spectrophotometrically at 562 nm (absorbance ferrozine-Fe 2+ complex) after the colour developed. The concentration of oxidized Fe(III)-(oxyhydr)oxide was determined by calculating the difference between total Fe and Fe 2+ concentrations (Table 1). Soil sterilization. Soils used for the incubation experiment (see below) were sterilized in an autoclave for 20 min at 121 °C for 3 consecutive days to remove the microbial population with resistant structures such as endospores and conidia. Furthermore, soils were fumigated with chloroform vapour in a vacuum chamber for 24 h 38 . Autoclaving was used because it does not create significant changes in the SOM structure, mainly leading to changes in carbohydrate and N-alkyl regions of the 13 C-CP/MAS spectra due to the lysis of microorganisms and the subsequent loss of microbial C in the aqueous phase 39 . Gamma radiation was avoided because some reports indicate that it causes Fe reduction and oxidation [40][41][42] . Gamma radiation increased the bioavailability of Fe(III)(oxyhydr)oxide minerals, which resulted in increased Fe(III)(oxyhydr)oxide reduction 43 .
Microorganism culture and enzyme extraction. White rot fungi were isolated from wood logs in the same areas where soil sampling was conducted. The white rot fungi were cultured and maintained in Koroljova-Skorobogat'ko medium at pH 5 44 . This is a typical medium used to grow fungi for enzymatic extraction when required 45,46 . The medium (g l −1 ) consisted of: 3.0 peptone, 10.0 glucose, 0.6 KH 2 PO 4 , 0.001 ZnSO 4 , 0.4 KH 2 PO 4 , 0.0005 FeSO 4 , 0,05 MnSO 4 , and 0,5 MgSO 4 and the fungi exhibited strong growth 45,46 . Sterile Koroljova-Skorobogat'ko medium was dispersed into sterile 250 ml Erlenmeyer flasks at a rate of 50 ml of medium per flask. The flasks were inoculated with homogenized mycelia suspension and incubated in an orbital shaker at 30 °C and at a rate of 200 rpm. The flasks with growing cultures of white root fungi were removed at different time intervals over the course of the experiment for processing. MnP and LiP were isolated from fungal culture slants in a Koroljova liquid broth medium (10 ml) after 24, 48, 72, 96 and 120 h to obtain mycelia and spores by centrifugation at 4 °C (10,000 rpm for 10 min). All purification and protein concentration steps were performed at 4 °C. Small pre-weighed quantities of ammonium sulphate were added to 250 ml of culture supernatant from 20 to 80% saturation. Each precipitated fraction was separated by centrifugation at 10,000 rpm for 15 min at 4 °C, dissolved in a minimum volume of 0.1 M Tris-HCl (pH 9.0) and dialyzed twice for 6-8 h against the same buffer. The dissolved fractions were stored at 4 °C. Ligninolytic enzyme activity (LiP and MnP) was estimated in the crude culture filtrate and ammonium sulphate precipitates using the standard protocols described below.
Enzyme assay. MnP activity was measured by the oxidation of MnSO 4 (1.0 mM) substrate. Reactions were conducted in a 3 ml cuvette containing 2.5 ml of buffer (20 mM sodium tartrate at pH 4.5), 1.0 ml of substrate, 1.0 ml of enzyme extract from the supernatant, and 0.5 ml of 2.0 mM H 2 O 2 . Manganese peroxidase was determined spectrophotometrically at 238 nm 47 . Lignin peroxidase was evaluated using veratryl alcohol (2.0 mM) as a substrate. The reactions were carried out in 3 ml cuvettes containing 1.25 ml of 50 mM sodium tartrate buffer at pH 2.5, 0.5 ml of enzyme extract, 0.25 ml of substrate, and 0.5 ml of 500 μM H 2 O 2 . Lignin peroxidase was measured at 310 nm. All oxidative enzymatic activities were expressed as units (U) per millilitre (i.e., one millimole of substrate oxidized per minute) 48 .
The standard Bradford method was used to estimate the concentration of proteins in the supernatant. Bovine serum albumin (BSA) was used as a standard. One millilitre of enzyme extract was mixed with 1 ml of Bradford reagent (Amresco, USA) and incubated for five days. Protein concentrations were measured at 595 nm. Approximately 3 ml of mixed enzyme extract was used for the identification of MnP and LiP. We used Type II horseradish peroxidase (Sigma Aldrich) dissolved in phosphate buffer as an enzyme standard. HPLC-MS/MS (GE Healthcare, USA) was used for protein separation. The outflow was monitored at 280 nm for protein detection. The fractions were assayed for MnP and LiP activity and total protein content. Experiment 1: incubation under biotic and abiotic conditions. Four replicates of 13 g of moist (80% of field capacity) sterilized soil (abiotic) and another portion of non-sterilized soil (biotic) were incubated in serum bottles (120 mml) at 20 °C in anaerobic conditions. Another round of abiotic and biotic incubation was conducted under aerobic conditions. Serum bottles were equipped with a septum for gas sampling. Anaerobic incubations were previously tested by injecting oxygen-free gas (N 2 ) into the headspace of each serum bottle until < 2% O 2 was reached (PCE Instrument model PCE-228-R, Germany) 49 . Anaerobic conditions were monitored and CO 2 was collected after 0.3, 4, 8, 12, 24 and 36 h of incubation. Preliminary studies indicate that after further incubation for > 3 days, CO 2 levels increased little. For gas sampling, 10 ml was extracted using a syringe, and this was then injected into a gas chromatograph coupled with thermal conductivity and a flame photometric detector. The initial H 2 O 2 content from each soils were determined previously to sterilization and ranged between 25.6 ± 0.7 and 33.7 ± 0.5 µM g −1 soil (Table 3).
Free radical detection. The presence of hydroxyl radicals in the soil was first tested using hexanol substrate. Approximately, 5 g of each sterilized soil (13 replicates) was incubated for 36 h in anaerobic conditions with 5 ml of hexanol (2 mM) (Sigma-Aldrich). A H 2 O 2 :Fe(II) ratio of 10:1 was used to induce Fenton reactions (see below). Hydroxyl radicals do not react strongly with the superoxide anion but with hexanol, as hydroxyl radicals oxidize preferentially short-range organic molecules 23,24 . In total, 39 soil samples were analysed for 10 randomly selected regions of interest (ROI, 33,489 μ 2 ). Hexanol oxidation was calculated as the difference between the initial amount and the amount of hexanol remaining. The hexanol was quantified using a Hewlett-Packard 5890A gas chromatograph (Thermo Fisher, Waltham, Massachusetts USA) with a flame ionization detector equipped with a 15 m × 0.53 mm DB-1 capillary column.
In the fluorescence experiment, the generation of ·OH radicals was examined in anaerobic and sterilized soils using a 2′,7′-dichlorodihydrofluorescein diacetate (DCFH 2 ) 25 fluorescent probe in an excitation/emission of 488/530 nm and via laser scanning confocal microscopy (CLSM) (Olympus Fluoview 1000, Florida, USA). Maximum fluorescence emissions were found for a ratio of 10:1 H 2 O 2 :Fe(II). Using a closed vacuum plate with 50 μl of the fluorescent DCFH 2 probe 56 , the samples were analysed for free radicals after 36 h of incubation 57 . The emissions observed using CLSM were attributed to hydroxyl radicals reacting in the soil. The images were processed using image processing software (software FV10-ASW v.0.2c), and fluorescence intensity was expressed as relative fluorescence (AU) as given by the software. A control soil without H 2 O 2 and Fe(II) additions was also included.
Statistical analysis. Two-way ANOVAs were conducted to determine significant differences in CO 2 released, hydrogen peroxide consumed, and Fe(II)-HCl solubilized for experiment 1. To test differences for the same variables in the second, third, and fourth experiments, one-way ANOVAs were performed. Regressions between CO 2 and H 2 O 2 or Fe(II)-HCl extractable and between H 2 O 2 and Fe(II)-HCl extractable were performed. All analyses were conducted using XLSTAT software by Addinsoft (Premium) 2019, version 4.1. Significant differences were set at a p value of 0.05. Datasets were tested for normal distributions and homoscedasticity. Datasets abnormally distributed were log transformed when necessary. (