On 12 March 2023, twelve in situ mesocosms were deployed in the south harbour of Helgoland (54° 10`36.9`` N, 7° 53`36.0`` E; North Sea, Germany, see Alfred-Wegener-Institut Helmholtz-Zentrum für Polar- und Meeresforschung, 2023) to investigate the effect of OAE on biogeochemical responses of a temperate eutrophic community from the North Sea. Each mesocosm consisted of a transparent cylindrical polyurethane bag (Ø = 2 m), which ended in a 1.6 m conical sediment trap, with an overall length of 3.5 m. It was suspended in a polyethylene floating frame, allowing for the observation of pelagic communities under natural temperature and light conditions. The mesocosms were filled with seawater originating from the Helgoland Roads observatory site (Wiltshire et al., 2010; water depth at site ∼ 6–8 m). Using a peristaltic pump, water from 2–3 m depth (minimizing benthic influence) was screened (< 3 mm) and transferred into an intermediate reservoir. From there, all mesocosms were filled simultaneously with ∼ 5.9 m³. Pumping speed averaged ∼ 14 m³ h⁻¹ to minimize biological stress, resulting in a ∼ 12 h filling-process (for technical details see Bach et al., 2019b). Filling took place on 13 March, marking day zero of the experiment. The days preceding the OAE manipulation (day 4) were used for baseline characterization of various water column parameters, while sediment-trap samples from these initial days were discarded due to filling-related particle disturbance. Additionally, CTD profiles (CTD60M, Sea & Sun Technology GmbH, Germany) measured temperature, salinity, pH, chlorophyll a, dissolved oxygen, and photosynthetically active radiation before OAE manipulation to ensure homogeneity across mesocosms and alignment with conditions at the Helgoland Roads site (Wiltshire et al., 2010). We note that enclosure and the four-day pre-manipulation confinement period may have influenced community development relative to ambient field conditions. However, because all mesocosms experienced the same filling and confinement history prior to OAE manipulation, such effects are unlikely to confound the post-manipulation treatment comparisons presented here. The OAE manipulation was simulated using a CO₂-unequilibrated approach, meaning that dissolved inorganic carbon (DIC) was not raised alongside TA, deliberately resulting in strong (yet transient) perturbations of seawater carbonate chemistry (e.g. pH_T, ΩCa/Ar) until re-equilibration with the atmosphere (Bach et al., 2019a; Renforth and Henderson, 2017). Accordingly, this strategy was chosen since it reflects a more realistic pathway for large-scale and economically feasible OAE implementation than CO₂ pre-equilibration of solutions prior to alkalinity release (He and Tyka, 2023). While the study-design encompassed varying dilution scenarios, to differentiate impacts of point-based versus more uniform alkalinity perturbations (Eisaman et al., 2023), here we will prioritize analysis of response signals over the common alkalinity/pH gradient. Informing about environmental safety of varying application modes remains relevant, but equally important is the assessment of the net CO₂ sequestration outcome of OAE when factoring in potential changes to the biological carbon pump. This focus reflects both the broader relevance of alkalinity-driven bloom and export responses for evaluating net CO₂ sequestration outcomes, and the inherent limitations of sediment-trap-based export metrics for resolving dilution-specific signals as integrated sinking material cannot be attributed to a specific depth layer of origin. For coherence with other publications coming from this experiment, the full treatment design is described below and the corresponding colour coding is retained in all figures.

The carbonate chemistry manipulation was realized 4 d after filling and aimed to simulate calcium-based OAE using NaOH and stoichiometrically proportionated CaCl₂ solutions to mimic cation release during mineral dissolution. Therefore, the mesocosms were strategically assigned to two sets of six: one set received alkalinity throughout the enclosed water column (immediate dilution), representing an idealized rapid-dilution of alkalized waters and conceptually related to well-mixed upper-mixed-layer application modes, such as ship-wake release (Caserini et al., 2021), while the other set was initially alkalized only in the top layer (delayed dilution) and mixed after 2 d. For this, 17 L of CaCl₂ solution (in pre-filtered freshwater) were applied evenly across the perimeter of the mesocosm using a custom-built device (see Riebesell et al., 2013 for technical details), either over the entire depth (immediate) or only within the top 80 cm (delayed). To ensure full treatment delivery, an additional 17 L of freshwater was flushed into each mesocosm, applied either across the full depth or surface-only, further solidifying stratification in the delayed treatment through density differences (ΔPSU ≈ 0.5). Concentrations of CaCl₂ solutions corresponded to half of the respective target alkalinity additions. This calculation assumes Ca(OH)2-based OAE, where dissolution of one mole of Ca(OH)2 releases one mole of Ca²⁺ and two equivalents of alkalinity. To raise alkalinity, NaOH solutions (in pre-filtered freshwater) were then added using the same device, either throughout the full water column (immediate) or confined to the surface (delayed). In the delayed treatments, upper-layer alkalinity concentrations were intended to be doubled relative to the immediate treatments so that, the intended target alkalinity levels were reached only after mixing of the water column two days later. Alkalinity concentrations (post-mixing) were applied in increments of 250 µmol TA kg⁻¹, reaching ΔTA = 1250 µmol kg⁻¹ relative to a background alkalinity of 2330 µmol kg⁻¹. To achieve mixing of the delayed dilution treatments and avoid procedural bias across treatments, all mesocosms were homogenized by bubbling pressurized air through the sediment trap, 48 h after manipulation. The order of CaCl₂ application was randomized, while NaOH application proceeded from lowest to highest treatment to avoid carryover effects, alternating between equivalent levels of delayed and immediate dilution scenarios. Control mesocosms were treated similarly throughout the manipulation, but with freshwater only. Mooring positions along the pier were randomized in order to not have an alkalinity gradient along a natural one such as light availability. A schematic overview of the treatment setup and manipulation timeline is provided in Fig. S1 in the Supplement. For details on changes in carbonate chemistry parameters see Fig. S2.

We note that CO₂ equilibration during our experiment was minimal (Fig. S2) yet realistic, considering that CO₂ re-equilibration with the atmosphere after alkalinity enhancement will typically take months to years under natural oceanographic conditions as well (He and Tyka, 2023; Jones et al., 2014) and was similar to other OAE mesocosm studies (Schneider et al., 2026). Accordingly, TA targets were intentionally high to maximize detectability of biological responses across a wide pH range and the use of NaOH allowed for complete and rapid mixing, enabling controlled and precise TA additions (Iglesias-Rodríguez et al., 2023).

Sampling was initiated on day one using a polypropylene tube integrating the upper 2 m of the water column with a volume of 4.5 L. Upon treatment additions, but prior to mixing (days five and six), samples in the delayed dilution mesocosms were collected separately from the top and bottom layers using 5 L Niskin bottles (Hydro-Bios, Kiel, Germany). Bulk water samples for the immediate dilution treatments continued to be taken with a polypropylene tube sampler. Post-mixing, all mesocosms were sampled every 2 d between 09:00 and 12:00 am (UTC+1) using the same integrating polypropylene tube sampler. A CTD60M (Sea & Sun Technology GmbH, Germany) was cast in the beginning of every sampling for abiotic parameters such as temperature, salinity, pH, Chl a, dissolved oxygen (O₂) and photosynthetically active radiation. Then, per sampling occasion, 15–30 L of water were sampled (4–7 tubes), distributed into several containers dedicated to different analyses, and generally kept dark and at in situ temperature until returned to the laboratory. Particulate material collected in the sediment traps (PM_Sed) was retrieved through a pre-fixed silicone hose with a manual vacuum pump, maintaining pressures below 0.3 bar. The material was transferred into 5 L glass bottles (Schott Scandinavia A/S, Kgs, Denmark) and stored in the dark until processed in the laboratory (see Boxhammer et al., 2016 for technical details). Whenever subsamples were required, the sediment was gently re-suspended by rotating the bottles, ensuring a homogeneous mixture before withdrawal for further analyses. To limit shading and nutrient consumption caused by organism growth, the inner walls of the mesocosms were cleaned with brushes every 6 d. To further counteract shading, divers cleaned the outer walls with brushes on three occasions during the experiment.

To align comparisons of mesocosms on a common biological clock (i.e., trophic state), we identified phytoplankton bloom start and duration separately for each mesocosm using Chl a dynamics. Although treatment-induced shifts in bloom timing are relevant to OAE environmental safety, a calendar-day fixed analysis would inadvertently mix bloom and non-bloom days across mesocosms and blur differences in OAE-mediated biomass build-up and stoichiometry. From sampled Chl a concentrations, short-term variability was reduced using a centered 3-sampling-day moving average (note: for the delayed treatment, top and bottom layers were averaged on days 5–6). A mesocosm-specific baseline (B) was defined as the median of smoothed Chl a values during days 1–6. Bloom detection started on day 7, after full treatment manipulation was achieved. Bloom start was defined as the first of two consecutive sampling days in which (i) smoothed Chl a exceeded a baseline-relative threshold on both days: Chl a ≥ (1+α)⋅B (with α= 0.35 and B = baseline), and (ii) day-to-day slopes of the smoothed Chl a series were positive on both days. Bloom end was determined only after the main Chl a peak and was defined as the first of two consecutive sampling days in which (i) smoothed Chl a fell back to Chl a≤ (1+β)⋅B on both days (with β= 0.70, and again B = baseline), and (ii) at least one day had a negative slope. Separate start and end thresholds were used to provide hysteresis (with α<β). Among various tested combinations of α- and β-values the selected pair preserved sensible fit to the observed bloom-patterns of smoothed and raw Chl a within all treatments. To further evaluate how well the selected thresholds captured bloom development across mesocosms, we compared the threshold-defined bloom window with a reference bloom window around each mesocosm's Chl a peak, which was bounded by the minima before and after the peak. For both windows, we calculated the area under the Chl a curve (termed AUC) and expressed the ratio of these areas (AUC_{α ∕ β} / AUC_reference) as AUC_m %. This metric was used to assess how completely the threshold-based method captured each mesocosms bloom. A detailed visualization of the analysis per mesocosm can be found in Fig. S4, providing raw and smoothed Chl a values, baselines and thresholds, defined start and end days per mesocosm, as well as AUC_m % diagnostics. All analyses were conducted in R (R Core Team, 2021) using the “zoo” package (Zeileis and Grothendieck, 2005) for centred 3 d smoothing and windowed run tests (rollapply), and ggplot2 (Wickham, 2016) for visualization.

Sediment deposition events may not only occur at different points in time relative to the bloom start but could also exhibit different durations. Analysing sediment deposition on fixed calendar days would therefore distort estimates of export magnitude and stoichiometry. Similarly to water column blooms, we identified sediment deposition events per mesocosm to align comparisons on a common biological clock and accommodate variation in the coupling of production and export. Daily POC fluxes were used to quantify sediment deposition events. Cumulative export was calculated by summing daily fluxes to the end of the experiment, and short-term variability was reduced using a centred 3-sampling-day moving average. From there, we calculated the day-to-day slopes (m) of the smoothed cumulative curve, which served as a deposition intensity proxy. Event detection was restricted to a mesocosm-specific search window beginning at the day of water column bloom onset and ending at the day of bloom termination +w (an extension to the search window). To remove continuous background deposition before bloom-driven export, a baseline slope (mB) was defined as the median slope from days ≥ 5 and < bloom onset, and relative deposition intensity was defined as mrel=m-mB. For each mesocosm, event detection was centred around the day of maximum relative intensity (mmax), representing peak deposition. Deposition event start was defined as the first day within the search window where mrel≥ α⋅mmax and the end of events as the day on which mrel ≤ (1 -α) ⋅mmax (note, end detection was only allowed after mmax and water column bloom end). After testing several α and extended search windows (w) combinations, we chose α= 0.32 and w= 6 d. The combination yielded start and end days consistent with the observed phenology of cumulative POC flux and slope time series. To further evaluate the chosen α- and w-combination capturing the deposition events, we compared two metrics: (a) the cumulative flux captured by the detected event window relative to total cumulative flux over the experiment, and (b) flux density, defined as the captured cumulative flux divided by the event duration in days. Here, we note that mesocosms with secondary blooms and associated secondary deposition pulses had a lower proportion of total cumulative flux captured within the detected event, reflecting export distributed across multiple pulses rather than a failure of event detection; this did not affect our OAE analysis, as treatment comparisons were based on averages of the first bloom and associated deposition event. Detailed per-mesocosm visualization of the analysis can be found in Fig. S5, providing raw and smoothed cumulative POC flux values, slopes, detected start, end and peak deposition days, as well as proportion of total flux captured and flux density. Analyses were conducted in R (R Core Team, 2021) using the “zoo” package (Zeileis and Grothendieck, 2005) for centred 3 d smoothing and windowed run tests (rollapply), and ggplot2 (Wickham, 2016) for visualization.

To assess OAE effects on biogeochemical water-column and sediment parameters, daily responses (i.e., sampling days) were either averaged or summed up (for cumulative fluxes), yielding a single independent estimate per mesocosm for each analysis window (bloom phase, deposition event, or last experimental day as cumulative endpoint). Linear models were then fitted (across dilution scenarios) using measured in situ mean pH_T as the primary explanatory variable. Where relevant, we also ran parameter regressions, including cross-phase fitting, linking bloom and sediment deposition averages. This allowed us to estimate effect sizes of within phase relationships and disentangle drivers of production–export coupling. Model assumptions were checked prior to analysis, i.e., linearity (residual–fitted plots and Reset test), homoscedasticity (scale-location plots and Breusch–Pagan test) and normality of residuals (qq-plots and Shapiro–Wilk test) with base R and the lmtest package (R Core Team, 2021; Zeileis and Hothorn, 2002). Whenever model assumptions were violated, either data transformations were applied, or outliers were flagged visually in figures and noted in statistical tables (Table S1). All plots, including diagnostics, were produced using ggplot2 (Wickham, 2016).

Deployment of unequilibrated OAE across varying dilution scenarios was successful, achieving target alkalinity post-mixing (Figs. 1b, S3). Carbonate saturation states (ΩCa/Ar) remained high after mixing and carbonate precipitation was triggered in the two highest alkalinity mesocosms from mid-experiment onwards, decreasing TA and pH_T (Fig. S2) and yielding high, threshold-like PIC fluxes in respective mesocosms. However, this did not confound results, as analyses were based on measured pH_T (not target levels) and carbonate formation neither directly altered organic export magnitude, nor indirectly via increased particle sinking velocities (Fig. S6, Table S1). Additionally, blooms of comparable magnitude occurred regardless (Fig. 2a, c). This is consistent with prior observations, and we refer to Suessle et al. (2025) for a detailed discussion of OAE-driven carbonate precipitation and its effect on biological carbon sequestration. While CO₂ increased from carbonate precipitation and atmospheric ingassing, the rise in fCO₂ over the experiment was relatively small in the two highest mesocosms (Fig. S2b, d). CO₂ levels closely tracked initial treatment spacing at ΔTA ≥ 750 µmol kg⁻¹, generally remaining below 50 µatm (down to fCO₂ < 15 µatm and pH_T > 9.25). Bloom-driven CO₂ drawdown was small and only evident under ambient or moderate alkalinity increases (Fig. S2). Initial nutrient conditions reflected typical North-Sea spring conditions (Wiltshire et al., 2010) and were sufficient to support ample biomass growth (Si ≈ 14.5 µmol L⁻¹, NO3-≈ 17.7 µmol L⁻¹, PO43-≈ 0.05 µmol L⁻¹, Fig. S7). Increased alkalinity treatments initially showed slowed nutrient drawdown but did not alter overall consumption consistently (Fig. S7, Table S1) which closely followed bloom development throughout the experiment. Because sediment traps integrated particle signals from both initially alkalized and initially unalkalized layers, and because main export responses were directionally consistent across dilution scenarios (Fig. 3e), the common pH_T gradient was retained as the primary focus of the export analysis (see Sect. 2.1). Mesocosms with similar alkalinity levels were therefore treated as duplicates, while original treatment colors were retained for transparency. Further, we focus here on water column driven export dynamics, while general carbonate-chemistry feedback and bloom-timing effects, relevant to OAEs environmental safety, are addressed elsewhere (Tammen et al., 2026).

Across mesocosms, the calculated bloom onset and termination based on Chl a dynamics captured 95 ± 2.7 % (mean ± SD) of the total biomass standing stocks (Fig. S4). Start and end days varied between day 7 and 15, and day 15 and 35, respectively, with earlier bloom onset and termination in the low- to intermediate-alkalinity treatments and the latest onset and termination in the highest-alkalinity treatments (details in Fig. S4). Within blooms, averaged phytoplankton biomass metrics (Chl a and POC_WC) were not affected by the OAE induced pH_T-gradient and displayed similar concentrations (Fig. 2b, c, Table S1). Averaged Chl a concentrations varied between 5.7 and 3.5 µg L⁻¹ and POC_WC concentrations between 42.7 and 27.8 µmol L⁻¹ (Fig. 2b, c). Fucoxanthin, a diatom-associated accessory pigment used as a proxy for diatom biomass (see Sect. 2.3.2), tracked temporal Chl a dynamics (Fig. 2a, d), indicating diatom-driven bloom development, and was likewise not affected by pH_T (Fig. S8, Table S1). In contrast, water column biogenic silica concentrations (BSi_WC) within blooms declined with increasing pH_T, by 40 % from 5.5 to 3.3 µmol L⁻¹ and water column silica ballasting ratios (BSi_WC : POC_WC) halved from 0.16 to 0.08 mol : mol (Fig 2e, f, Table S1). Over time, POC_WC concentrations generally remained elevated after build-up, albeit some variability, but BSi_WC concentrations showed a consistent rise followed by a pronounced decline across all mesocosms (Fig. S8). Consequently, water-column silica ballasting ratios (BSi_WC : POC_WC) decreased over the course of the experiment.

Sediment deposition following bloom events in each mesocosm ranged between 37 % and 81 % of total export, varying with distinct deposition dynamics (e.g., secondary pulses following secondary blooms, Fig. S5). The onset of deposition lagged blooms by 3.5 ± 3.0 d (mean ± SD, details in Fig. S5), indicating tight but varying coupling of production and export of biomass, and showed no systematic delay under OAE. Within the defined deposition events, averaged POC and BSi flux magnitudes showed no detectable pH effect (Fig. 3b, d, Table S1), ranging from 6.2 to 2.2 µmol L⁻¹ d⁻¹ and from 1.2 to 0.6 µmol L⁻¹ d⁻¹, respectively. In general, sediment-trap BSi fluxes were positively correlated with water column BSi production (Fig. S9, Table S1). Likewise, POC and BSi fluxes correlated positively (Fig. S9, Table S1) and followed temporal patterns similar to water column Chl a dynamics, but with the previously noted delay and more episodic, less uniform peaks (compare Figs. 2a; 3a, c). In contrast, sediment silica ballasting ratios (BSi_Sed : POC_Sed) declined sharply with increasing pH_T: deposition-averaged values fell by 60 % from 0.27 to 0.10 mol : mol, while daily ratios decreased over time (Fig. 3e, f, Table S1). Other deposition-averaged fluxes (TPN, TPP) and experiment-integrated cumulative fluxes of all major elements were unaltered by OAE (Figs. S10, S11, Table S1). This confined the sediment signal to (a) a compositional change rather than changes in bulk flux, and (b) post-bloom deposition pulses, rather than continuous export.

Notably, silica ballasting ratios (BSi : POC) increased from the water column to the sediment trap, rising approximately twofold at ambient alkalinity with diminishing enrichment as alkalinity increased (Fig. 4a, comparing Fig. 2f and 3f). Accordingly, sediment and water column silica ballasting ratios correlated, but exceeded a 1 : 1 scaling: each mol : mol decrease in BSi_WC : POC_WC corresponded to a 1.73 mol : mol decrease in BSi_Sed : POC_Sed (slope = 1.73, Table S1). Additionally, particle porosity in the 100–250 µm size class increased consistently with alkalinity-driven pH_T (Fig. S10, Table S1), and negatively correlated with sediment silica ballasting ratios (Fig. 4b, Table S1). These porosity changes, however did not translate into systematic changes in particle sinking velocities (Fig. S9; Table S1), which in general were unaffected by pH_T, aside from higher velocities under the highest alkalinity treatments (Fig. S10; Table S1). Consistent with this decoupling, sinking velocities also did not scale with either water column or sediment silica ballasting ratios (Fig. S9; Table S1). Finally, we found no evidence for enhanced POC remineralization as Chl a-normalized community respiration and bacterial abundances were unaffected by pH_T and did not scale with particle porosity (Fig. S12, Table S1).

Within bloom phases, average BSi concentrations and water column silica ballasting ratios (BSi_WC : POC_WC) declined across the alkalinity-induced pH_T gradient, despite unchanged bloom magnitudes (Chl a, POC_WC) across treatments. Notably, the decoupling of silica from bulk biomass was even more pronounced in sinking compared to suspended material. Together, these observations suggest enhanced BSi dissolution at higher pH_T. Because seawater is generally under-saturated with respect to silica (Lewin, 1961), dissolution rates can be substantial, reaching up to 43 % of gross production rates during blooms (Beucher et al., 2004). Moreover, dissolution rates are known to increase at higher pH (Brady and Walther, 1989; Socratis et al., 2008; Van Cappellen et al., 2002), due to facilitated hydrolysis of siloxane bonds at the frustule surface (Barker et al., 1994). In line, BSi_Sed : POC_Sed exhibited a steeper decline across the applied pH_T gradient (Fig. 4a, see slopes in Table S1), suggesting that silica loss intensified during particle transit. Living diatoms protect their frustules with organic coatings (Lewin, 1961; Van Cappellen et al., 2002), but upon senescence (i.e., bloom termination and export), bacterial degradation of these coatings strongly accelerates pH-enhanced BSi dissolution (Bidle and Azam, 1999). Given the higher dissolution rates in older material, our results are consistent with chemically controlled BSi loss, as silica frustules lose their coatings and become increasingly susceptible to pH-driven hydrolysis during transit. This mechanism could explain the observed decline in water column silica ballasting ratios (BSi_WC : POC_WC) by up to 50 % per unit increase in pH, a number consistent with chemical studies reporting a 60 %–70 % per-unit-pH sensitivity of dissolution rates (Dove and Elston, 1992; Greenwood et al., 2005). Additionally, the global-scale pH sensitivity of BSi dissolution was estimated by Taucher et al. (2022), who reported a 17 % increase in export Si : N under an approximate pH decline of 0.3 units (under end-of-century RCP 8.5 scenarios). Scaled to a full pH unit, this corresponds to an estimated 56 % decrease in dissolution and, despite the opposite sign of the perturbation, falls within our estimate of up to 60 % increase in dissolution per unit pH increase (measured from BSi_Sed : POC_Sed). The convergence of these independent estimates, derived from contrasting pH perturbations across different ecosystems and experimental approaches, further supports a view of chemically controlled, pH-sensitive BSi dissolution as a general and broadly applicable mechanism.

Although our experiment was conducted in a coastal system, the mechanism proposed here may extend beyond such regions if the observed BSi loss is primarily governed by pH-enhanced dissolution. This is particularly relevant given recent global OAE-efficiency estimates: Zhou et al. (2025) showed that OAE efficiency varies strongly with latitude and season, identifying high latitudes around ∼ 50° N and ∼ 50° S, including parts of the North Pacific and Southern Ocean, as favourable deployment locations due to enhanced surface retention of added alkalinity and efficient air–sea CO₂ equilibration. Yet, these regions are also among the most relevant globally for seasonal diatom-driven carbon export (Le Moigne et al., 2012, Ragueneau et al., 2006). Taucher et al. (2022) further identified these regions as highly sensitive to pH-driven silica preservation under ocean acidification, suggesting they may also be particularly susceptible to silica dissolution under OAE. Importantly, Zhou et al. (2025) estimated OAE efficiency primarily from physical–chemical controls while assuming negligible biogeochemical feedbacks from carbonate-chemistry changes. Such maps therefore provide an essential baseline, but not necessarily a complete estimate of retained net CO₂ sequestration under OAE. Our findings suggest this distinction matters in highly productive, diatom-dominated systems, where OAE-driven BSi dissolution could weaken silica ballasting and potentially alter biological-pump efficiency. However, whether this translates into a net reduction in CO₂ sequestration will depend on how dissolution-derived DSi is redistributed within the water column and on its role in regulating diatom growth.

Despite the relevance of this mechanism, recent OAE work has documented changes in DSi drawdown and BSi dynamics (Ferderer et al., 2022; Gately et al., 2023; Paul et al., 2025), but direct evidence for impacts on BSi dissolution under OAE still remains limited, particularly along the sinking pathway. A key distinction of our experiment was the strong carbonate-chemistry perturbation (pH_T > 9.25) extending beyond the range typically tested to date (pHT= 8.2–9.0; Ferderer et al., 2024, 2025; Gately et al., 2023; Guo et al., 2024, 2025; Li et al., 2024; Suessle et al., 2025), across a highly resolved gradient (duplicated, six alkalinity levels). Smaller perturbations would inherently reduce pH-sensitive dissolution and, with fewer treatment levels and/or replication, make subtle responses harder to distinguish from background variability. Detectability is further constrained by smaller or inconsistent blooms, reported in many studies (1–5 µg Chl a L⁻¹; Ferderer et al., 2024; Guo et al., 2024; Kousoulas et al., 2025; Suessle et al., 2025), whereas our experiment consistently reached above 7.5 µg Chl a L⁻¹. Higher biomass likely increased signal-to-noise ratios by leveraging dissolution changes and in combination with the long experimental duration, allowing for a full bloom progression in all treatments (onset to export). Critically, our clearest fingerprint emerged when separating suspended from sinking material, with the pH signal intensifying during transit (Fig. 4a), shown by > 1 slope when scaling BSi_WC : POC_WC with BSi_Sed : POC_Sed (Table S1). Although vertical transport may be less pronounced in dynamic coastal systems, the signal observed over only 3 m transit may represent a conservative estimate of dissolution along longer sinking pathways. Studies focusing only on suspended pools or production metrics (Ferderer et al., 2025; Gately et al., 2023; Subhas et al., 2022), would miss the export-phase intensification, leaving the signal too weak to detect in the suspended fraction. Notably, reduced water column BSi at otherwise similar biomass build-up, has been reported for a diatom-dominated OAE experiment (pH ≈ 8.6; Ferderer et al., 2022), though the authors could not resolve the responsible mechanism. Moreover, their signal did not propagate into sediment-trap material, potentially because of the lower export magnitudes as well as sampling frequency compared to our study, likely limiting the detectability due to noise. Similarly, a related analysis of the present experiment did not detect a clear fCO₂ effect on bloom-phase water-column BSi concentrations. This is not necessarily inconsistent with our results, as that analysis used a broader suite of water-column parameters to define bloom phases, resulting in different bloom-phase windows, and retained the initial dilution-scenario grouping. In addition, fCO₂ and pH emphasize different aspects of the OAE perturbation, reflecting e.g., carbon-availability constraints for phytoplankton or pH-dependent chemical processes such as silica dissolution, respectively. These differences further emphasize that the detectability of silica-related OAE responses can depend on both temporal and analytical framing. Finally, although the OAE studies discussed here span diverse ecosystems, ocean-acidification work has shown that the pH sensitivity of silica dissolution is global (Taucher et al., 2022). It further supports the directionality implied here and suggests that null results under OAE may instead reflect limited pH-range forcing and/or resolution, both statistical and methodological, rather than the absence of a dissolution response.

Although the decline in water column and sediment BSi : POC ratios suggests enhanced pH-driven silica dissolution, we note that a corresponding increase or hampered drawdown of dissolved silicate (DSi) was not detectable from water column concentrations. The signal was likely obscured by rapid re-assimilation during bloom phases, with treatment-specific differences in bloom dynamics (exponential vs. gradual development) further masking its detectability. Additionally, DSi enrichment within pore-water of sinking aggregates, likely a substantial fraction of dissolution-derived silica, did not contribute to water column measurements and was also not quantified from sediment trap samples, hindering silicon mass-balance approaches. Together, these constraints limited our ability to resolve dissolution signals from water column DSi alone, although we acknowledge that enhanced silica regeneration certainly occurred and is mechanistically implied by the observed BSi losses.

Although our results strongly suggest pH-driven chemical control of silica dissolution, we evaluated whether other production-side (silicification, community composition) or export-side (remineralization, sinking time) processes could alternatively explain the BSi : POC response under OAE. Physiologically, higher pH could in principle impede silicification by maintaining higher Si solubility and steepening the pH gradient that diatoms must overcome within their silicification compartments (Martin-Jézéquel et al., 2000; Vrieling et al., 1999). However, direct experimental evidence under OAE is still scarce (Ferderer et al., 2024, 2025; Gately et al., 2023; Oberlander et al., 2025), and responses under acidification are inconsistent, with silicification reported to both increase and decrease (Hervé et al., 2012; Petrou et al., 2019). While we did not directly quantify per-cell silicification, it is generally thought to increase at lower growth rates (Martin-Jézéquel et al., 2000; Timmermans et al., 2004). In our experiment, however, Chl a dynamics suggest that diatom growth decreased at higher alkalinity (early exponential vs. delayed gradual bloom development) consistent with our alkalinity perturbations reducing CO₂ to long-known growth-limiting levels (∼ 1 µmol kg⁻¹, fCO₂ < 15 µatm; Raven, 1993; Riebesell et al., 1993). In summary, these production-side considerations argue against a simple, uniform decline in species-level silicification to explain the observed decline in water column silica ballasting.

Further, community shifts could reduce water column silica ballasting ratios if OAE favored e.g., fewer diatoms relative to non-silicifying taxa, or more lightly silicified diatom species. Yet, evidence that OAE consistently drives community changes of sufficient magnitude to generate the strong BSi_WC : POC_WC signals observed remains limited (Groppelli et al., 2026; Guo et al., 2024; Li et al., 2024; Subhas et al., 2022; Xin et al., 2024). While we did not resolve taxonomic composition or diatom size spectra, ocean-acidification studies have shown, that elevated fCO₂ can favor larger diatoms, a pattern attributed to alleviated diffusive CO₂ limitation and downregulation of energetically costly CCMs with increasing cell size (Bach and Taucher, 2019; Rost et al., 2008; Sommer et al., 2015; Wu et al., 2014). By extension, CO₂ limitation under unequilibrated OAE could bias competitiveness towards smaller taxa, consistent with Kousoulas et al. (2025), identifying specific larger diatom species as losers under unequilibrated OAE (low fCO₂). In a system typically dominated by large diatoms (Wiltshire et al., 2010) and subjected to CO₂ limitation exceeding its natural variability (Kirchner et al., 2020), such a competitive shift could be clearly expressed as a restructuring toward smaller diatoms. Yet smaller diatoms are generally thought to be more heavily silicified (per cell; Ragueneau et al., 2006; Sarthou et al., 2005), which at similar bloom magnitudes (see Chl a, POC_WC) would predict higher BSi per carbon biomass; this directionality directly opposes our observations, reinforcing pH-driven BSi dissolution as the dominant explanation. However, we acknowledge, that community shifts remain a plausible contributor to observed water column BSi_WC : POC_WC signals, but they would not explain why the strongest decline in silica ballasting ratios occurs in exported material.

Lastly, changes in microbial carbon remineralization or particle sinking time could in principle alter sediment trap silica ballasting ratios (BSi_Sed : POC_Sed). Because organic carbon remineralization proceeds faster than silica dissolution, exported particles typically become enriched in BSi relative to POC with depth (Armstrong et al., 2001; Karakuş et al., 2025; Ragueneau et al., 2006). Consistently, we observed a two-fold enrichment of BSi : POC from the water column to the sediment trap at ambient alkalinity, but this enrichment was significantly reduced at higher alkalinity. Such a pattern would require systematic pH-driven changes in remineralization rates and/or residence time during sinking (i.e., sinking velocities). However, biomass-normalized remineralization proxies (CR : Chl a, Bac : Chl a) showed no systematic variation with pH, nor with particle porosity, known to enhance bacterial remineralization during transit (Grossart and Ploug, 2001; Ploug et al., 2002). Likewise, particle sinking velocities showed no consistent relationship with pH (aside from the pronounced increase associated with carbonate precipitation) and were not systematically related to porosity, also known to influence settling speed (Azetsu-Scott and Passow, 2004; Bach et al., 2019c). Thus, export-side changes in organic carbon remineralization metrics or sinking time were not apparent in our dataset. Taken together, the evaluated production- and export-side alternatives are not consistent with the observed direction and magnitude of the silica ballasting ratio (BSi : POC) response, further supporting pH-driven BSi dissolution to be the most likely explanation.

In addition to pH, we would like to extend our considerations to particle-quality traits. Aggregate microenvironments may modulate BSi dissolution during export. Higher aggregate porosity can enhance porewater exchange, which has been linked to elevated BSi dissolution in sinking particles (Moriceau et al., 2014; Passow et al., 2003). BSi dissolution kinetics are hampered by DSi accumulation in aggregate porewater, suppressing dissolution relative to freely suspended diatom frustules (Moriceau et al., 2007), with the net effect of porosity depending on the balance between porewater exchange and Si-solute build-up. In our mesocosms, porosity of sediment-trap particles increased along the alkalinity-induced pH gradient during bloom-following deposition events. Although we cannot quantify how strongly porosity contributed to BSi dissolution, the tight covariation between porosity and BSi_Sed : POC_Sed (Fig. 4b) suggests that particle-quality traits may provide an additional control on export-phase BSi loss, and could modulate the pH signal.