Antarctic sea ice is one of the largest and most dynamic ecosystems on Earth, with a maximum aerial extent of 19 × 106 km2 in winter and a minimum of 3 × 106 km2 in summer (Parkinson and Cavalieri, 2012). Measurements of primary production in Antarctic pack ice are scarce (Roukaerts et al., 2016), but the available evidence suggests that Antarctic pack ice contributes to a small, but significant, fraction of the primary production of the Southern Ocean (Legendre et al., 1992; Arrigo and Thomas, 2004; Saenz and Arrigo, 2014). Sea ice is a semi-solid medium permeated by a network of channels and pores that are variably connected with seawater (Weeks, 2010). These brine-filled spaces can be heavily colonized by a sympagic (ice-associated) microbial community that is taxonomically diverse and metabolically active (Arrigo et al., 2010; Caron and Gast, 2010; Deming, 2010; and references therein). During its incorporation into the ice, the microbial community is exposed to major biogeochemical and physical changes in its habitat, including fluctuations in temperature, salinity, dissolved oxygen, light, pH, the surrounding organic matrix, and nutrients. These conditions change further during consolidation and melting of the sea ice (Thomas et al., 2010; Fransson et al., 2013; Vancoppenolle et al., 2013).
All organisms must obtain essential elements, termed nutrients, from their external environment to grow. The macro-nutrients (i.e., needed in large amounts) include dissolved inorganic nitrogen (DIN) in the form of nitrate (NO3–), nitrite (NO2–), and ammonium (NH4+), and dissolved inorganic phosphorus (mostly phosphate; PO43–). These nutrients provide structural and functional components to all organisms (Gruber, 2007; Paytan and McLaughin, 2007). By contrast, dissolved silicon [mostly silicic acid; Si(OH)4] is a macro-nutrient predominantly used by diatoms to build their frustules (biogenic silica; bSiO2) and to a lesser extent by radiolarians and silicoflagellates (Tréguer and De La Rocha, 2013). Since primary production in sea ice is thought to be dominated by diatoms (Arrigo et al., 2010), Si(OH)4 has also been suggested as a potentially limiting nutrient in this ecosystem (Gosselin et al., 1990; Smith et al., 1990).
Although many nutrient transformations (e.g., converting one form to another) have been either documented or inferred in Antarctic pack ice, the overall pattern of nutrient concentrations has remained elusive (Arrigo et al., 1995; Gleitz et al., 1995; Rysgaard et al., 2004, 2008; Fransson et al. 2011; Fripiat et al., 2014a, 2014b; Baer et al., 2015; Roukaerts et al., 2016). Previous studies are based on a few ice cores only, limited in space and time (e.g., Thomas et al., 1998; Becquevort et al., 2009). Hence, the high spatial and temporal variability that characterizes pack ice (e.g., Eicken et al., 1991; Rysgaard et al., 2001) has never really been accounted for. We performed a large-scale compilation of nutrient concentration data for pack ice from the Southern Ocean, using both previously published and unpublished data. We describe the patterns that are elucidated by such a large dataset and discuss several associated underlying processes. The information compiled here will also aid in a better parameterization of models representing sea ice algal production (Steiner et al., 2016).
This compilation gathers much of the currently available nutrient data (concentrations of NO3–, NO2–, NH4+, PO43–, and Si(OH)4) from the Antarctic pack ice. The data were derived from peer-reviewed publications, cruise reports, and direct contributions by field-research teams. The dataset is based on nutrient analyses performed on 2639 ice sections from 306 ice cores and on 93 samples of sackhole brines, all collected in the course of 19 cruises (see Table S1). The locations of these studies are shown in Figure 1.
During most of the cruises, bulk ice nutrient concentrations (in µmol L–1) were measured in melted ice core sections (n = 2487). The general procedure consists of collecting a core, dividing it into sections (average section thickness = 0.09 ± 0.04 m) using a clean stainless steel saw, followed by the melting of the ice sections in the dark at ambient temperature or < 4°C (see Miller et al., 2015). Nutrient concentrations in brine were obtained either from measurements in samples extracted from centrifuged ice sections (n = 152; average section thickness = 0.14 ± 0.05 m) (Arrigo et al., 2003; Munro et al., 2010), or using the sackhole technique (n = 93), i.e., drilling partial core holes to a desired depth within the ice and allowing brines from the surrounding ice to drain into the hole (Gleitz et al., 1995). These methods have been shown to be robust for nutrient sampling (Miller et al., 2015). In the following discussion, both centrifuged and bulk melted ice sections are presented together after salinity-normalization (i.e., equivalent nutrient concentration at seawater salinity; section 3.2). Sackhole data are used only for comparison with corresponding ice cores taken during the same cruises (section 3.4).
Nutrient concentrations were measured in filtered and unfiltered samples (Table 1), either in field laboratories soon after melting (ice core sections) or collection (brines) (52% of the analyses), or at home-based laboratories following storage either at ≤ –18°C or by poisoning with HgCl2 and refrigeration (Dore et al., 1996; Kattner et al., 1999; Hydes et al., 2008). No significant differences have been reported in the literature between samples stored frozen or poisoned and samples treated immediately (Dore et al., 1996; Kattner et al., 1999; Wurl, 2009; Fawcett et al., 2014). The only exception is NH4+ in poisoned samples, for which a systematic enrichment has been reported (Kattner et al., 1999). This type of storage was applied to 27% of the NH4+ samples from this dataset (Thomas et al., 1998; Kennedy et al., 2002; Nomura et al., 2016), a potential bias discussed further (Section 3.2). No differences have been reported between filtered and unfiltered samples during storage (Dore et al., 1996; Kattner et al., 1999; Fawcett et al., 2014). Another concern is Si(OH)4 polymerization during freezing storage and its slow depolymerization when the sample is thawed for analysis, potentially resulting in underestimation of the actual Si(OH)4 concentration (e.g., Hydes et al., 2010). Prolonged thawing has been applied for Si(OH)4 determination in this dataset, which has been proven suitable for the recovery of the polymerized forms of silicic acid during analysis (Dore et al., 1998).
|Method||Analysis||Filtration||Storage||# Coresa||# Sackholesa|
|Colorimetric + OPAd||on ship||yes||none||38||14|
|Colorimetrice||home laboratory||yes||< –18°C; < 18 months||22||0|
|Colorimetric + OPAf||home laboratory||yes||< –18°C; < 6 months||34||0|
|Colorimetric + OPAg||home laboratory||yes||HgCl2 poisoning; 4°C; < 3 yearsh||53||17(17)|
|Colorimetrici||home laboratory||no||< –20°C; < 3 months||17(17)||0|
|Colorimetricj||home laboratory||no||–80°C; < 6 months||12||0|
|Colorimetrick||home laboratory||no||HgCl2 poisoning; –20°C; < 3 months||3(3)||0|
|Colorimetricl||home laboratory||no||HgCl2 poisoning; 4°C; < 8 months||6||11|
The sea ice nutrient measurements presented here (Table 1) are mostly based on automated or manual colorimetric analysis (e.g., Hydes et al., 2010). In some studies, NH4+ concentrations were measured using the fluorometric method (“OPA”) described in Holmes et al. (1999). To avoid analytical salinity effects given the wide range of salinities in sea ice samples, from melted ice sections to high-salinity brines, the calibration standards were prepared in artificial seawater solutions with salinities similar to those of the samples analysed. The measuring technique for DIN targets individual chemical species: NO3–, NO2–, or NH4+/ NH3. Soluble reactive phosphorus is defined as the dissolved P fraction that reacts in an acid solution containing molybdate ions to form a complex that can be coloured by further reduction with ascorbic acid. This fraction includes mostly dissolved inorganic PO43– (HPO42– and PO43–) but also some easily hydrolysable inorganic and organic P forms (Paytan and McLaughlin, 2007). Over the pH range that characterizes both sea ice and seawater, non-ionized Si(OH)4 is the dominant form of dissolved silicon, with the remainder being largely SiO(OH)3– (Sjöberg et al., 1981). Hereafter, soluble reactive phosphorus and dissolved silicon are referred to as phosphate (PO43–) and silicic acid (Si(OH)4), respectively. When NO2– concentrations were unavailable, the available NO3– + NO2– concentrations are presented as NO3– only. This assumption is reasonable given the small and relatively constant contribution of NO2– to the NO3– + NO2– pool (median contribution of 5% in this dataset; Table S1).
There are concerns that the salinity change during the melting of ice core sections may induce osmotic shock to the ice-associated microbial cells, causing cell lysis and release of the intracellular nutrient content into solution. Significant differences in cell counts between melting treatments have been reported for samples containing flagellates and ciliates, which are considered to be particularly susceptible to osmotic shock (Garrison and Buck, 1986; Michelsen and Witkowski, 2010; Rintala et al., 2014), but also for bacteria in winter ice with brine salinities > 100 (Ewert et al., 2013). The changing conditions during melting could also induce stress to live cells, resulting in efflux of intracellular nutrients to the external medium. Measured nutrient concentrations would be expected to increase with increasing biomass if contribution by cell lysis or nutrient efflux from stressed live cells were significant (Thomas et al., 1998). The absence of a significant correlation between bulk nutrient and chlorophyll-a concentrations in bulk sea ice suggests minimal contribution of intracellular nutrients from algal cells to the measured concentrations (range of variability was 450-fold for bulk chlorophyll-a concentration and 40-fold for bulk nitrate concentration; Table S1).
High intracellular concentrations have been reported for all nutrients in flagellates and ciliates, with intracellular NO3– and NH4+ concentrations ranging from undetectable to 47.4 mmol L–1 (Dortch et al., 1984; Lomas and Glibert, 2000; Kamp et al., 2015). Using these values and focusing on cell lysis, the typical upper range for algal cell abundance in Antarctic pack ice (107 cell L–1), and maximum sea ice flagellate cell volume (370 µm3) (Garrison and Buck, 1989), we estimated the maximum potential contribution of cell lysis to the dissolved nutrient pool of melted ice core sections. We further assumed Redfield N:P ratio to estimate the intracellular PO43– pool (Sterner and Elser, 2002). Because only flagellates appear to be susceptible to cell lysis during sample melting, the melting effect on measured Si(OH)4 concentrations was assumed to be negligible. This calculation shows that the maximum contribution of the intracellular nutrient pool would be equivalent to 0.18 µmol L–1 for both NH4+ and NO3–, and 0.02 µmol L–1 for PO43–. Such contributions from cell lysis are marginal as they are lower than most of the measured nutrient concentrations in melted bulk sea ice (Figure 2). During a recent Baltic sea ice study, where direct and salinity-buffered melting were compared, no significant differences in nutrient concentrations were observed (Rintala et al., 2014). However, as pointed out by Miller et al. (2015), a more systematic investigation is required of the different sample treatments, including centrifugation of ice sections.
As with any literature compilation and given what could be viewed as a relatively small amount of data (306 ice cores from 19 cruises), there are inevitable biases in our dataset in terms of both spatial and temporal coverage. Most of the data (53%) were obtained from sea ice in the Atlantic sector of the Southern Ocean, while 26% of the data were obtained from sea ice in the Bellingshausen, Amundsen, and Ross Seas, and 21% from Eastern Antarctic sea ice (Table 2). A large proportion of the Antarctic pack ice not represented here is therefore still undocumented. Spring (21 September to 20 December) is the most represented season (55%), followed by summer (21 December to 20 March; 22%), winter (21 June to 20 September; 16%), and autumn (21 March to 20 June; 6%) (Figures 1 and 3; Table 2).
|Sector||Longitude||# Cores||# Sackholes||Time frame||Ice thickness (m)|
|Atlantic||60°W/20°E||161||31||27 April–02 March||0.1–4.3|
|Australian||90°E/160°E||55||23||27 September–28 October||0.3–2.3|
|Ross||160°E/130°W||43||4||6 November–1 January||0.1–1.5|
|Bellingshausen/Amundsen||60°W/130°W||36||3||23 April–1 March||0.4–4.3|
The average thickness of ice (0.85 ± 0.65 m; n = 306) and snow (0.17 ± 0.18 m; n = 150) are indistinguishable from that estimated by the ASPeCt (Antarctic Sea ice Processes and Climate) dataset built from ship-based observations around Antarctica (0.87 ± 0.91 and 0.16 ± 0.20 m, respectively; n = 23373) (Worby et al., 2008). However, thinner ice types have been under-sampled in our dataset, especially in autumn and winter when the pack ice expands. The evolution from thinner to thicker ice from autumn through to summer is roughly reproduced in our dataset (Figure 3), which is nevertheless biased towards thicker ice. Pressure ridges make up a significant fraction of the Antarctic pack ice cover (with surface ridging covering 12 ± 15 %; Worby et al., 2008), but none of the compiled ice cores falls in this category. Based on autonomous underwater vehicle retrievals, Williams et al. (2015) recently estimated that deformed ice comprised an average of 57 % (volumetric) of the investigated floes, far exceeding that estimated from previous shipboard observations and drilling data.
For all these reasons, our discussion will be focused on level ice and associated nutrient transformations from late winter to late summer, i.e., the most represented time periods in the current data compilation. We do not make the distinction between first-year and multi-year ice because no clear differences in nutrient concentrations were observed, and only 9 of the 306 cores have been identified as multi-year ice (in peer-reviewed publications or cruise reports).
Seawater is the main source of nutrients in Antarctic pack ice (Gleitz et al., 1995), with a minor contribution expected from atmospheric deposition. Nutrient-rich Circumpolar Deep Water ascends into the surface of the Antarctic Zone of the Southern Ocean (south of the Polar Front; Figure 1). Upwelled waters are either transported northward or southward to form the upper and lower branches of the meridional overturning circulation, before the available nutrient pools can be fully utilized by phytoplankton (Speer et al., 2000; Sarmiento et al., 2004; Rintoul et al., 2009). The inability to strip nutrients out of the surface oceanic water has been attributed to light and iron co-limitation (Martin et al., 1990; Mitchell et al., 1991) and results in high macro-nutrient concentrations year-round in the Antarctic Zone (Garcia et al., 2014): specifically, the NO3– concentrations range from 30–35 µmol L–1 to 20–25 µmol L–1, the PO43– concentrations from 2.0–2.4 to 1.4–2.0 µmol L–1, and the Si(OH)4 concentrations from 50–90 to 40–75 µmol L–1 during winter and summer, respectively. The higher Si(OH)4 compared to NO3– and PO43– depletion in the surface waters has been attributed to the influence of iron-limited diatom growth that dramatically increases their Si to nutrient assimilation ratios (where ‘nutrient’ refers to both N and P; Hutchins and Bruland, 1998; Takeda, 1998; Claquin et al., 2002), along with processes involved in the so-called “silicate pump” (i.e., deeper remineralization of Si relative to C, N, and P; Dugdale et al., 1995). Both NH4+ and NO2– are intermediaries in the biological N cycle (assimilation, ammonification, and nitrification). By producing and consuming both NH4+ and NO2–, the microbial community maintains low and relatively constant concentrations of these compounds (usually below 0.4 µmol L–1) year-round in the surface waters (Gruber, 2007).
Nutrient dynamics in sea ice are driven by biologically-mediated consumption and assimilation into biomass and by production via remineralization, as well as by brine transport. Because they are expelled from the ice crystal lattice, dissolved sea salts are mostly concentrated in the interstitial brine (Vancoppenolle et al., 2013). Controlled by the same physical processes, nutrients in sea ice would behave like major dissolved sea salts when biological activity is negligible. Upon freezing, dissolved sea salts are partly incorporated in the sea ice but they are quickly lost due to desalination processes within a few days (Notz and Worster, 2009). Hence, pack ice has a typical bulk salinity (Sbulk) of ~ 5, whereas seawater in the sea-ice covered Antarctic Zone has a salinity of ~ 34 (Figure 4). During ice growth, exchange with seawater occurs nearly continuously in a thin layer near the ice-ocean interface (Rees-Jones and Worster, 2013). In this process, the downward temperature gradient generates an upward brine salinity gradient, destabilizing the brine column and forcing brine convection with seawater (Notz and Worster, 2009; Wells et al., 2011). Full-depth brine convective events may also occur episodically, once the ice has warmed sufficiently in spring to make the entire ice thickness permeable to fluid transport (Griewank and Notz, 2013; Jardon et al., 2013). Seawater flooding of the snow base increases the salt and nutrient content near the ice surface. Seawater flooding is commonly observed in Southern Ocean pack ice characterized by high snow accumulation (up to 3 m) on relatively thin ice (Worby et al., 2008). As a result, the snow-ice interface often sinks below sea level, resulting in a negative ice freeboard (the elevation of the snow-ice interface relative to the local sea surface) and hydraulically forcing the infiltration of seawater and brine into snow, with slush and snow ice forming in the process (Jeffries et al., 1997, 2001; Haas et al., 2001; Maksym and Markus, 2008; Papadimitriou et al., 2009).
The combination of these processes explains the different salinity profiles observed in winter and spring pack ice (C- and S-shaped profiles; Figure 4) (Eicken, 1992), compared to summer pack ice which exhibits lower near-surface salinities than in the underlying layers (?- and i-shaped profiles) due to surface melting in summer (Eicken, 1992; Haas et al., 2001; Weeks, 2010). The effect of fluid transport through sea ice is discernible in profiles of nutrient concentrations in sea ice. If biological activity were negligible, bulk nutrient concentrations would follow the conservative trend of the major dissolved salts as measured by bulk salinity. Seawater-derived nutrients (NO3–, PO43–, and Si(OH)4) present a distribution roughly similar to salinity, with both C-shaped and S-shaped profiles in both winter and spring, as well as ?-shaped and i-shaped profiles in summer (Figures 2 and 4). Despite large scatter, the correlation between bulk nutrient concentrations and bulk salinity is significant in all seasons (p-value < 0.05; not shown). Winter NO3– and Si(OH)4 concentrations are the most highly correlated with salinity (slope of 0.7 and 1.1, R2 of 0.45 and 0.62, p-value < 0.001, respectively). The large scatter can be attributed to variability in biological nutrient transformations (section 3.2). Similar to salinity, bulk nutrient concentrations in sea ice are lower than those in seawater. This difference indicates that, following incorporation into sea ice, nutrients are partly expelled out of the growing sea ice during desalination.
Net consumption of nutrients during microalgal growth is associated with their assimilation into organic matter during the spring–summer bloom (Figure 5). Total concentrations (organic + inorganic) are only available for nitrogen, for which data on particulate N (PN; n = 606), dissolved organic N (DON; n = 858) and DIN are available (Figure 5; Table S1 in supplementary materials; mainly from spring to summer). No data are available for organic P and only Fripiat et al. (2007) reported measurements of biogenic silica concentrations in Antarctic pack ice. Most of the observations indicate lower total N concentrations in summer, and even more so in spring, than in seawater (Figure 5d). However, the concentration of total N is higher than would be predicted from the salinity of the melted sample (~ 5 µmol L–1) and consists mostly of organic N (Figure 5). Higher bulk total N concentrations than in seawater are commonly observed in the bottom sea ice layer in spring and at all depths in summer, with maximum PN, DON, and DIN concentrations of 616, 78, and 81 µmol L–1, respectively. These concentrations are equivalent to ~ 15–20 times the concentration in seawater. The mass balance of nutrients in sea ice is controlled by desalination and microbial activity. During ice growth, desalination results in nutrient expulsion from the ice but the activity of ice-associated organisms will generate an interior sink for nutrients via assimilation into biomass. This biologically-mediated sink can be higher than the net removal of nutrients from the system via desalination. It is still uncertain whether the bulk of organic matter produced in situ or scavenged from the seawater is degraded and respired within sea ice or in surface waters after melting, or if it is exported to the deep ocean (Smith and Nelson, 1985; Riebesell et al., 1991; Boetius et al., 2013). The overall balance amongst these processes will determine the fraction of the nutrients (and carbon) removed from surface oceanic water through the sea ice biological pump.
As discussed above, bulk salinities and solute concentrations are affected by the fluid transport, while brine salinity and nutrient concentrations are affected by temperature-driven concentration and dilution. To tease apart these physical effects, the salinity-normalized nutrient concentration C* is calculated as follows:(1)
where C is the measured nutrient concentration (bulk ice or brine), Sw is the salinity of seawater, and S the corresponding measured salinity in the sample (bulk ice or brine). We use a constant initial seawater salinity of 34.3, as surface salinity values in the polar Antarctic zone range from 33.5 to 35 (World Ocean Atlas 2013), which implies a maximum uncertainty of 5% in the estimates of C*. This level of uncertainty is below the analytical precision of nutrient measurements (relative standard deviation of ~ 10%). Normalization to salinity filters out the effect of physical processes and allows us to focus on the effects of biogeochemical processes, which are the topics of the following sections. This assumption is valid as long as nutrients come from seawater; it could be invalidated either when nutrient-loaded meltwater from snow infiltrates sea ice or when infiltrated seawater passes through intermediate ice layers where biogeochemical processes have altered the original seawater nutrient-to-salinity ratio. In order to better assess the effect of nutrient-loaded snow, we recommend that, in future, researchers systematically measure nutrient concentrations in the overlying snow.
The annual cycle of nutrients in pack ice was investigated here by grouping the data into seven periods of about one month each (Figures 3, 6 and 7). Given the small amount of data available for austral autumn and early winter, those data were binned into a single time period (from March to July) and will be discussed briefly at the end of this section. Results are also presented as a function of depth (surface, 0.0–0.2 m from the ice surface; bottom, 0.0–0.1 m from the bottom; and interior, between the surface and bottom layers), reflecting the main sea ice habitats (Arrigo and Thomas, 2004). In support of the circumpolar seasonal trends, the seasonal evolution for the Atlantic sector (between 60°W and 8°E) is shown for comparison and is in good agreement with the circumpolar trends (Figures S1 and S2). At any given time, a large variability in salinity-normalized nutrient concentrations is evident (Figures 6 and 7), most likely due to the large spatial variability common to many sea ice properties (Eicken et al., 1991; Arrigo and Thomas, 2004). Despite this variability, clear and contrasting seasonal trends for the different nutrients were discernible (Figures 6 and 7), as also represented in vertical profiles (Figure 8).
The *NO3– concentrations in winter sea ice are indistinguishable from seawater concentrations (Figures 6a and 8a), suggesting either little or balanced NO3– production (nitrification) and consumption (assimilation) during this period. Following the increase in solar radiation in spring and the resulting algal bloom, *NO3– tends to be depleted significantly in comparison to seawater at all depths within sea ice from September to March (Figures 6a and 8a; see Table S2 for pairwise multiple comparison; Gleitz et al., 1995; Thomas et al., 2010). The *NO3– concentrations tend to be higher at the bottom of the ice due to replenishment by nutrient-rich underlying seawater (Figures 6a and 8a).
Together with the decrease in solar radiation, *NO3– concentrations tend to increase in February (significantly only in the interior of sea ice; Table S2). During this time, sea ice around Antarctica is at its annual minimal areal extent, with a perennial ice cover remaining in the western Weddell Sea and in coastal regions along the Bellingshausen, Amundsen, and Ross Seas (Figure 1; Parkinson and Cavalieri, 2012). Two processes can be responsible for such an increase in *NO3– concentrations: (i) an increase in the exchange with nutrient-rich seawater in porous decaying sea ice (Fritsen et al., 1994; Kattner et al., 2004; Haas et al., 2001), or (ii) an imbalance between the processes of NO3– production (nitrification, partly light-inhibited) and consumption (assimilation, light-dependent) with the decrease in solar radiation. Nitrification has been shown to be significant in sea ice (Priscu et al., 1990; Fripiat et al., 2014a, 2015; Baer et al., 2015; Firth et al., 2016), with the microbial community being embedded in biofilms and exposed to both low-light and high NH4+ concentrations from decaying organic matter (Hagopian and Riley, 1998; Meiners et al., 2004; Ward, 2007; Deming, 2010).
In agreement with in situ production, *NH4+ and *NO2– typically accumulated within pack ice at all times and all depths (Figures 6b, 6c and 8b). The *NH4+ concentrations are relatively constant in spring (from September to December; see Table S2 for pairwise multiple comparison). In the pelagic euphotic zone, NH4+ produced by remineralization is swiftly assimilated back into biomass, maintaining low and constant concentrations in the surface waters (Gruber, 2007). Such a scenario is likely to occur within productive sea ice in spring, implying a balance between NH4+ production (remineralization) and consumption (assimilation and nitrification) processes.
The *NH4+ concentrations increase significantly in summer (January – February; see Table S2 for pairwise multiple comparison; Figures 6b and 8b). This increase cannot be explained by an increase in the exchange with NH4+-poor seawater (< 0.4 µmol L–1), as this process would dilute instead of concentrate the NH4+ pool. Similar to NO3–, remineralization is not directly affected by light but assimilation by (algal) primary producers is light-dependent. When light decreases (Figure 6c), such assimilation is likely to decrease while the unaffected remineralization rates will result in a net increase in the *NH4+ concentration. The build-up of a large pool of ice-trapped organic matter from spring to summer and its subsequent remineralization will further accentuate this trend. The available data in both January and February, however, have been measured only on poisoned samples (HgCl2; Thomas et al., 1998; Kennedy et al., 2002). Such preservation has been shown to have an effect on NH4+ concentrations, being systematically higher than for samples analyzed immediately onboard ship (Kattner et al., 1999). By taking the NH4+ relationship between poisoned and immediately treated samples in Kattner et al. (1999), a median of 2.3 μmol L–1 measured on poisoned samples in bulk summer sea ice (Figure 2) will give a concentration of ~ 1.5 μmol L–1 in immediately treated samples, implying a correction in salinity-normalized concentrations from 18 to 12 μmol L–1 for a bulk salinity of 4.5 (Equation 1). This corrected value is still higher than spring *NH4+ concentrations, being closer to 6 μmol L–1, in agreement with the hypothesis described above. We recommend freezing as a better mode for preservation in future studies (Dore et al., 1998; Wurl, 2009; Fawcett et al., 2014).
The *NO2– concentrations remain relatively low and constant in spring–summer (with median *NO2– concentrations between 0.2 and 0.8 µmol L–1; Figure 6b; see Table S2 for pairwise multiple comparison), also implying a balance between production (NH4+ oxidation, i.e., first step in the nitrification process) and consumption (NO2– oxidation, i.e., second step of nitrification, and assimilation). To conclude, DIN appears to be actively assimilated and regenerated within pack ice, supporting the view that the sympagic microbial community is efficient in processing fixed nitrogen either to synthesize new biomass or to use as a source of energy for growth (e.g., Fripiat et al., 2015).
Silicic acid is mainly required for the growth of diatoms, with likely minor consumption by silicoflagellates and radiolarians, to form their cell walls (i.e., biogenic silica, bSiO2) (Tréguer and De La Rocha, 2013). Despite the growing recognition of the role played by flagellates in sea ice habitats (Caron and Gast, 2010; Torstensson et al., 2015), diatoms are thought to dominate primary production in Antarctic sea ice (Arrigo et al., 2010). Silicon is therefore a potentially limiting element for diatom-based primary production in sea ice (as suggested for Arctic sea ice by Gosselin et al., 1990, and Smith et al., 1990).
In Antarctic pack ice, *Si(OH)4 is partially depleted in comparison to seawater at all depths in December and January during the spring–summer transition (see Table S2 for pairwise multiple comparison; Figure 7c). Such partial depletion is poorly represented in vertical profiles (Figures 2 and 8) when regrouped as spring and summer sea ice. The strongest depletion occurs in January during the most under-sampled time period in our data set (one cruise in the Weddell Sea, five ice cores; Kennedy et al., 2002). Relative to NO3–, the small depletion in Si(OH)4 concentrations from winter to summer is at odds with the idea that sea ice primary production is dominated by diatoms (Thomas and Arrigo, 2004). The average Si:N ratio for a broad range of diatom species growing under nutrient-replete conditions is 1.0, and this ratio increases during light, N, P or Fe-limited growth (Brzezinski, 1985; Hutchins and Bruland, 1998; Takeda, 1998; Claquin et al., 2002). Further, the *Si(OH)4 concentrations tend to be depleted later than NO3–, with a time lag of approximately 1–2 months (Figure 7c). These findings suggest that a significant fraction of primary productivity in sea ice is sustained by flagellates (e.g., Becquevort et al., 2009; Arrigo et al., 2014; Torstensson et al., 2015).
Similar to NO3–, the *Si(OH)4 concentrations increase in January – February (see Table S2 for pairwise multiple comparison), indicating either an increase in the exchange with the nutrient-rich seawater or a net increase in biogenic silica dissolution relative to its production. The temporal trend of increasing concentrations of *NH4+ in sea ice suggests that dilution by infiltration of seawater rich in Si(OH)4 but poor in NH4+ cannot account for the observed increase in *Si(OH)4 concentration in summer sea ice and that the more likely explanation is dissolution of biogenic silica in the ice. It is generally assumed that biogenic silica dissolution rates are low under sea ice conditions, especially due to low temperatures. However, biogenic particles tend to remain trapped in the brine network, implying a much longer residence time for detrital biogenic silica in sea ice (weeks to months) compared to that of detritus in the euphotic zone of the ocean (days to weeks). Assuming that the specific dissolution rates (Vd) measured in the Ross Sea (0.01 to 0.19 d–1; Nelson et al., 1991) are representative of sea ice, half of the detrital biogenic silica in sea ice, i.e., ln(2)/Vd, can be dissolved in 4 to 70 days. In addition, the often high bacterial population density in sea ice (Deming, 2010) should promote efficient removal of the organic coating from diatom frustules, exposing naked frustules to the ambient brine environment under-saturated with respect to bSiO2 (Bidle and Azam, 1999). Biogenic silica dissolution is therefore likely to be significant in Antarctic sea ice (Fripiat et al., 2014b), as manifested in the increasing concentrations of *Si(OH)4 in late summer.
In contrast to the NO3–-depleted sea ice, *PO43– concentrations in sea ice increase progressively in spring–summer to values higher than in seawater (see Table S2 for pairwise multiple comparison; Figures 7b and 8c), except for two outliers on 15 January at the surface and interior of the ice, which were the lowest *PO43– concentrations of this dataset. This time period is under-represented in our data set (one cruise in the Weddell Sea, five ice cores; Kennedy et al., 2002) so that we cannot rule out a bias in terms of how representative the available data are in January. Excess PO43– has been observed in several instances in Antarctic pack ice (Clarke and Ackley, 1984; Arrigo et al., 2003; Kattner et al. 2004; Papadimitriou et al., 2007; Becquevort et al., 2009; Munro et al., 2010; Meiners et al., 2011). The unique behavior of PO43– in sea ice relative to that in the pelagic realm is discussed further in Section 3.5. Intriguingly, *PO43– is depleted relative to seawater in winter with a tendency to lower concentrations in the interior and at the surface of the ice (see Table S2 for pairwise multiple comparison; Figures 7b and 8c). Hu et al. (2014) reported PO43– co-precipitation with ikaite (CaCO3·6H2O) in laboratory experiments. Ikaite has been mainly extracted from the surface and interior of the ice where low temperature, high brine salinity, and low porosity prevail (Dieckmann et al., 2008; Papadimitriou et al., 2013; Rysgaard et al., 2014; Moreau et al., 2015); these conditions are expected to prevail in Antarctic pack ice in winter.
Although usually overlooked, autumn blooms have been documented in Antarctic sea ice (Fritsen et al., 1994; Delille et al., 2002; Meiners et al., 2012). Such blooms can explain the observed partial *NO3– depletion with a concomitant accumulation in both *NH4+ and *NO2– in autumn–early winter (Figure 6). The *PO43– concentrations indicated accumulation in sea ice to concentrations higher than those in seawater, but *Si(OH)4, rather than being depleted, was in the range of seawater concentrations (Figure 7). As in early spring, NO3– depletion and the closeness of Si(OH)4 concentrations to seawater values together suggest that diatoms are also not the dominant primary producers in sea ice in autumn. Additional studies are needed in this time period, which likely contributes a significant, if small, fraction of the total primary production in Antarctic sea ice (Saenz and Arrigo, 2014; Lieser et al., 2015).
Together with light, nutrients likely limit primary production in Antarctic sea ice (Arrigo and Thomas, 2004; Vancoppenolle et al., 2013). Co-limitation occurs when one or several specific nutrients are at insufficient concentrations to sustain maximum growth rates. Inhibited growth at high salinity has also been suggested to influence the distribution of primary productivity within sea ice (Arrigo and Sullivan, 1992). Iron and other trace metals are usually found at high concentrations in Antarctic sea ice (Lannuzel et al., 2016), in strong contrast with Southern Ocean surface waters (Martin et al., 1990).
In the present dataset, the most likely limiting nutrient in pack ice is DIN, although the lowest median *DIN concentrations are still significant (> 12 µmol L–1; Figure 6). For comparison, phytoplankton in the euphotic zone are usually N-limited when DIN is significantly below 2 µmol L–1 (Moore et al., 2013). This consideration arises by the observation that *PO43– is present at higher concentrations in sea ice than in the deep ocean and that *Si(OH)4 is depleted to a lower extent than *DIN (> 15 µmol L–1; Figure 7). However, salinity-normalized concentrations do not represent the concentrations available to the sympagic organisms in individual brine pockets and channels. To estimate brine concentrations from measurements in bulk (melted) sea ice, the brine volume fraction must be estimated from bulk ice salinity and temperature, assuming ice-brine (thermal) equilibrium (Cox and Weeks, 1983). Unfortunately, temperature measurements were seldom available for most of the ice sections compiled in this investigation (which future studies need to rectify, as urged by Miller et al., 2015). By dividing the median bulk concentrations for DIN, PO43–, and Si(OH)4, binned by time period, by the maximum expected ice porosity (0.2) characteristic of warm and saline Antarctic pack ice (e.g., Tison et al., 2008), the median nutrient concentrations in brines for the time periods derived from the lowest concentrations in bulk sea ice were estimated at 7.2, 0.3, and 7.9 µmol L–1, respectively, concentrations still much higher than those encountered in the oligotrophic ocean. In comparison, the median concentrations for DIN, PO43–, and Si(OH)4, for the sackhole brines in spring–summer (n = 57) are 1.1, 0.3, and 32.8 µmol L–1, respectively. The latter analysis is based on a much smaller amount of data, so that the representativeness both in space and time should be taken with caution.
We are not aware of any studies reporting the affinity of sea ice algae for nutrients, defined for phytoplankton as the efficiency with which the cell exploits low nutrient concentrations. Nutrient affinity is usually inferred from the half saturation constant in a Michaelis-Menten saturation function. In the ocean, relatively large variations in nutrient affinity are reported, with half-saturation constants varying from 0.02 to 10.3, 0.01 to 8.9, and 0.2 to 61 µmol L–1 for DIN, PO43– and Si(OH)4, respectively (Eppley et al., 1969; Nelson et al., 2001; Sarthou et al., 2005). Given this variability, it is difficult to assess accurately which nutrients may limit primary production in Antarctic sea ice. Nutrient affinity is affected by cell size (Eppley et al., 1969; Timmermans et al., 2005), temperature (Nedwell et al., 1999; Reay et al., 1999), and salinity (Aslam et al., 1984; Martinez et al., 1994). Given the biotic conditions encountered in sea ice brines (low temperatures and high salinity), the affinity for nutrients is likely to differ from that in seawater and requires further investigation (Thomas and Dieckmann, 2002). Investigation of potential systematic differences in cell properties (e.g., cell size, surface-to-volume ratio) between sea ice and pelagic microorganisms are also crucially needed. For the ocean, incubation experiments involving nutrient additions have typically been used to assess which nutrients are limiting, allowing also the determination of kinetic uptake parameters (i.e., half saturation constant and maximum specific uptake rate). However, we acknowledge the inherent difficulties in performing similar incubation experiments for sea ice (Miller et al., 2015). The utilization of protein biomarkers of nutrient limitation could be valuable in this regard (Saito et al., 2014), as this approach does not require manipulation of the microorganisms.
Adsorption here refers to the accumulation of chemicals at the solid-liquid interface. Nutrient adsorption is still overlooked in sea ice. To consider this process in more detail, a comparison was made between sackhole and adjacent bulk ice core data. It is recognized that the spatial variability of sea ice properties might partially invalidate such a comparison, as adjacent cores can have very different biogeochemical compositions (Eicken et al., 1991), and brine collected in the holes integrates the biogeochemical properties of numerous individual brine structures from an undefined volume of ice (over several tens of centimeters; Miller et al., 2015). For these reasons, only qualitative comparisons of large differences are considered. No clear differences in salinity-normalized concentrations for either NO3– + NO2–or Si(OH)4 were evident. In contrast, higher salinity-normalized concentrations are observed in bulk-melted ice sections for NH4+ and, to a lesser extent, for PO43– (Figure 9).
NH4+ adsorption onto organic matter is a well-known process within soils (Sollins et al., 1988; Spotiso, 2008; Thompson, 2012), sediments (Blackburn and Henriksen, 1983; Seitzinger et al., 1991), and biofilms (Kurniawan et al., 2012). This adsorption results from the presence of ionizable functional groups (carboxyl and hydroxyl groups being the most important) that confer a negative net charge to organic matter following deprotonation at pH values also typically encountered in sea ice. Sea ice contains a large amount of organic matter, both living and detrital, that remains trapped within the ice (Thomas et al., 1998, 2001; Kattner et al, 2004; Dumont et al., 2009; Underwood et al. 2013). Organic matter is under-represented in sackhole samples (Weissenberger, 1992; Becquevort et al., 2009), likely due to preferential adsorption onto the ice walls, ‘filtration’ by the brine channel network, and the impeded transport of sticky, gelatinous biofilms (Miller et al., 2015). Any NH4+ adsorbed onto organic matter will not be completely collected with the sackhole technique, while, to be measured in bulk-melted ice sections, NH4+ desorption must occur. It is likely that the melting of ice core sections induces desorption of this easily exchangeable pool via dilution by meltwater and the associated change in the ionic strength and pH of the melting medium (Spotiso, 2008; Thompson, 2012; Kurniawan et al., 2012). Clearly, further work is required to better characterize NH4+ adsorption in sea ice, which potentially immobilizes the NH4+ produced by remineralization in close proximity to the microbial community.
The comparison of PO43– concentrations between sackholes and bulk-melted ice sections also suggests some adsorption within sea ice but to a lesser extent than for NH4+ (Figure 9). PO43– adsorption is a well-known process in soils (Sollins et al., 1988; Spotiso, 2008) and sediments (Paytan and McLaughlin, 2007) but mainly on minerals, such as clays and metal (oxy-hydro) oxides. However, such minerals are not likely to be abundant in Antarctic pack ice, nor does PO43– react directly with organic matter, likely the main adsorbent within sea ice. However, PO43– does react with Fe and Al associated with organic matter (metal-DOM complexes; Yuan and Lavkulich, 1994; Zhou et al., 1997; Maranger and Pullin, 2003). The presence of both large quantities of organic matter and trace metals in sea ice may promote this adsorption pathway (Thomas et al., 2001; Dumont et al., 2009; Lannuzel et al., 2011), as suggested in Becquevort et al. (2009). It should be noted that concentration differences between sackhole brines and melted bulk sea ice are also reported for dissolved Fe in Antarctic sea ice, suggesting potential Fe adsorption within sea ice in agreement with our hypothesis (Lannuzel et al., 2016).
Both DIN and Si(OH)4 were found to be partially depleted in spring–summer while PO43– tended to accumulate in Antarctic sea ice, all relative to a simple physical concentration-dilution process upon incorporation of surface seawater nutrients into sea ice as reflected in salinity changes (Figures 6, 7 and 8). These patterns are also reflected in the ratios of DIN to PO43– and Si(OH)4 to PO43–, which both decrease from late winter to spring–summer, with median values relatively close to seawater (~ 16 and 35) in winter decreasing to 4.7 and 7.6, respectively, in spring–summer (Figure 10). Accumulation of PO43– has been reported in many instances in Antarctic pack ice (Clarke and Ackley, 1984; Arrigo et al., 2003; Kattner et al. 2004; Papadimitriou et al., 2007; Becquevort et al., 2009; Munro et al., 2010; Meiners et al., 2011), as well as in land-fast sea ice (Arrigo et al., 1995; Cozzi, 2008).
To accumulate to salinity-normalized concentrations higher than in seawater, nutrients must be trapped within sea ice. Exchange with the nutrient pool of surface seawater and nutrient assimilation into biomass can lead to the build-up of a large interior pool of biomass-associated nutrients that can be trapped in the narrow brine channel system of sea ice. Bacterial colonization, algal mortality, cell lysis, and sloppy feeding can mobilize the ice-trapped organic matter and promote its remineralization (Günther et al., 1999; Thomas and Dieckmann, 2002), allowing the accumulation of excess nutrient concentrations relative to surface seawater. Assimilation and remineralization at constant N:P:Si cannot lead to preferential accumulation of a single nutrient as observed for PO43–. Excess PO43– will develop only if phosphorus is preferentially assimilated or remineralized relative to DIN and Si(OH)4.
(i) Preferential P assimilation. The stoichiometric composition of algae is species-specific and depends on the biochemical allocation of resources for different growth strategies (Geider and La Roche, 2002; Sterner and Elser, 2002; Klausmeier et al., 2004; Arrigo, 2005). Klausmeier et al. (2004) and Arrigo (2005) defined two categories of phytoplankton: the bloomers, allocating more resources into the growth machinery such as ribosomal RNA (enriched in both N and P; “growth rate hypothesis”; optimal N:P = 8.2), and the survivalists, allocating more resources to acquisition machinery (light or nutrients) such as proteins and chlorophyll (enriched in N but not in P; optimal N:P = 45). Following this view, sea ice algae during the bloom period could allocate a significant share of resources into the growth machinery, accumulating P-rich biomass. Diatoms, often observed to dominate primary productivity in sea ice, are known to have low cell N:P, further accentuating this trend (Arrigo et al., 1999; Martiny et al., 2013). In a closed system, the ratio of DIN:PO43– would increase following assimilation and return to the initial DIN:PO43– ratio upon remineralization. A decrease in the DIN:PO43– ratio, as observed, would require removal of excess DIN from sea ice during the bloom, which can occur via exchange with seawater if the P-rich biomass is retained in the ice microstructure. Subsequent remineralization of the retained P-rich, diatom-dominated organic pool could then release sufficient PO43– to cause the observed decrease in the ratios of DIN:PO43– and Si(OH)4:PO43–. This effect could be further accentuated by the preferential assimilation of N accompanying the switch from bloomers (low N:P) to survivalists (high N:P) when conditions become less favorable for growth and light is decreasing (Klausmeier et al., 2004; Arrigo, 2005). This scenario is likely to occur at the bottom of ice floes, when continuous brine convection provides an efficient mechanism to fractionate P from N across the ice-seawater interface during the ice algal bloom. The observed higher accumulation of PO43– towards the ice-ocean interface appears consistent with this hypothesis (Figures 7b and 8c).
(ii) Preferential P remineralization. Organic matter is trapped in great quantities within sea ice for weeks to months and cold-adapted bacteria are known to thrive in this specific environment (Thomas et al., 1998, 2001; Hudson et al., 2000; Junge et al., 2004; Meiners et al., 2004; Deming, 2010; Bowman, 2015). An excess of phosphorus can also be explained by preferential remineralization of phosphorus with respect to N and Si. This process has already been suggested to occur in the ocean (Dugdale et al., 1995; Clark et al., 1998, 1999; Loh and Bauer, 2000; Paytan and McLaughlin, 2007; Letscher and Moore, 2015). The large organic pool within sea ice is mostly produced by the in situ microbial community and, at least initially, should represent relatively fresh material. Over time, the selective remineralization of organic P will decrease the DIN:PO43– and Si(OH)4:PO43– ratios in the brine.
(iii) Phosphate adsorption. As previously discussed in Section 3.4, phosphate adsorption, most probably onto metal-organic matter complexes (Yuan and Lavkulich, 1994; Zhou et al., 1997; Maranger and Pullin, 2003), could provide an alternative mechanism to a change in the metabolic stoichiometry (assimilation and remineralization) described above. Surface waters in the Southern Ocean are enriched in PO43– due to the upwelling of nutrient-rich Circumpolar Deep Water (Sarmiento et al., 2004). Over time, and additionally with brine convection, adsorption will result in accumulation of PO43– within sea ice, which will also be consistent with a higher accumulation of PO43– toward the ice-ocean interface (Figures 7b and 8c).
All three hypotheses, (i) to (iii), need further testing. Clearly, the phosphorus cycle in sea ice has been overlooked and is differently constrained from the one known to occur in the open ocean. Studies investigating the C:N:P stoichiometric composition of particulate and dissolved organic matter will be useful to elucidate the pathways described in the above hypotheses: low PON:POP will support the growth hypothesis (Klausmeier et al., 2004; Arrigo, 2005), while high DON:DOP will support the remineralization hypothesis (Letscher and Moore, 2015). PO43– adsorption will have no effect on either PON:POP or DON:DOP, but ligand formation with metal-organic complexes implies that adsorbed PO43– is not readily exchangeable and special care should be taken to desorb PO43– prior to organic matter analysis.
The current compilation of data on dissolved inorganic nitrogen, phosphate, and silicic acid concentrations from a large expanse of the ice pack of the Southern Ocean considerably improves our understanding of the overall nutrient dynamics in sea ice and has identified several overlooked aspects of it. Ice growth is accompanied by a net loss of nutrients from sea ice via desalination. During the first stages of sea ice growth, its bulk nutrient concentrations correlate the most with salinity, indicating that nutrients behave like the major dissolved sea salts. After incorporation, biologically-mediated nutrient consumption and production result in the decoupling of nutrient concentrations from salinity. Depending on the magnitude of primary production and exchange with seawater, nutrient assimilation into ice-trapped biomass generates an interior nutrient store in sea ice, which, upon remineralization, may serve to either counteract or overcome the loss of nutrients by desalination.
The salinity-normalized concentrations (C*) of DIN and Si(OH)4 in Antarctic pack ice follow the general trends expected for productive ecosystems. With increased insolation in spring–summer, NO3– and Si(OH)4 are partially assimilated into biomass and biogenic silica, respectively. Nitrate is more depleted than Si(OH)4 in comparison to seawater concentrations (Cw) and earlier in the growing season, suggesting a significant contribution of flagellates to sea ice primary production. Intermediate nutrients (NH4+ and NO2–) accumulate in sea ice (C* > Cw) to relatively invariable concentrations that indicate an overall balance between production and consumption processes. Following the decrease in solar radiation in late summer and the build-up of a large pool of ice-trapped organic matter during the preceding growing period, the DIN and Si(OH)4 concentrations (C*) increase (especially for NH4+) in sea ice likely due to an imbalance between nutrient production (light-independent or light-inhibited) and consumption (largely light-dependent) processes, and faster remineralization (dissolution for biogenic silica) rates in late summer. For both NO3– and Si(OH)4, we cannot rule out that an increase in the exchange with seawater in decaying sea ice may replenish these nutrients in the brine network. In contrast to the trends for both DIN and Si(OH)4, a large accumulation in sea ice is observed in spring–summer for PO43– (C* > Cw). The excess PO43– could be explained by a greater allocation to P-rich biomolecules during ice algal blooms coupled with removal of the residual excess DIN with brine convection, a preferential remineralization of phosphorus, and/or retention in sea ice via PO43– adsorption onto metal-organic complexes. Additional studies are needed to test these hypotheses and resolve previously overlooked aspects of the phosphorus cycle with respect to its speciation and abundance relative to N, C and Si.
We suggest that differences in nutrient concentrations obtained by the sackhole and bulk ice collection methods provide evidence for the adsorption of NH4+, and to a lesser extent, PO43– within sea ice. The involved mechanism has, as yet, unaccounted-for consequences for both nutrient mobility and availability in sea ice. A better understanding of the affinity of sea ice algae for nutrients is also required to decipher accurately which nutrients limit sea ice primary productivity and, therefore, affect the structure of the sympagic microbial community in both space and time.
The data are accessible in the supplementary Table S1.
The supplemental files for this article can be found as follows:
We thank the ship captains, crews, and our colleagues from many different countries who supported the sea ice sampling activities during the various field programs that contributed to this study. This compilation has been done in the framework of the Scientific Committee on Oceanic Research (SCOR) working group 140 on Biogeochemical Exchange Processes at Sea Ice Interfaces (BEPSII) and the Scientific Committee on Oceanic Research (SCAR) expert group on Antarctic Sea ice Processes and ClimaTe (ASPeCT). We thank BEPSII chairs Jacqueline Stefels and Nadja Steiner, as well as the ASPeCt chairs Stephen Ackley and Marilyn Raphael for their practical and moral support.
François Fripiat was a postdoctoral fellow at the FWO (Flanders Research Foundation, Belgium). Part of this work has been led under Belgian funding projects from BELSPO (SD/CA/05A), FNRS (2.4584.09 and 2.4517.11) and CFWB (ARC n°02/07-287). Stephen Ackley is grateful for support by the US National Science Foundation (Grant #1341717). David Thomas, Hilary Kennedy, and Stathys Papadimitriou are grateful for the support they received from NERC, The Royal Society, and The Leverhulme Trust. Klaus Meiners is grateful for support by the Australian Government through Australian Antarctic Science grants (#2767, #4073) and the Antarctic Climate and Ecosystems Cooperative Research Centre. Martin Vancoppenolle acknowledges support from BISICLO (FP7 CIG 321938).
The authors have no competing interests to declare.
Arrigo KR 2005. Marine microorganisms and global nutrient cycles. Nature 437: 349–355, DOI: http://dx.doi.org/10.1038/nature04158
Arrigo KR, Brown ZW and Mills MM 2014. Sea ice algal biomass and physiology in the Amundsen Sea, Antarctica. Elem Sci Anth 2: 000028.DOI: http://dx.doi.org/10.12952/journal.elementa.000028
Arrigo KR, Dieckmann G, Gosselin M, Robinson DH, Fritsen CH and Sullivan CW 1995. High resolution study of the platelet ice ecosystem in McMurdo Sound, Antarctica: biomass, nutrient, and production profiles within a dense microalgal bloom. Mar Ecol Prog Ser 127: 255–268, DOI: http://dx.doi.org/10.3354/meps127255
Arrigo KR, Robinson DH, Dunbar RB, Leventer AR and Lizotte MP 2003. Physical control of chlorophyll a, POC, and TPN distributions in the pack ice of the Ross Sea, Antarctica. J Geophys Res 108(C10): 3316.DOI: http://dx.doi.org/10.1029/2001JC001138
Arrigo KR Robinson DH Worthen DL Dunbar RB DiTullio GR et al. 1999. Phytoplankton community structure and the drawdown of nutrients and CO2 in the Southern Ocean. Science 283: 365–367, DOI: http://dx.doi.org/10.1126/science.283.5400.365
Arrigo KR and Sullivan SW 1992. Salinity and temperature covariation on the photophysiological characteristics of Antarctic sea ice microalgae. J Phycol 28: 746–756, DOI: http://dx.doi.org/10.1111/j.0022-3646.1992.00746.x
Arrigo KR and Thomas DN 2004. Large scale importance of sea ice biology in the Southern Ocean. Antarct Sci 16(4): 471–486, DOI: http://dx.doi.org/10.1017/S0954102004002263
Aslam M, Huffaker RC and Rains DW 1984. Early effects of salinity on nitrate assimilation in barley seedlings. Plant Physiol 76: 321–325, DOI: http://dx.doi.org/10.1104/pp.76.2.321
Baer SE, Connelly TL and Bronk DA 2015. Nitrogen uptake dynamics in landfast sea ice of the Chukchi Sea. Polar Biol 38: 781–797, DOI: http://dx.doi.org/10.1007/s00300-014-1639-y
Becquevort S Dumont I Tison JL Lannuzel D Sauvée ML et al. 2009. Biogeochemistry and microbial community composition in sea ice and underlying seawater off East Antarctica during early spring. Polar Biol 32: 879–895, DOI: http://dx.doi.org/10.1007/s00300-009-0589-2
Bidle KD and Azam F 1999. Accelerated dissolution of diatom silica by marine bacterial assemblages. Nature 397: 508–512, DOI: http://dx.doi.org/10.1038/17351
Blackburn TH and Henriksen K 1983. Nitrogen cycling in different types of sediments from Danish waters. Limnol Oceanogr 28(3): 477–493, DOI: http://dx.doi.org/10.4319/lo.1983.28.3.0477
Boetius A Albrecht S Bakker K Bienhold C Felden J et al. 2013. Export of algal biomass from the melting Arctic sea ice. Science 339: 1430–1432, DOI: http://dx.doi.org/10.1126/science.1231346
Bowman JS 2015. The relationship between sea ice bacterial community structure and biogeochemistry: A synthesis of current knowledge and known unknowns. Elem Sci Anth 3: 000072.DOI: http://dx.doi.org/10.12952/journal.elementa.000072
Brzezinski MA 1985. The Si:C:N ratios of marine diatoms: interspecific variability and the effect of some environmental variables. J Phycol 21: 345–357, DOI: http://dx.doi.org/10.1111/j.0022-3646.1985.00347.x
Claquin P, Martin-Jézéquel V, Kromkamp JC, Veldhuis MJW and Kraay GW 2002. Uncoupling of silicon compared with carbon and nitrogen metabolisms and the role of the cell cycle in continuous cultures of Thalassiosira Pseudonana (Bacillariophyceae) under light, nitrogen, and phosphorus control. J Phycol 38: 922–930, DOI: http://dx.doi.org/10.1046/j.1529-8817.2002.t01-1-01220.x
Clarke DB and Ackley SF 1984. Sea ice structure and biological activity in the Antarctic marginal ice zone. J Geophys Res 89(C2): 2087–2095, DOI: http://dx.doi.org/10.1029/JC089iC02p02087
Clark LL, Ingall ED and Benner R 1998. Marine phosphorus is selectively remineralized. Nature 493: 426.DOI: http://dx.doi.org/10.1038/30881
Clark LL, Ingall ED and Benner R 1999. Marine organic phosphorus cycling: novel insights from nuclear magnetic resonance. Am J Sci 299(9): 724–737, DOI: http://dx.doi.org/10.2475/ajs.299.7-9.724
Cox GFN and Weeks WF 1983. Equations for determining the gas and brine volumes in sea-ice samples. J Glaciol 29(102): 306–316, DOI: http://dx.doi.org/10.1017/S0022143000008364
Cozzi S 2008. High-resolution trends of nutrients, DOM and nitrogen uptake in the annual sea ice at Terra Nova Bay, Ross Sea. Antarct Sci 20(5): 441–454, DOI: http://dx.doi.org/10.1017/S0954102008001247
Delille D, Fiala M, Kuparinen J, Kuosa H and Plessis C 2002. Seasonal changes in microbial biomass in the first-year ice of the Terre Adélie area (Antarctica). Aquat Microb Ecol 28: 257–265, DOI: http://dx.doi.org/10.3354/ame028257
Dieckmann GS, Lange MA, Ackley SF and Jemmings JC Jr. 1991. The nutrient status in sea ice of the Weddell Sea during winter: effects of sea ice texture and algae. Polar Biol 11: 449–456, DOI: http://dx.doi.org/10.1007/BF00233080
Dieckmann GS Nehrke G Papadimitriou S Göttlicher J Steininger R et al. 2008. Calcium carbonate as ikaite crystals in Antarctic sea ice. Geophys Res Let 35(L08): 501.DOI: http://dx.doi.org/10.1029/2008GL033540
Dore JE, Houlihan T, Hebel DV, Tien G, Tupas L and Karl DM 1996. Freezing as a method of sample preservation for the analysis of dissolved inorganic nutrient in seawater. Mar Chem 53: 173–185, DOI: http://dx.doi.org/10.1016/0304-4203(96)00004-7
Dortch Q, Clayton JR Jr., Thoresen SS and Ahmed SI 1984. Species differences in accumulation of nitrogen pools in phytoplankton. Mar Biol 81: 237–250, DOI: http://dx.doi.org/10.1007/BF00393218
Dugdale RC, Wilkerson FP and Minas HJ 1995. The role of a silicate pump in driving new production. Deep-Sea Res Part I 42(5): 697–719, DOI: http://dx.doi.org/10.1016/0967-0637(95)00015-X
Dumont I, Schoemann V, Lannuzel D, Chou L, Tison JL and Becquevort S 2009. Distribution and characterization of dissolved and particulate organic matter in Antarctic pack ice. Polar Biol 32: 733–750, DOI: http://dx.doi.org/10.1007/s00300-008-0577-y
Eicken H 1992. Salinity profiles of Antarctic sea ice: Field data and model results. J Geophys Res 97(C10): 15545–15557, DOI: http://dx.doi.org/10.1029/92JC01588
Eicken H, Lange MA and Dieckmann GS 1991. Spatial variability of sea-ice properties in the Northwestern Weddell Sea. J Geophys Res 96(C6): 10603–10615, DOI: http://dx.doi.org/10.1029/91JC00456
Eppley RW, Rogers JN and McCarthy JJ 1969. Half-saturation constants for uptake of nitrate and ammonium by marine phytoplankton. Limnol Oceanogr 14: 912–919, DOI: http://dx.doi.org/10.4319/lo.1969.14.6.0912
Ewert M, Carpenter SD, Colangelo-Lillis J and Deming JW 2013. Bacterial and extracellular polysaccharide content of brine-wetted snow over Arctic winter first-year sea ice. J Geophys Res 118(2): 726–735, DOI: http://dx.doi.org/10.1002/jgrc.20055
Fawcett SE, Lomas MW, Ward BB and Sigman DM 2014. The counterintuitive effect of summer-to-fall mixed layer deepening on eukaryotic new production in the Sargasso Sea. Global Biogeochem Cy 28: 86–102, DOI: http://dx.doi.org/10.1002/2013GB004579
Firth E, Carpenter SD, Sørensen HL, Collins RE and Deming JW 2016. Bacterial use of choline to tolerate salinity shifts in sea-ice brines. Elem Sci Anth 4(1): 000120.DOI: http://dx.doi.org/10.12952/journal.elementa.000120
Fransson A, Chierici M, Miller LA, Carnat G, Thomas H, Shadwick E, Pineault S and Papakyriakou TM 2013. Impact of sea ice processes on the carbonate system and ocean acidification state at the ice-water interface of the Amundsen Gulf, Arctic Ocean. J Geophys Res 118: 1–23, DOI: http://dx.doi.org/10.1002/2013JC009164
Fransson A, Chierici M, Yager P and Smith WO 2011. Antarctic sea ice carbon dioxide system and controls. J Geophys Res 116(C12): 035.DOI: http://dx.doi.org/10.1029/2010JC006844
Fripiat F, Cardinal D, Tison JL, Worby A and André L 2007. Diatoms-induced Si-isotopic fractionation in Antarctic sea-ice. J Geophys Res 112(G02): 001.DOI: http://dx.doi.org/10.1029/2006JG000244
Fripiat F, Sigman DM, Fawcett SE, Rafter PA, Weigand MA and Tison JL 2014a. New insights into sea ice nitrogen biogeochemical dynamics from the nitrogen isotopes. Global Biogeochem Cy 28DOI: http://dx.doi.org/10.1002/2013GB004729
Fripiat F, Sigman DM, Massé G and Tison JL 2015. High turnover rates indicated by changes in the fixed N forms and their stable isotopes in Antarctic landfast sea ice. J Geophys Res 120DOI: http://dx.doi.org/10.1002/2014JC010583
Fripiat F, Tison JL, André L, Notz D and Delille B 2014b. Biogenic silica recycling in sea ice inferred from Si-isotopes : constraints from Arctic winter first-year sea ice. Biogeochem 119: 25–33, DOI: http://dx.doi.org/10.1007/s10533-013-9911-8
Fritsen CH, Lytle VI, Ackley SF and Sullivan CW 1994. Autumn bloom of Antarctic pack-ice algae. Science 266: 782–784, DOI: http://dx.doi.org/10.1126/science.266.5186.782
Garcia HER Locarnini L Boyer TP Antonov JI Baranova OK et al. 2014. Levitus, S, Mishonov, A and Technical Dissolved Inorganic Nutrients (phosphate, nitrate, silicate). World Ocean Atlas 2013, NOAA Atlas NESDIS 76. 4
Garrison DL and Buck KR 1986. Organism losses during ice melting: a serious bias in sea ice community studies. Polar Biol 6: 237–239, DOI: http://dx.doi.org/10.1007/BF00443401
Garrison DL and Buck KR 1989. The biota of Antarctic pack ice in the Weddell Sea and Antarctic Peninsula Regions. Polar Biol 10: 211–219, DOI: http://dx.doi.org/10.1007/BF00238497
Garrison DL and Close AR 1993. Winter ecology of the sea ice biota in Weddell Sea pack ice. Mar Ecol Prog Ser 96: 17–31, DOI: http://dx.doi.org/10.3354/meps096017
Geider RJ and La Roche J 2002. Redfield revisited: variability of C:N:P in marine microalgae and its biochemical basis. Eur J Phycol 37: 1–17, DOI: http://dx.doi.org/10.1017/S0967026201003456
Gleitz M, Loeff MRvd, Thomas DN, Dieckmann GS and Millero FJ 1995. Comparison of summer and winter inorganic carbon, oxygen, and nutrient concentrations in Antarctic sea ice brine. Mar Chem 51: 81–91, DOI: http://dx.doi.org/10.1016/0304-4203(95)00053-T
Gleitz M and Thomas DN 1993. Variation in phytoplankton standing stock, chemical composition and physiology during sea-ice formation in the southeastern Weddel Sea, Antarctica. J Exp Mar Biol Ecol 173: 211–230, DOI: http://dx.doi.org/10.1016/0022-0981(93)90054-R
Gosselin M, Legendre L, Therriault JC and Demers S 1990. Light and nutrient limitation of sea ice microalgae (Hudson Bay, Canadian Arctic). J Phycol 26: 220–232, DOI: http://dx.doi.org/10.1111/j.0022-3646.1990.00220.x
Griewank PJ and Notz D 2013. Insights into brine dynamics and sea ice desalination from a 1-D model study of gravity drainage. J Geophys Res 118: 1–17, DOI: http://dx.doi.org/10.1002/jgrc.20247
Günther S and Dieckmann GS 1999. Seasonal development of algal biomass in snow-covered fast ice and the underlying platelet layer in the Weddell Sea, Antarctica. Antarct Sci 11(3): 305–315, DOI: http://dx.doi.org/10.1017/S0954102099000395
Haas C, Thomas DN and Bareiss J 2001. Surface properties and processes of perennial Antarctic sea ice in summer. J Glaciol 47(159): 613–625, DOI: http://dx.doi.org/10.3189/172756501781831864
Hagopian DS and Riley JG 1998. A closer look at the bacteriology of nitrification. Aquac Eng 18: 223–244, DOI: http://dx.doi.org/10.1016/S0144-8609(98)00032-6
Holmes RM, Aminot A, Kerouel R, Hooker BA and Peterson BJ 1999. A simple and precise method for measuring ammonium in marine and freshwater ecosystems. Can J Fish Aquat Sci 56: 1801–1808, DOI: http://dx.doi.org/10.1139/f99-128
Hudson AL, Krieger-Brockett BB and Deming JW 2000. Remarkably low temperature optima for extracellular enzyme activity from Arctic bacteria and sea ice. Environ Microbiol 2: 383–388, DOI: http://dx.doi.org/10.1046/j.1462-2920.2000.00118.x
Hutchins DA and Bruland KW 1998. Iron-limited diatom growth and Si:N uptake ratios in a coastal upwelling regime. Nature 393: 561–564, DOI: http://dx.doi.org/10.1038/31203
Hu YB, Dieckmann GS, Wolf-Gladrow DA and Nehrke G 2014. Laboratory study on coprecipitation of phosphate with ikaite in sea ice. J Geophys Res 119: 7007–7015, DOI: http://dx.doi.org/10.1002/2014JC010079
Hydes DJ Aoyama M Aminot A Bakker K Becker S et al. 2010. Determination of dissolved nutrients (N, P, Si) in seawater with high precision and inter-comparability using gas-segmented continuous flow analysers. The GO-SHIP Repeat Hydrography Manual: A collection of Expert Reports and Guidelines.
Jardon FP, Vivier F, Vancoppenolle M, Lourenço A, Bouruet-Aubertot P and Cuypers Y 2013. Full-depth desalination of warm sea ice. J Geophys Res 118: 1–13, DOI: http://dx.doi.org/10.1029/2012JC007962
Jeffries MO, Krouse HR, Hurst-Cushing B and Maksym T 2001. Snow-ice accretion and snowcover depletion on Antarctic first-year sea ice floes. An Glaciol 33: 51–60, DOI: http://dx.doi.org/10.3189/172756401781818266
Jeffries MO, Worby AP, Morris K and Weeks WF 1997. Seasonal variations in the properties and structural composition of sea ice and snow cover in the Bellingshausen and Amundsen Seas, Antarctica. J Glaciol 43(143): 138–151, DOI: http://dx.doi.org/10.1017/S0022143000002902
Junge K, Eicken H and Deming JW 2004. Bacterial activity at –2 to –20°C in Arctic wintertime sea ice. Appl Environ Microbiol 70(1): 550–557, DOI: http://dx.doi.org/10.1128/AEM.70.1.550-557
Kamp A, Hogslund S, Risgaard-Petersen N and Stiel P 2015. Nitrate storage and dissimilatory nitrate reduction by eukaryotic microbes. Front Microbiol 6(1499)DOI: http://dx.doi.org/10.3389/fmicb.2015.01492
Kattner G 1999. Storage of dissolved inorganic nutrients in seawater: poisoning with mercuric chloride. Mar Chem 67: 61–66, DOI: http://dx.doi.org/10.1016/S0304-4203(99)00049-3
Kattner G, Thomas DN, Haas C, Kennedy H and Dieckmann GS 2004. Surface ice and gap layers in Antarctic sea ice: highly productive habitats. Mar Ecol Prog Ser 277: 1–12, DOI: http://dx.doi.org/10.3354/meps277001
Kennedy H, Thomas DN, Kattner G, Haas C and Dieckmann GS 2002. Particulate organic matter in Antarctic summer sea ice: concentration and stable isotopic composition. Mar Ecol Prog Ser 238: 1–13, DOI: http://dx.doi.org/10.3354/meps238001
Klausmeier CA, Litchman E, Daufresne T and Levin SA 2004. Optimal nitrogen-to-phosphorus stoichiometry of phytoplankton. Nature 429: 171–174, DOI: http://dx.doi.org/10.1038/nature02454
Kurniawan A, Yamatoto T, Tsuchiya Y and Morisaki H 2012. Analysis of the ion adsorption-desorption characteristics of biofilm matrices. Microbes Environ 27(4): 399–406, DOI: http://dx.doi.org/10.1264/jsme.2.ME11339
Lannuzel D, Bowie AR, van der Merwe PC, Townsend AT and Schoemann V 2011. Distribution of dissolved and particulate metals in Antarctic sea ice. Mar Chem 124: 134–146, DOI: http://dx.doi.org/10.1016/j.marchem.2011.01.004
Lannuzel D Chever F van der Merwe PC Janssens J Roukaerts A et al. 2016. Iron biogeochemistry in Antarctic pack ice during SIPEX-2. Deep-Sea Res Part II 131: 11–122, DOI: http://dx.doi.org/10.1016/j.dsr2.2014.12.003
Lannuzel D Vancoppenolle M van der Merwe P de Jong J Meiners KM et al. 2016. Iron in sea ice: review and new insights. Elem Sci Anth 4: 000130.DOI: http://dx.doi.org/10.12952/journal.elementa000130
Legendre L Ackley SF Dieckmann GS Gulliksen G Horner R et al. 1992. Ecology of sea ice biota, 2. Global significance. Polar Biol 12: 429–444, DOI: http://dx.doi.org/10.1007/BF00243114
Letscher RT and Moore JK 2015. Preferential remineralization of dissolved organic phosphorus and non-Redfield DOM dynamics in the global ocean: Impacts on marine productivity, nitrogen fixation, and carbon export. Global Biogeochem Cy 29: 325–340, DOI: http://dx.doi.org/10.1002/2014GB004904
Lieser JL Curran MAJ Bowie AR Davidson AT Doust SJ et al. 2015. Antarctic slush-ice algal accumulation not quantified through conventional satellite imagery: Beware the ice of March. The Cryosphere Discussion 9: 6187–6222, DOI: http://dx.doi.org/10.5194/tcd-9-6187-2015
Loh AN and Bauer JE 2000. Distribution, portioning and fluxes of dissolved and particulate organic C, N, and P in the eastern North Pacific and Southern Oceans. Deep-Sea Res Part I 47: 2287–2316, DOI: http://dx.doi.org/10.1016/S0967-0637(00)00027-3
Lomas MW and Glibert PM 2000. Comparisons of nitrate uptake, storage, and reduction in marine diatoms and flagellates. J Phycol 36: 903–913, DOI: http://dx.doi.org/10.1046/j.1529-8817.2000.99029.x
Maksym T and Markus T 2008. Antarctic sea ice thickness and snow-to-ice conversion from atmospheric reanalysis and passive microwave snow depth. J Geophys Res 113(C02): S12.DOI: http://dx.doi.org/10.1029/2006JC004085
Maranger R and Pullin MJ 2003. Elemental complexation by dissolved organic matter in lakes: Implications for Fe speciation and the bioavailability of Fe and P In: Findlay, SEG and Sinsabaugh, RL eds. Aquatic Ecosystems: Interactivity of dissolved organic matter. New York, USA: Elsevier, DOI: http://dx.doi.org/10.1016/B978-012256371-3/50009-3
Martin JH, Gordon RM and Fitzwater SE 1990. Iron in Antarctic waters. Nature 345: 156–158, DOI: http://dx.doi.org/10.1038/345156a0
Martiny AC Pham CTA Primeau FW Vrugt JA Moore JK et al. 2013. Strong latitudinal patterns in the elemental rations of marine plankton and organic matter. Nat Geosci 6: 279–283, DOI: http://dx.doi.org/10.1038/ngeo1757
Meiners KM, Brinkmeyer R, Granskog MA and Lindfors A 2004. Abundance, size distribution and bacterial colonization of exopolymer particles in Antarctic sea ice (Bellingshausen Sea). Aquat Microb Ecol 35: 283–296, DOI: http://dx.doi.org/10.3354/ame035283
Meiners KM Golden KM Heil P Lieser JL Massom R et al. 2016. Introduction: SIPEX-2: A study of sea-ice physical, biogeochemical and ecosystem processes off East Antarctica during spring 2012. Deep-Sea Res Part II 131: 1–6, DOI: http://dx.doi.org/10.1016/j.dsr2.2016.06.010
Meiners KM, Norman L, Granskog MA, Krell A, Heil P and Thomas DN 2011. Physico-ecobiogeochemistry of East Antarctic pack ice during the winter-spring transition. Deep-Sea Res Part II 58: 1172–1181, DOI: http://dx.doi.org/10.1016/j.dsr2.2010.10.033
Meiners KM Vancoppenolle M Thanassekos S Dieckmann GS Thomas DN et al. 2012. Chlorophyll a in Antarctic sea ice from historical ice core data. Geophys Res Let 39(L21): 602.DOI: http://dx.doi.org/10.1029/2012GL053478
Michelsen DM and Witkowski A 2010. Melting sea ice for taxonomic analysis: a comparison of four melting procedures. Polar Res 29: 451–454, DOI: http://dx.doi.org/10.3402/polar.v29i3.6088
Miller LA Fripiat F Else BGT Bowman JS Brown KA et al. 2015. Methods for biogeochemical studies of sea ice: the state of the arts, caveats, and recommendations. Elem Sci Anth 3: 000038.DOI: http://dx.doi.org/10.12952/journal.elementa.000038
Mitchell BG, Brody EA, Holm-Hansen O, McClain C and Bishop J 1991. Light limitation of phytoplankton biomass and macronutrient utilization in the Southern Ocean. Limnol Oceanogr 36(8): 1662–1677, DOI: http://dx.doi.org/10.4319/lo.1918.104.22.1682
Moore CM Mills MM Arrigo KR Berman-Frank I Bopp L et al. 2013. Processes and patterns of oceanic nutrient limitation. Nat Geosci 6: 701–710, DOI: http://dx.doi.org/10.1038/ngeo1765
Moreau S Vancoppenolle M Delille B Tison JL Zhou J et al. 2015. Drivers of inorganic carbon dynamics in first-year sea ice: a model study. J Geophys Res 120: 471–495, DOI: http://dx.doi.org/10.1002/2014JC010388
Munro DR, Dunbar RB, Mucciarone DA, Arrigo KR and Long MC 2010. Stable isotope composition of dissolved inorganic carbon and particulate organic carbon in sea ice from the Ross Sea, Antarctica. J Geophys Res 115(C09): 0005.DOI: http://dx.doi.org/10.1029/2009JC005661
Nedwell DB 1999. Effect of low temperature on microbial growth: lowered affinity for substrates limits growth at low temperature. FEMS Microbiol Ecol 30: 101–111, DOI: http://dx.doi.org/10.1111/j.1574-6941.1999.tb00639.x
Nelson DM, Ahern JA and Herlihy LJ 1991. Cycling of biogenic silica within the upper water column of the Ross Sea. Mar Chem 35: 461–476, DOI: http://dx.doi.org/10.1016/S0304-4203(09)90037-8
Nelson DM, Brzezinski MA, Sigmon DE and Franck VM 2001. A seasonal progression of Si limitation in the Pacific sector of the Southern Ocean. Deep-Sea Res Part II 48: 3973–3995, DOI: http://dx.doi.org/10.1016/S0967-0645(01)00076-5
Notz D and Worster MG 2009. Desalination processes of sea ice revisited. J Geophys Res 114(C05): 006.DOI: http://dx.doi.org/10.1029/2008JC004885
Orsi AH, Whitworth T III and Nowlin WD Jr. 1995. On the meridional extent and fronts of the Antarctic Circumpolar Current. Deep-Sea Res Part I 42(5): 641–673, DOI: http://dx.doi.org/10.1016/0967-0637(95)00021-W
Papadimitriou S, Kennedy H, Kennedy DP and Thomas DN 2013. Ikaite solubility in seawater-derived brines at 1 atm and sub-zero temperatures to 265 K. Geochim Cosmochim Acta 109: 241–253, DOI: http://dx.doi.org/10.1016/j.gca.2013.01.044
Papadimitriou S Thomas DN Kennedy H Haas C Kuosa H et al. 2007. Biogeochemical composition of natural sea ice brines from the Weddell Sea during early austral summer. Limnol Oceanogr 52(5): 1809–1823, DOI: http://dx.doi.org/10.4319/lo.2007.52.5.1809
Papadimitriou S, Thomas DN, Kennedy H, Kuosa H and Dieckmann GS 2009. Inorganic carbon removal and isotopic enrichment in Antarctic sea ice gap layers during early austral summer. Mar Ecol Prog Ser 386: 15–27, DOI: http://dx.doi.org/10.3354/meps08049
Parkinson CL and Cavalieri DJ 2012. Antarctic sea ice variability and trends, 1979–2010. The Cryosphere 6: 871–880, DOI: http://dx.doi.org/10.5194/tc-6-871-2012
Paytan A and McLaughlin K 2007. The Oceanic phosphorus cycle. Chem Rev 107(2): 563–576, DOI: http://dx.doi.org/10.1021/cr0503613
Priscu JC, Downes MT, Priscu LR, Palmisano AC and Sullivan CW 1990. Dynamics of ammonium oxidizer activity and nitrous oxide (N2O) within and beneath Antarctic sea ice. Mar Ecol Prog Ser 62: 37–46, DOI: http://dx.doi.org/10.3354/meps062037
Raymond B 2014. The maximum extent of sea ice in the southern hemisphere by day and winter season. Australian Antarctic Data Center – CAASM Metadata. (http://data.aad.gov.au/aadc/metadata/metadata_redirect.cfm?md=/AMD/AU/sea_ice_extent_winter).
Reay DS, Nedwell DB, Priddle J and Ellis-Evans JC 1999. Temperature dependence of inorganic nitrogen uptake: reduced affinity for nitrate at suboptimal temperatures in both algae and bacteria. Appl Environ Microbiol 65(6): 2577–2584.
Rees-Jones DW and Worster MG 2013. A simple dynamical model for gravity drainage of brine from growing sea ice. Geophys Res Let 40: 307–311, DOI: http://dx.doi.org/10.1029/2012GL054301
Riebesell U, Schloss I and Smetacek V 1991. Aggregation of algae released from melting sea ice: implications for seeding and sedimentation. Polar Biol 11: 239–248, DOI: http://dx.doi.org/10.1007/BF00238457
Rintala JM Piiparinen J Blomster J Majaneva M Müller S et al. 2014. Fast direct melting of brackish sea-ice samples results in biologically more accurate results than slow buffered melting. Polar Biol 37: 1811–1822, DOI: http://dx.doi.org/10.1007/s00300-014-1563-1
Rintoul SR Balmeseda M Cunningham S Dushaw BD Garzoli S et al. 2009. Deep circulation and meridional overturning: Recent progress and a strategy for sustained observations. Proceeding of OceanObs’09: Sustained Ocean Observations and Information for Society, DOI: http://dx.doi.org/10.5270/OceanObs09
Roukaerts A, Cavagna AJ, Fripiat F, Lannuzel D, Meiners KM and Dehairs F 2016. Sea-ice algal primary production and nitrogen uptake rates off East Antarctica. Deep-Sea Res Part II 131: 140–149, DOI: http://dx.doi.org/10.1016/j.dsr2.2015.08.007
Rysgaard S and Glud RN 2004. Anaerobic N2 production in Arctic sea ice. Limnol Oceanogr 49(1): 86–94, DOI: http://dx.doi.org/10.4319/lo.2004.49.1.0086
Rysgaard S, Glud RN, Sejr MK, Blicher ME and Stahl HJ 2008. Denitrification activity and oxygen dynamic in Arctic sea ice. Polar Biol 31: 527–537, DOI: http://dx.doi.org/10.1007/s00300-007-0384-x
Rysgaard S, Kühl M, Glud RN and Hansen JW 2001. Biomass production and horizontal patchiness of sea ice algae in a High-Arctic fjord (Young Sound, NE Greenland). Mar Ecol Prog Ser 223: 15–26, DOI: http://dx.doi.org/10.3354/meps223015
Rysgaard S Wang F Galley RJ Grimm R Notz D et al. 2014. Temporal dynamics of ikaite in experimental sea ice. The cryosphere 8: 1469–1478, DOI: http://dx.doi.org/10.5194/tc-8-1469-2014
Saenz B and Arrigo KR 2014. Annual primary production in Antarctic sea ice during 2005-2006 from a sea ice state estimate. J Geophys Res 119: 3645–3678, DOI: http://dx.doi.org/10.1002/2013JC009677
Saito MA, McIlvin MR, Moran DM, Goepfert TJ, DiTullio GR, Post AF and Lamborg CH 2014. Multiple nutrient stresses at intersecting Pacific Ocean biomes detected by protein biomarkers. Science 345: 1173–1177, DOI: http://dx.doi.org/10.1126/science.1256450
Sarmiento JL, Gruber N, Brzezinski MA and Dunne JP 2004. High-latitude controls of thermocline nutrients and low latitude biological productivity. Nature 427: 56–60, DOI: http://dx.doi.org/10.1038/nature02127
Sarthou G, Timmermans KR, Blain S and Tréguer P 2005. Growth physiology and fate of diatom in the ocean: a review. J Sea Res 53: 25–42, DOI: http://dx.doi.org/10.1016/j.seares.2004.01.007
Seitzinger SP, Gardner WS and Spratt AK 1991. The effect of salinity on ammonium sorption in aquatic sediments: implications for benthic nutrient recycling. Estuaries 14(2): 167–174, DOI: http://dx.doi.org/10.2307/1351690
Sjöberg S, Nordin A and Ingri N 1981. Equilibrium and structural studies of silicon (IV) and Aluminium (III) in aqueous solution: Formation constants for the monosilicate ions SiO(OH)3– and SiO2(OH)22–, a precision study at 25°C in a simplified seawater medium. Mar Chem 10: 521–532, DOI: http://dx.doi.org/10.1016/0304-4203(81)90005-0
Smith REH, Harrison WG, Harris LR and Herman AW 1990. Vertical fine structure of particulate matter and nutrients in sea ice of the high Arctic. Can J Fish Aquat Sci 47: 1348–1355, DOI: http://dx.doi.org/10.1139/f90-154
Smith WO and Nelson DM 1985. Phytoplankton bloom produced by a receding ice edge in the Ross Sea: Spatial coherence with the density field. Science 227: 163–166, DOI: http://dx.doi.org/10.1126/science.227.4683.163
Sollins P, Robertson GP and Uehara G 1988. Nutrient mobility in variable- and permanent-charge soils. Biogeochem 6: 181–199, DOI: http://dx.doi.org/10.1007/BF02182995
Speer K, Rintoul SR and Sloyan B 2000. The diabatic Deacon cell. J Phys Oceanogr 30: 3212–3222, DOI: http://dx.doi.org/10.1175/1520-0485(2000)030<3212:TDDC>2.0.CO;2
Steiner N Deal C Lannuzel D Lavoie D Massonet F et al. 2016. What sea-ice biogeochemical modelers need for observers. Elem Sci Anth 4: 000084.DOI: http://dx.doi.org/10.12952/journal.elementa.000084
Takeda S 1998. Influence of iron availability on nutrient consumption ratio of diatoms in oceanic waters. Nature 393: 774–777, DOI: http://dx.doi.org/10.1038/31674
Thomas DN Kattner G Engbrodt R Giannelli V Kennedy H et al. 2001. Dissolved organic matter in Antarctic sea ice. An Glaciol 33: 297–303, DOI: http://dx.doi.org/10.3189/172756401781818338
Thomas DN Lara RJ Haas C Schnack-Schiel SB Dieckmann GS et al. 1998. Biological soup within decaying summer sea ice in the Amundsen Sea, Antarctica. Antarctic sea ice biological processes, interactions and variability. Antarctic Research Series 73: 161–171, DOI: http://dx.doi.org/10.1029/AR073p0161
Timmermans KR, van der Wagt B, Veldhuis MJW, Maatman A and de Baar HJW 2005. Physiological responses of three species of marine pico-phytoplankton to ammonium, phosphate, iron and light limitation. J Sea Res 53: 109–120, DOI: http://dx.doi.org/10.1016/j.seares.2004.05.003
Tison JL Worby A Delille B Brabant F Papadimitriou S et al. 2008. Temporal evolution of decaying summer first-year sea ice in the Western Weddell Sea, Antarctica. Deep-Sea Res Part II 55: 975–987, DOI: http://dx.doi.org/10.1016/j.dsr2.2007.12.021
Torstensson A, Dinasquet J, Chierici M, Fransson A, Riemann L and Wulff A 2015. Physicochemical control of bacterial and protist community composition and diversity in Antarctic sea ice. Environ Microb 17(10): 3869–81, DOI: http://dx.doi.org/10.1111/1462-2920.12865
Tréguer PJ and De La Rocha CL 2013. The World Ocean silica cycle. Annu Rev Mar Sci 5: 477–501, DOI: http://dx.doi.org/10.1146/annurev-marine-121211-172346
Trevena AJ, Jones GB, Wright SW and van den Enden RL 2000. Profiles of DMSP, algal pigments, nutrients and salinity in pack ice from eastern Antarctica. J Sea Res 43: 265–273, DOI: http://dx.doi.org/10.1016/S1385-1101(00)00012-5
Underwood GJC Aslam S Michel C Niemi A Norman L et al. 2013. Broad-scale predictability of carbohydrates and exopolymer in Antarctic and Arctic sea ice. Proc Natl Acad USA 110: 15734–15739, DOI: http://dx.doi.org/10.1073/pnas.1302870110
Vancoppenolle M Meiners KM Michel C Bopp L Brabant F et al. 2013. Role of sea ice in global biogeochemical cycles : emerging views and challenges. Quat Sci Rev 79: 207–230, DOI: http://dx.doi.org/10.1016/j.quascirev.2013.04.011
Wells AJ, Wettlaufer JS and Orzag SA 2011. Brine fluxes from growing sea ice. Geophys Res Let 38(L04): 501.DOI: http://dx.doi.org/10.1029/2010GL046288
Williams G Maksym T Wilkinson J Kunz C Murphy C et al. 2015. Thick and deformed Antarctic sea ice mapped with autonomous underwater vehicles. Nature Geoscience 8: 61–67, DOI: http://dx.doi.org/10.1038/ngeo2299
Worby AP, Geiger CA, Paget MJ, Van Woert ML, Ackley SF and DeLiberty T 2008. Thickness distribution of Antarctic sea ice. J Geophys Res 113(C05): S92.DOI: http://dx.doi.org/10.1029/2007JC004254
Wurl O 2009. Practical guidelines for the analysis of seawater In: USA: CRC press, DOI: http://dx.doi.org/10.1201/9781420073072
Yuan G and Lavkulich LM 1994. Phosphate sorption in relation to extractable iron and aluminium in spodosols. SSSAJ 2(58): 343–346, DOI: http://dx.doi.org/10.2136/sssaj1994.03615995005800020013x
Zhou M, Rhue RD and Harris WG 1997. Phosphorus sorption characteristics of Bh and Bt horizons from sandy coastal plain soils. SSSAJ 61(5): 1364–1369, DOI: http://dx.doi.org/10.2136/sssaj1997.03615995006100050011x