Twenty mesocosms (0.6 m height, 0.25 m radius) were constructed at the experimental site in the Drie Eiken Campus of the University of Antwerp, Belgium (51° 9.6967^′ N, 4° 24.5132^′ E), and placed outdoors to receive natural rainfall. To allow leachate collection, a 2 cm hole at the bottom of each mesocosm was connected via polyurethane tubing to a glass collector (2.3 L). To prevent soil from leaching into the glass collector, a soil exclusion mat (black woven polypropylene; weight = 100 g m⁻²; BRICO Belgium) covered the bottom of each mesocosm.

The experimental treatments were randomized within the facility in order to minimize differences in sun exposure, and mesocosms were wrapped in reflective foil to avoid excessive heating. In order to compare treatments with and without AMF, all soil was pasteurized by heating for 4 h at 80 °C (Ven et al., 2019; Verlinden et al., 2018). This procedure was intended to substantially reduce the abundance of fungal propagules, particularly AMF spores, while avoiding complete sterilization of the soil. AMF colonization and hyphal length results at the end of the experiment confirmed that pasteurization succeeded, as treatments that were not inoculated (see further) showed clearly lower hyphal length and colonization (Fig. 1).

The bottom 40 cm of all mesocosms was filled with a pasteurized Plaggic anthrosol soil with sandy loam texture (69.5 % sand, 28.1 % silt, 1.8 % clay; Table S1 in the Supplement) originating from a pasture in Zandhoven, Belgium. The initial soil was slightly acidic (mean pH ± SE = 5.6 ± 0.3; soil : water = 1 : 2.5, see further for detailed method), with an organic carbon content of 0.8 ± 0.05 % (mean ± SE; determined by loss-on-ignition at 550 °C for 4 h) and a potential cation exchange capacity (CEC) of 3.9 ± 0.6 meq 100 per g soil (mean ± SE; see further for method). On 23 May 2022, the top 20 cm was filled with non-amended, pasteurized soil for the control treatments (n= 10 mesocosms). To mimic amendment incorporation through ploughing, the top 20 cm of the basalt treatments (n= 10 mesocosms) received pasteurized soil with a mixture of 0.98 kg (equivalent to 50 t ha⁻¹) of freshly mined Eifel Basalt (Table 1; Rheinischen Provinzial-Basalt- und Lavawerke (RPBL); 50° 41.4833^′ N, 7° 19.1198^′ E), with particle size between 0.02 and 0.2 mm (Fig. S1) and specific surface area (SSA) corresponding to 6.283 ± 0.001 m² g⁻¹ (mean ± SE) measured on three technical replicates with a Quantachrome Autosorb iQ using the Braunauer-Emmet-Teller method. The measurement used nitrogen (N₂) as adsorbate with multi-point (5 points) and isotherm (77 K) settings. The samples were degassed at 300 °C with 200 min of soak time. High measurement quality was ensured by frequent reference (Bundesanstalt für Materialforschung und -prüfung) measurements. Basalt mineralogy was obtained through XRD analysis on samples milled in ethanol for 10 min (Bruker D8 Advance, Cu Kα radiation at 30 mA and 40 kV, 2θ from 5 to 70°). An internal standard (10 wt % Al₂O₃) was added during sample preparation to determine amorphous phase content. Basalt elemental composition (XRF) was provided by RPBL.

On 15 June 2022, two seeds of dwarf corn plants (Zea mays L., 1753; golden midget variety) were sown in each mesocosm to mimic a field density of about 13 plants per m². For half of the treatments (five control and five basalt mesocosms), seeds were inoculated with AMF (Rhizophagus irregularis; Symplanta) prior to sowing. Dry inoculum (40 g) was suspended in 200 mL of deionized water in a glass beaker and thoroughly homogenized. Seeds were subsequently added to the suspension and mixed thoroughly to ensure a uniform coating of the inoculum on the seed surface. The remaining 10 mesocosms (five control and five basalt treatments) received a sterilized inoculum (Table 2), obtained by suspending 40 g of dry inoculum in 200 mL of deionized water in a glass bottle and autoclaving the inoculum at 121 °C for 25 min. In addition, a microbial wash was added to every plant to avoid initial differences in microbial community due to inoculation (Wagg et al., 2011). The microbial wash was obtained by suspending 20 g of dry inoculum in 400 mL of deionized water. After mixing, the liquid inoculum was filtered through a Whatman Grade 41 ashless filter paper (12.5 cm diameter, nominal retention: 20–25 µm, Cat. No. 1441 125, Cytiva), and a few drops were inspected under a microscope to ensure the absence of AMF spores. Afterwards, 10 mL of microbial wash were transferred to each seed before sowing. All pots were fertilized with nitrogen, phosphorous and potassium (NPK; 96–10–39.5 kg ha⁻¹) by adding ammonium nitrate (NH₄NO₃), triple super phosphate (TSP; 45 % P₂O₅) and potassium sulphate (K₂SO₄). The N fertilization amount was similar to that used in Ven et al. (2019), whereas P and K application amounts were halved to avoid overfertilization in combination with the added silicates. To prevent severe drought stress during dry spells, mesocosms were irrigated with rainwater collected in underground tanks. All mesocosms received the same amount of water (285 mm; cumulative over the experimental period).

One mesh bag (13 × 3 × 2 cm) with a mesh size of 30 µm, which is permeable to AMF hyphae but excludes roots, was buried vertically in each mesocosm at a depth of 0–10 cm. The mesh bags were filled with white sand that was preheated in the oven at 550 °C for 5 h to remove organic matter.

During the experiment, several plants were infected with corn smut, a disease caused by the pathogenic fungus Ustilago maydis (DC., 1842). The fungus forms tumours on the aerial parts of its host plant (Matei and Doehlemann, 2016) and can significantly decrease maize yield (Clough et al., 2011). Whenever a plant was infected and a tumour was observed, the tumour was removed from the plant. Fresh weight was determined, whereafter the tumour was dried in the oven at 70 °C for 48 h and its dry weight was recorded. Corn smut weight did not differ among the treatments (Table S2).

From 1 June 2022, soil pore water samples were collected every two weeks using rhizon samplers (Rhizon Flex, Rhizosphere Research Products B.V.) installed vertically at 0–10 cm depth in each mesocosm. Pore water analyses included alkalinity, pH, and concentrations of DIC, aluminium (Al), nickel (Ni), and zinc (Zn). Pore water calcium (Ca), iron (Fe), potassium (K), magnesium (Mg), sodium (Na), ammonium-nitrogen (NH4+-N), nitrate-nitrogen (NO3--N), phosphate-phosphorus (PO43--P), silicon (Si), sulphate (SO42-), copper (Cu) and manganese (Mn) concentrations were also quantified and are reported in Figs. S2–S3. Soil pore water pH was measured with a flat membrane electrode (6.0256.100, Metrohm) connected to a 914 pH/Conductometer (2.914.0020, Metrohm). DIC was measured on three technical replicates with a TOC analyser (Formacs™ HT Series, Skalar) using deionized water as blank and sodium carbonate (EMSURE, Supelco) as standard; whereas alkalinity, NH4+-N, NO3--N, SO42- and PO43--P were measured on three technical replicates by a continuous flow analyser (SAN++^® Advanced Series, Skalar) using sodium carbonate (Certipur, Merck Group) and standard NH4+, NO3-, PO43- and SO42- solutions (Certipur, Supelco) as quality controls respectively. DIC, NH4+-N, NO3--N, PO43--P and SO42- analyses were conducted in-house on samples filtered through a disposable 0.45 µm PET-45/25 membrane filter (CHROMAFIL, Macherey-Nagel). Elemental analyses were performed by inductively coupled plasma-optical emission spectrometry (ICP-OES, DSOI SpectroGreen, SPECTRO) in the Helmholtz Laboratory for the Geochemistry of the Earth Surface (HELGES) on samples filtered through a disposable 0.2 µm PET-20/25 membrane filter (CHROMAFIL, Macherey-Nagel) and acidified with 10 mL 65 % nitric acid (HNO₃), using international water reference material SLRS-6 (NRC-CNRC) as quality control. Alkalinity measurements were carried out in-house on unfiltered samples.

Measurements of soil chemical fertility (here defined as soil pH, CEC and base saturation) were performed on soil samples collected before basalt application and on topsoil samples (0–20 cm) collected at the end of the experiment (12 September 2022). Topsoil pH was measured by collecting, pooling and air-drying three subsamples per mesocosm. Subsequently, 4 g of soil was dissolved in 10 mL deionized water (soil : water = 1 : 2.5) and shaken before pH measurement. Soil potential CEC and base saturation were determined by 1 M ammonium acetate (NH₄OAc) displacement at pH 7.0 using ICP-OES (iCAP6300 Duo, Thermo Fisher Scientific; Brown, 1943).

Sequential extraction techniques are designed to quantify elements in different soil fractions (Tessier et al., 1979). These are valuable for calculating weathering rates of the silicate minerals (Niron et al., 2024; Vienne et al., 2024) as well as to quantify cations available for plant uptake (i.e., in the soil exchangeable complex). For this, soil samples were collected at the beginning of the experiment (day 9 after basalt amendment) at a depth of 0–20 cm (sampling deeper soil layers was not possible as it would entail destructive sampling). At the end of the experiment (day 113), soil samples were taken at three depth intervals (thus defining three soil layers: 0–20, 20–40, and 40–60 cm) and subsequently air-dried.

Sequential extractions were performed using protocols adapted from Tessier et al. (1979) and Uhlig and Von Blanckenburg (2019). In a four-step process, Al, Ca, Cr, Fe, K, Mg, Na, Ni, Si, and Zn were extracted from four soil pools, i.e., the exchangeable, carbonate, reducible and oxidizable pools. Cations that remained in the soil after the extraction process are considered to be part of the primary or secondary minerals' structure, and thus unlikely to be released under typical soil conditions (Tessier et al., 1979). The concentrations of Al, Ca, Cr, Fe, K, Mg, Na, Ni, Si, and Zn for each extraction step were then quantified in the Helmholtz Laboratory for the Geochemistry of the Earth Surface (HELGES) on three technical replicates by ICP-OES (DSOI Spectrogreen, SPECTRO), using international water reference material SLRS-6 (NRC-CNRC) as quality control. In order to exclude the cations extracted from the initial soil and un-weathered basalt, and investigate the effect of basalt and AMF on the cations in the various soil fractions, soil cation concentrations at the start of the experiment were subtracted from the concentrations measured at the end of the experiment. In the main text only cation concentrations in the exchangeable fraction are reported and widely discussed. These are cations adsorbed onto the soil's exchangeable complex, and are therefore relevant for soil fertility, plant uptake and growth. Results from reducible and oxidizable pools are reported in the supplements (Figs. S4–S5; Tables S3–S4) and are only briefly discussed in the main text, as they provide indication on clay-sized mineral and stable organic C formation respectively.

Weathering rates were calculated based on the major cations (Ca, Mg, Na, K) released from the applied basalt as in Steinwidder et al. (2025). These cations can follow several paths: they either leach out of the soil, are taken up by plants, or remain within the soil system. During the experiment, high temperatures (mean summer temperature = 19.6 °C, compared to the 17.9 °C average between 1991 and 2020; Koninklijk Meteorologisch Instituut Van België, 2022) were registered, and leaching occurred only at the beginning of the experiment and in minimal volumes (mean ± SE = 0.7 ± 0.1 L; Table S5), as most of the water in the mesocosms was lost through evapotranspiration driven by plant uptake and atmospheric evaporative demand. The leaching loss of cations was thus negligible and only the cations accumulating in plant biomass and soil pools were used for the weathering rate calculations.

To determine the amount of each cation released from the applied basalt and taken up by plants (ΔCat_plant), leaf cation concentrations in the C-AMF treatment (Cat_{C−AMF (leaf)}; see Sect. 2.5 for method) were subtracted from cation concentrations in basalt-applied treatments (Cat_{treatment (leaf)}; Eq. 1). Average leaf cation concentration was used to calculate the increase in mol charge equivalents with basalt application compared to C-AMF treatment. 1ΔCatplant=Cattreatmentleaf-CatC-AMF(leaf) In order to determine the amount of each cation released into the soil from the weathering of the applied basalt over the experimental duration (ΔCat_soil), initial (day 9) cation concentrations in each sequentially extracted pool i (Cat_day 9,i) were subtracted from the final cation concentrations extracted at the experiment's conclusion (Cat_day 113,i; day 113; Eq. 2). 2ΔCatreleased_treatment,i=Catday113,i-Catday9,i As the extraction process also extracts primary minerals from un-weathered basalt, this approach accounts for the contribution of the un-weathered basalt to the extracted cations pool by subtracting the initial (mostly un-weathered) soil + basalt mixture from the final concentrations. Because no soil samples were collected immediately after amendment (at day 0), samples obtained at day 9 were used as the initial soil + basalt mixture. As weathering rates are highest immediately after rock application, this approach likely underestimates the true weathering rates. Nevertheless, the day 9 measurements still provide an appropriate baseline for testing our central hypothesis, namely whether AMF enhance basalt weathering rates. Although some weathering occurred before the first sampling event (Fig. S6), AMF-driven weathering is unlikely to have contributed substantially during this period because fungal hyphae require time to establish. This interpretation is supported by the pore water DIC dynamics (Fig. 3), which indicate that AMF activity increased progressively throughout the experiment rather than immediately after inoculation. Consequently, while the use of day 9 samples likely results in conservative estimates of absolute weathering rates, it does not bias our assessment of the relative effect of AMF on weathering.

For the 0–20 cm layer, initial (day 9) cation concentrations were subtracted from the final concentrations. For the deeper layers, where no basalt was incorporated, initial cation concentrations (Cat_day 9,i) were assumed to be equivalent to initial concentrations in the top layer of the control treatment without basalt (C-AMF). Any cation increase observed in the lower layers was therefore attributed to weathering products, as un-weathered basalt was absent in these layers. This calculation assumes that cation migration to the deeper soil layers occurs exclusively as a result of weathering.

Finally, in order to account for potential changes over time in the soil due to plant uptake and/or inclusion of cations within clays, the increases in cation concentration in the basalt treatments for each sequentially extracted soil pool i (ΔCat_soil,i) were expressed relative to the C-AMF treatment (ΔCatreleased_C-AMF,i; Eq. 3). Weathering rates (Wr; expressed as log₁₀ (mol charge equivalents m⁻² s⁻¹)) were then calculated as in Steinwidder et al. (2025; Eq. 4): 3ΔCatsoil,i=ΔCatreleased_treatment,i-ΔCatreleased_C-AMF,i4Wr=log⁡102×ΔCai+ΔMgi+(ΔNai+ΔKi)time×applicationamount×SSA Where ΔCa_i, ΔMg_i, ΔNa_i, and ΔK_i are the concentration changes in each soil fraction (i.e., exchangeable, carbonate, reducible and oxidizable pools) and plant pool i calculated as mentioned above (i.e., ΔCat_soil,i and ΔCat_plant), time is the experimental duration in seconds, application amount is 980 g per mesocosm (equivalent to 50 t ha⁻¹) and SSA is the specific surface area of the applied basalt, with a value of 6.283 m² g⁻¹ (see Sect. 2.1).

Plants were harvested on 12 September 2022. The three top leaves of each plant were sampled for further analysis, whereafter the aboveground biomass was harvested and separated into stems, leaves, tassels and corn. Aboveground biomass was then dried at 70 °C for 48 h and the dry weight of each organ was determined. After harvesting the aboveground biomass, roots were sampled from the topsoil (0–20 cm), middle soil (20–40 cm) and bottom soil (40–60 cm) layers to estimate the root biomass within each mesocosm. For each layer, two 100 cm³ cores were taken directly beneath each plant and one between the two plants. The roots were then washed using a 1 mm mesh sieve, after which they were dried at 70 °C for 48 h and weighed. Root biomass estimates assumed that cores beneath the plants represented root growth in half of the mesocosm, while cores between the plants reflected the other half (as in Ven et al., 2020). Before analysis, the three top leaves (hereafter referred to as leaves), stems, tassels, corn kernels and roots were ground using a centrifugal mill (ZM 200, Retsch GmbH) with a 0.25 mm mesh size sieve.

Plant samples were analysed for nutrients (C, Ca, Fe, K, N, Mg, P) and heavy metals (Al, Cd, Cr, Ni, Pb, V and Zn). Dried, homogenized plant material was subjected to acid digestion with 70 % HNO₃ at 60 °C for 30 min, followed by the addition of 30 % hydrogen peroxide (H₂O₂) and further heating at 120 °C for 90 min. After cooling and filtering, elemental concentrations were measured by ICP-OES (Thermo Scientific, iCAP 6300 Duo). Quantification was based on multi-element calibration standards (CPAChem), with yttrium (Merck) used as an internal standard. A certified reference material (Hay Powder BCR129, CPAChem) was processed alongside the samples using identical digestion procedures. Quality control checks were conducted every 20 measurements to ensure analytical precision and accuracy. Plant Ni, Cr and Mg results are reported in the main text, while concentrations of all other elements are reported in the Supplement (Fig. S7). Biogenic Si was determined by digestion of a 0.03 g plant sample with 25 mL 0.5 M sodium hydroxide (NaOH) and then analysed with a continuous flow analyser (SAN++^® Advanced Series, Skalar) following DeMaster (1981) and Saccone et al. (2007).

To determine plant root colonization by AMF, plant roots were first cleared and then stained using a non-vital staining technique (Vierheilig et al., 2005). Washed roots were cleared by placing them in an Erlenmeyer flask containing a 5 % potassium hydroxide (KOH) solution which was then set in a warm water bath at 90 °C for 8 min. Hereafter, the roots were rinsed and stained with 10 % Sheaffer Black ink in 10 % acetic acid by placing them in a warm water bath at 90 °C for 10 min. To remove excess ink, the roots were immersed in lactoglycerol (1 : 1 : 1 lactic acid : glycerol : deionized water) and stored in an Eppendorf tube with lactoglycerol overnight at 4 °C (Fig. S8). The proportion of roots colonized with mycorrhizal fungi was then quantified by counting arbuscules, vesicles and hyphae using the gridline intersection method (Giovannetti and Mosse, 2006).

During the harvest on 12 September 2022, the mesh bags were removed from the mesocosms and stored frozen until further analysis. Hyphal length of the mycorrhizae was subsequently determined according to Rillig et al. (1999) with adaptations as in Ven et al. (2019).

All statistical analyses were performed in R using packages nlme, lmerTest and dunn.test (Kuznetsova et al., 2017; Pinheiro et al., 2007; R Core Team, 2024; v4.3.1; Dinno, 2024). The level of significance for all analyses was set at p< 0.05. A factorial analysis of variance (ANOVA) was used to investigate the effects of basalt application, AMF inoculation, and their interaction on soil pH, CEC, base saturation, exchangeable cation concentration in each soil layer and weathering rates. If normality or homoscedasticity of the model residuals were not met after log- or square-root transformation, the non-parametric Kruskal-Wallis test was used with treatment (C-AMF, C+AMF, B-AMF and B+AMF) as explanatory variable. A post-hoc test (Tukey's honestly significant difference test or Dunn's multiple comparison test for parametric and non-parametric analyses respectively) was conducted to explore significant differences among treatments.

When cation concentrations in soil were below the detection limit (= bd; Tables S6–S7), the concentrations were set to zero to allow further statistical analyses. In some cases, the presence of the cation was detectable, but the very low concentration did not allow an accurate quantification. For these measurements, half of the limit of quantification was used for statistical analyses.

To quantify treatment effects on variables with repeated measurements over time, i.e., pore water pH, DIC, alkalinity, and nutrient and heavy metal concentrations in the pore water, a linear mixed model was employed. Basalt application, AMF, time (days after basalt application), and their interactions were included as fixed effects, and mesocosm was included as a random effect term. To assess whether the presence of galls from corn smut was affected by basalt, AMF or their interaction, a generalized linear model was used with the binomial family, as appropriate when modelling binary response variables.

The data and model code in support of our findings are openly available in Zenodo at 10.5281/zenodo.16813184 (Boito et al., 2025).

At the end of the experiment, basalt significantly increased soil pH (+0.71 ± 0.14), CEC (+0.43 ± 0.18 meq 100 g⁻¹), and base saturation (+13.6 ± 3.5 %; Fig. 2). The influence of basalt on soil pH, CEC, and base saturation was not affected by AMF. Similarly, pore water pH (+0.41 ± 0.12) and alkalinity (+0.26 ± 0.08 meq L⁻¹) also increased with basalt, again without influence of AMF (Fig. 3). All reported values represent mean basalt effects ± SE. Concerning DIC, our data showed significant two- and three-way interactions between basalt and time and between basalt, AMF, and time respectively. Without AMF, basalt increased pore water DIC concentrations between the start and the end of the experiment by 2.35 mg L⁻¹. This effect became more pronounced in the presence of AMF : DIC concentrations in the B+AMF treatment increased by 9.6 mg L⁻¹ more than in the control over the same period (day 10–102; Fig. 3).

On the other hand, concentrations of plant-available nutrients in the pore water were generally not significantly affected by basalt application nor AMF presence, with the exception of basalt-driven increases in Mg and Na in the middle of the growing season (Fig. S2). Pore water Mg also showed a significant three-way interaction effect of basalt, AMF and time, with AMF reinforcing the positive effect of basalt.

Concerning heavy metals, Cr in the pore water was below the limit of quantification (< 0.02 mg L⁻¹ for pore water concentrations) in all samples and for Ni, 32.3 % of the samples were below the limit of quantification. Nonetheless, basalt increased Ni concentration until around day 75 (Fig. 4). A significant time × basalt interaction was found on Zn concentrations in the pore water, although without a clear trend. Pore water Al decreased with basalt amendment, and AMF presence decreased pore water Al but only in control mesocosms (significant basalt × AMF interaction).

Similarly, basalt weathering rates were not affected by AMF presence (Fig. 7), with rate constants corresponding to -9.97 ± 0.04 and -10.01 ± 0.05 log₁₀ (mol charge equivalents m⁻² s⁻¹) for treatments with and without AMF, respectively (mean ± SE). This corresponds to the weathering of 37.5 % ± 3.7 and 33.2 % ± 4.0 of Ca-, Mg-, Na- and K-bearing minerals in the applied basalt (including both crystalline and amorphous phases), in the presence and absence of AMF respectively, over the 113-day experimental period.

When comparing Mg, Ca, Na and K changes in soil pools with changes in plant pools, it emerged that the greatest contribution to the increase in released cations was in the soil phase, with a total increase in the soil about two orders of magnitude greater than in the plants (Table S8).

Generally, plant growth parameters were not affected by basalt or AMF, including measurements of individual plant organs (Figs. S9–S10). In addition, no effect of basalt on AMF hyphal length and root colonization was found (Fig. 1). Corn smut presence did not differ among treatments, nor did the weight of the galls (Table S2). Elemental concentrations (Ca, Fe, Mg, K, Si, P) in plant parts were typically not affected by basalt or AMF application, with a few exceptions. A notable exception was Mg, whose concentration in plant organs was generally higher with basalt application, save for corn Mg where no basalt effect was found, and tassel Mg in which a post-hoc comparison revealed an increase with basalt only in absence of AMF (B-AMF treatment compared to C-AMF and C+AMF; Fig. 8; Table S9). Despite this, no significant AMF × basalt interaction effect on tassel Mg emerged. On the other hand, in contrast with other elements in other plant organs, a borderline significant (p= 0.08) basalt × AMF interaction effect was found on root Mg concentrations, which only increased with basalt when AMF were present. Moreover, basalt decreased leaf K, whereas AMF decreased leaf P. Finally, stem and tassel Si concentrations increased with basalt application (Fig. S7; Table S9).

Leaf Cr concentrations were all below the limit of quantification (< 0.0002 mg g⁻¹). Therefore, statistical analyses could not be conducted for leaf Cr. Basalt application did not affect Al, Cr and Zn concentrations in the various plant organs (Figs. 8 and S7; Table S9). In contrast, corn Ni concentrations were significantly higher with basalt and AMF, but a post-hoc pairwise comparison revealed that only the C-AMF – B+AMF difference was significant (Fig. 8; Table S9). Finally, AMF increased corn Cr (Fig. 8; Table S9).

In contrast with our hypothesis, AMF did not significantly increase basalt weathering rates. This limited response likely reflects the relatively nutrient-rich conditions of the experiment. The soil used was relatively fertile and only moderately acidic (initial pH = 5.6), and all mesocosms received NPK fertilizer (96–10–39.5 kg ha⁻¹). Although P and K application rates were slightly below Flemish recommendations (Departement Landbouw and Visserij, 2016; Vlaamse Land Maatschappij, 2026), no visible symptoms of nutrient deficiency were observed in the plants. Hence, P availability was likely sufficient, reducing the incentive for AMF-mediated P acquisition. Under such conditions, the potential for AMF to stimulate mineral dissolution through biological weathering could be reduced. These findings suggest that AMF-induced enhancement of silicate weathering may be limited in fertilized soils where plant P demand is largely satisfied.

Because the first soil samples were collected nine days after basalt application, the weathering rates estimated in our experiment likely underestimate absolute weathering rates, as mineral dissolution is generally fastest shortly after amendment. However, this limitation is unlikely to affect the comparison between AMF treatments: AMF colonization develops gradually following inoculation, making a substantial AMF contribution to weathering during the first 9 d unlikely. Thus, while the absence of day-0 measurements introduces uncertainty into the absolute weathering-rate estimates, it should not bias our conclusion that AMF did not measurably enhance basalt weathering.

Nevertheless, the weathering rates estimated through cation mass balance in our experiment (-9.97 ± 0.04 and -10.01 ± 0.05 log₁₀ mol charge equivalents m⁻² s⁻¹ in the presence and absence of AMF, respectively) were more than one order of magnitude higher than weathering rates based on cation tracing previously reported by comparable mesocosm experiments. In a similar experiment, Steinwidder et al. (2025) reported weathering rates of -11.15 ± 0.16 log₁₀ mol charge equivalents m⁻² s⁻¹ (14–15 times slower than in our experiment) using the same methodology, 15 months after application of 50 t ha⁻¹ of the same basalt to the same soil, albeit unpasteurized. Similarly, Vienne et al. (2024) reported a mean weathering rate of -11.65 ± 0.09 log₁₀ mol charge equivalents m⁻² s⁻¹ (44–48 times slower than in our experiment) following application of 100 t ha⁻¹ of basalt over 137 d. The comparatively high weathering rates observed here may be related to the pasteurization process: heating the soil at 80 °C for 4 h likely generated substantial microbial necromass and increased dissolved organic carbon (DOC) concentrations. In particular, low-molecular weight organic acids, which are an important component of DOC, have been shown to sustain far-from-equilibrium conditions that drive rapid elemental loss, and potentially weathering rates as well (Perez-Fodich and Derry, 2019). Indeed, pore water DOC concentrations in pasteurized mesocosms were on average 158 % higher (+22.8 ± 3.5 mg L⁻¹, mean ± SE) than those observed in comparable unpasteurized systems (Fig. S11), consistent with enhanced DOC availability contributing to the higher weathering rates observed here.

Despite these comparatively high dissolution rates, weathering rates estimated from cation mass balance remained approximately three orders of magnitude lower than those predicted from laboratory-derived dissolution kinetics (-7.0 ± 0.08 log₁₀ mol charge equivalents m⁻² s⁻¹ for the amended feedstock; Sect. S1). Such discrepancy is consistent with previous observations that laboratory-derived weathering rates commonly exceed field-derived rates by one to five orders of magnitude (White and Brantley, 2003), while mesocosm experiments typically yield intermediate values (Malmström et al., 2000). Such differences highlight the strong influence of experimental scale on estimated weathering rates. However, variability in weathering rates cannot be attributed to experimental scale alone, as mineral dissolution rates are also strongly affected by feedstock properties and environmental conditions (Palandri and Kharaka, 2004). Even among basalt feedstocks, dissolution rates may vary by up to a factor six due to differences in mineralogy, glass content, particle size distribution, and elemental composition (Lewis et al., 2021). Likewise, environmental conditions such as soil type, temperature and water availability can substantially influence weathering dynamics (Dupla et al., 2025). Consequently, weathering rates reported across studies should be compared with caution, particularly when experiments differ simultaneously in scale, feedstock composition and environmental conditions.

Basalt, but not AMF, increased soil pH, CEC and base saturation (Fig. 2). The observed increases in soil pH, CEC, and base saturation upon basalt application align with our hypothesis of basalt improving soil chemical fertility, although these did not translate into increased maize growth or biomass during the 113 d experiment. The observed increase in base saturation was attributable to an increase in soil exchangeable Ca, Mg and Na due to basalt application (Fig. S13). Indeed, during weathering of basalt, protons are consumed and cations are released. Additionally, weathering of primary minerals promotes the formation of metal (hydr)oxides and secondary silicate phases, ultimately increasing the content of clay-sized particles in the soil and therefore CEC (Righi and Meunier, 1995). Our results corroborate previous work that observed increased soil pH and CEC upon basalt application to tropical soils (Anda et al., 2015; Conceição et al., 2022; Gillman, 1980). An increase in pH was also found in experiments conducted in using relatively younger, less cation-depleted soils upon basalt or dunite application (Rijnders et al., 2023, 2025; Skov et al., 2024; ten Berge et al., 2012).

In line with our soil nutrient data and contrary to our hypotheses, plant nutrient concentrations were generally not affected by basalt application or AMF presence, with the exception of Mg, which generally increased with basalt. Increased plant Mg can be directly linked with the observed increase in pore water Mg concentrations and Mg exchange capacity, leading to elevated Mg uptake. Our results are supported by research carried out on maize after basalt application (Boniao et al., 2006; Rijnders et al., 2025), and on ryegrass (ten Berge et al., 2012) and soybean (Moretti et al., 2019) after dunite application. These consistent findings indicate that EW can help alleviate Mg deficiency, which often occurs in agricultural systems that are fertilized with N, P, and K as uptake competition between these elements and Mg arises (Guo et al., 2016). Nevertheless, our plant data shows only limited evidence for a positive effect of basalt and AMF on crop yield and quality, indicating that the agronomic co-benefits of EW and AMF are modest under the relatively fertile conditions of this experiment (i.e., fertilized soil and only slightly acidic initial soil pH).

Furthermore, Na availability increased in both the soil exchangeable complex and the pore water, while leaf K concentration declined following basalt amendment. Although these changes were not associated with consistent negative effects on plant growth or biomass, they raise questions regarding the long-term EW consequences for plant nutrition, particularly shifts in the K : Na ratio that could ultimately constrain plant performance (Maathuis and Amtmann, 1999). Even though leaf Na concentrations were not measured in this experiment, we recognize Na-K antagonism as a potential concern over longer timescales, especially under repeated basalt applications.

Contrary to our hypothesis, basalt amendment did not affect AMF root colonization and hyphal length. This outcome may be partly explained by the adequate P availability in our experiment. Arbuscular mycorrhizal symbiosis is established by the allocation of photosynthetic C from the plant to the fungus, and an important driver of this symbiosis is low bioavailability of soil P (Leake and Read, 2017). In the present study, P availability was likely enhanced by fertilizer addition, reducing the plant's dependence on AMF-mediated nutrient acquisition. Consequently, plants may have allocated less C to the symbiosis, limiting fungal development and potentially explaining why basalt amendment did not increase AMF colonization or hyphal length.

In addition, the short experimental duration of our trial (113 d) might have constrained the potential for AMF to influence crop yield and quality. Indeed, a meta-analysis by Qin et al. (2022) identified experimental duration as the most important factor limiting the influence of AMF on crop growth, followed by soil texture, with a smaller AMF effect on sandy soils (> 50 % sand). Given both the short experimental duration of the present experiment and texture of the used soil (sandy loam; 69.5 % sand), it is likely that both factors played a role in the observed lack of AMF effect on plant biomass in our study. Although a longer experimental duration might have allowed both basalt- and AMF-mediated responses to develop more fully, extending the study was not feasible because the pasteurized, AMF-free mesocosms would eventually have been recolonized by AMF spores, thereby compromising the integrity of the AMF-free treatment.

Finally, soil pasteurization likely removed a substantial fraction of the indigenous microbial community, potentially limiting the extent to which basalt-induced improvements in soil chemistry could translate into plant responses. Many beneficial effects of increased soil pH on plant growth and nutrition are mediated by soil microorganisms through processes such as organic matter decomposition and consequent nutrient mineralization, solubilization, and uptake (Richardson et al., 2009; Van der Heijden et al., 2008). Moreover, soil pH is a major determinant of microbial community composition and activity (Fierer and Jackson, 2006; Lauber et al., 2009), meaning that microbial responses to pH change represent an important pathway through which basalt can influence nutrient cycling and crop performance. By substantially reducing microbial abundance and diversity, pasteurization may therefore have disrupted these microbial pathways, weakening the link between basalt-induced increases in pH and improvements in nutrient availability. Consequently, the reduced microbial community may have contributed to the limited crop responses observed, despite clear changes in soil chemical properties.

The observed lack of a plant biomass response is similar to results by Vienne et al. (2022), where the application of 50 t ha⁻¹ of basalt did not significantly affect potato growth. In other experiments, on the other hand, basalt application increased biomass of spring oat (Skov et al., 2024), sorghum (Kelland et al., 2020), and maize (Rijnders et al., 2025). Additional counter evidence is provided by the review of Swoboda et al. (2022), which focused primarily on silicate rock powder applications in highly weathered, nutrient-poor soils, and which reported a positive silicate effect on crop biomass for almost all studies using mafic and ultramafic rocks as feedstock. Taken together with previous studies, our results indicate that positive crop responses to basalt are not universal and may be small or absent in relatively fertile soils such as the one studied here. The contrasting responses reported across soils and regions emphasize the context dependence of EW outcomes. In our experiment, plant N : P ratios (around 7.7; Fig. S7) suggest that crop growth remained primarily constrained by N rather than P availability. Because basalt amendments supply base cations and, to a lesser extent, P, but do not contribute to biologically available N, their potential to alleviate the dominant nutrient limitation in our system was inherently limited. In contrast, EW may deliver greater agronomic benefits in highly weathered tropical soils, where soil acidity, low base saturation, and depletion of rock-derived nutrients are more common and where basalt-derived nutrient inputs can more directly alleviate nutrient constraints (Haque et al., 2025; Swoboda et al., 2022).

Our findings highlight the need for careful monitoring of soil and plant heavy metal concentrations following basalt amendment. Given the observed increases in pore water Zn and Ni, our results do not support the hypothesis that basalt application does not elevate the availability of heavy metals in the soil. This is noteworthy, as Ni release is among the primary environmental safety concerns associated with EW in agricultural contexts (Suhrhoff, 2022; te Pas et al., 2023). During the 113 d experimental period, average pore water Ni concentrations exceeded the freshwater Environmental Quality Standards (EQS) of both the European Union (EU; 4 µg L⁻¹) and Australia (0.3–10 µg L⁻¹, depending on water pH and hardness) in both the control and basalt treatments (7.1 ± 1.7 and 19.7 ± 4.9 µg L⁻¹, respectively; mean ± SE; ANZG, 2024; European Commission, 2006). This may be partly due to background soil Ni levels. Nevertheless, the observed concentrations remained below the regulatory limits set by other jurisdictions, such as the United States (52 and 470 µg L⁻¹ for chronic and acute exposure, respectively) and Canada (3–150 µg L⁻¹, depending on water hardness; British Columbia Ministry of Water Land and Resources Stewardship, 2024; Canadian Council of Ministers of the Environment, 1987; EPA, 1995).

Plant heavy metal concentrations were generally unaffected by basalt amendment, with the notable exception of an increase in Ni in corn tissue (0.42 ± 0.0001 and 0.65 ± 0.0004 mg kg⁻¹ for control – AMF and basalt + AMF respectively, mean ± SE), therefore only partially supporting the hypothesis that basalt amendment does not increase plant heavy metal concentrations. Despite the increase, corn Ni concentrations remained below the EU regulatory threshold of 0.8 mg kg⁻¹ which will come into effect in 2026 (European Commission, 2024). Our results therefore partially contrast with previous research, where Ni concentrations did not increase upon basalt application (Kelland et al., 2020; Rijnders et al., 2025; Vienne et al., 2022).

Heavy metal concentrations in the pore water and soil exchangeable complex were mostly not affected by AMF. On the other hand, AMF increased Cr concentration in the corn tissue. Therefore, our hypothesis that AMF presence would modulate heavy metal availability is only partially supported by our data. It is important to note that Cr concentrations in corn tissue were, regardless of treatment, higher than the average Cr concentrations found in common vegetables as identified by WHO (World Health Organization, 1988), which is in the range of 0.005–0.03 mg Cr kg⁻¹ fresh weight (Fig. S14). This finding suggests that AMF inoculation does not universally confer benefits and may, under certain conditions, such as in co-deployment with silicate amendment in soils with elevated background Cr contents, pose risks to food safety.