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The eruptions of Eyjafjallajökull (2010) and Grímsvötn (2011), Iceland, triggered immediate, international consideration of the respiratory health hazard of inhaling volcanic ash, and prompted the need to estimate the potential hazard posed by future eruptions of Iceland’s volcanoes to Icelandic and Northern European populations.
A physicochemical characterization and toxicological assessment was conducted on a suite of archived ash samples spanning the spectrum of past eruptions (basaltic to rhyolitic magmatic composition) of Icelandic volcanoes following a protocol specifically designed by the International Volcanic Health Hazard Network.
Icelandic ash can be of a respirable size (up to 11.3 vol.% < 4 μm), but the samples did not display physicochemical characteristics of pathogenic particulate in terms of composition or morphology. Ash particles were generally angular, being composed of fragmented glass and crystals. Few fiber-like particles were observed, but those present comprised glass or sodium oxides, and are not related to pathogenic natural fibers, like asbestos or fibrous zeolites, thereby limiting concern of associated respiratory diseases. None of the samples contained cristobalite or tridymite, and only one sample contained quartz, minerals of interest due to the potential to cause silicosis. Sample surface areas are low, ranging from 0.4 to 1.6 m2 g−1, which aligns with analyses on ash from other eruptions worldwide. All samples generated a low level of hydroxyl radicals (HO•), a measure of surface reactivity, through the iron-catalyzed Fenton reaction compared to concurrently analyzed comparative samples. However, radical generation increased after ‘refreshing’ sample surfaces, indicating that newly erupted samples may display higher reactivity. A composition-dependent range of available surface iron was measured after a 7-day incubation, from 22.5 to 315.7 μmol m−2, with mafic samples releasing more iron than silicic samples. All samples were non-reactive in a test of red blood cell-membrane damage.
The primary particle-specific concern is the potential for future eruptions of Iceland’s volcanoes to generate fine, respirable material and, thus, to increase ambient PM concentrations. This particularly applies to highly explosive silicic eruptions, but can also hold true for explosive basaltic eruptions or discrete events associated with basaltic fissure eruptions.
The 2010 eruption of Eyjafjallajökull volcano, Iceland, sent a plume of volcanic ash south-east across the Atlantic Ocean with ash fallout in Iceland, the UK and on mainland Europe . Substantial, but localized, ashfall in Iceland triggered concerns and anxiety about the safety of inhaling volcanic particulate for the general population and susceptible groups [2, 3], since respirable particulate matter (PM) is known to negatively impact population health [4, 5] and has recently been classified as a carcinogen . Although the thickness of ash deposited distally was negligible, the unanticipated phenomenon prompted similar public health concern across Northern Europe [7–9]. A year later, an eruption of Grímsvötn volcano produced minor ashfall in Iceland, the UK and Scandinavia [10, 11], again fueling the need to understand the respiratory hazard of these particles.
Physicochemical characteristics of inhaled particles are known determinants of biologic activity . Therefore, predictive screens for assessing particle toxicity can help improve risk management advice . The International Volcanic Health Hazard Network (www.ivhhn.org) promptly launched such efforts after both eruptions using a protocol designed to rapidly estimate the respiratory hazard through physicochemical and toxicological assessment of the ash [8, 14]. This protocol has been successfully implemented for a number of eruptions worldwide to inform ash hazard [8, 15–17]. The Eyjafjallajökull and Grímsvötn studies found that ash from the two eruptions did not possess most of the physicochemical characteristics often associated with acute or chronic respiratory disease, such as abundant crystalline silica or fiber-like particles. However, the ash from both eruptions contained respirable-sized (< 4 μm) material [8, 18], and caused a sustained pro-inflammatory response in lung cells in vitro , thereby indicating that inhaled material may trigger adverse health consequences.
In Iceland, the abundance of fine material in Eyjafjallajökull ash contributed significantly to ambient PM, due to both direct ash emissions  and re-suspension [19, 20], and several medical studies were initiated to determine any respiratory health consequences resulting from exposure to the ash. Early reported symptoms of upper airway and eye irritation and exacerbation of pre-existing asthma were limited, but ash exposure was associated with elevated prevalence of respiratory irritation and cough amongst residents of the most ash-exposed rural area close to Eyjafjallajökull [3, 21], and high PM levels were associated with emergency hospital visits in the capital city Reykjavík despite no ash accumulation . In the immediately affected areas, an association was found between long-term exposure to volcanic ash and a higher prevalence of respiratory ailments , supporting the few previous epidemiological studies conducted elsewhere that consider moderate to heavy long-term exposure to ash and respiratory health .
Less is known about the health effects from exposure to long-range transported volcanic ash, although some cases of exacerbated respiratory ailments have been reported [25, 26]. As in Iceland, studies were prompted across Europe following the eruptions of Eyjafjallajökull and Grímsvötn due to the potential hazard posed. Increases in ambient PM were reported in Scandinavia but with inconclusive or unreported health outcomes [11, 27]. In the UK, ash was detected from both eruptions [10, 28], but syndromic surveillance did not pick up any adverse effects following ash exposure .
The Health Protection Agency (now Public Health England) carried out a review of the potential effects of volcanic ash inhalation, focusing on the low exposures likely to affect the UK , as part of work to inform UK policy during future ashfall events. This review occurred concurrently with the inclusion of the risk description for long-range volcanic hazards in the UK National Risk Registry of Civil Emergencies. The HPA, in consultation with IVHHN, recommends communicating the proportion of respirable material in ash and the presence or absence of crystalline silica at the earliest stage following a major eruption to public health officials so that they can provide evidence-based advice to the general public. The present study is a result of the recommendations from the aforementioned HPA review and aims to provide a baseline for early evidence on the likely physicochemical characteristics of different types of Icelandic ash, upon which initial advice during the next Icelandic ashfall incident can be founded.
The Icelandic volcanoes span a spectrum of eruption styles and magma types, from those that produce effusive, gas and lava-rich eruptions to those generating large explosions where vast quantities of ash are produced . However, historical records and reconstructions from the geological record indicate that three quarters of all Holocene eruptions in Iceland were explosive [30, 31]. Cryptotephras (ash horizons in distal sedimentary sequences) have been identified across northwestern Europe from many of these eruptions , and there is evidence that the Icelandic volcanoes are entering a period of increased volcanic activity . Therefore, there is an urgent need to assess the potential respiratory hazard of Icelandic ash from the range of volcanoes that might erupt in the foreseeable future, likely affecting communities in Iceland, the UK and the rest of Europe.
Due to the limited number of recent eruptions, compiling evidence on the effects that future eruptions may have on public health is best investigated through studying previous activity of the range of Icelandic volcanoes. In this study, we apply the screening strategy used on the Eyjafjallajökull 2010 and Grímsvötn 2011 ash  to samples of archived Icelandic ash, as analysis consistent with this protocol facilitates comparisons with existing heath studies. Only the particle-specific hazard is addressed herein. The recent Bárðarbunga-Veiðivötn fissure eruption at Holuhraun has highlighted how volcanic gas (predominantly SO2) and sulfate aerosol emissions can negatively impact air quality and health [34, 35], and previous eruptions of Iceland’s volcanoes have resulted in substantial environmental loading of adsorbed materials, particularly fluorine . Both gas and leachate hazards also need to be considered during future eruptions.
Postglacial volcanism in Iceland occurs within geographically distinct fissure systems and the associated central volcanoes, collectively termed volcanic systems [37, 38]. There are about 30 active volcanic systems in Iceland, 20 of which feature fissure swarms (fracture zones where eruptions occur along fissures) and 19 have at least one central volcano . Felsic (silica rich) and intermediate magma is confined to the central volcanoes, whereas mafic (silica poor) magma has erupted at both the associated fissure swarms and at the central volcanoes [37, 38]. A total of 16 volcanic systems have been active in the last 11 centuries. Eruption frequency varies, being highest at the Grímsvötn volcanic system, with about 70 eruptions during this period. However, of the roughly 200 recorded eruptions, less than 30 erupted felsic or intermediate magma and only Askja, Hekla and Öræfajökull have produced dacitic or rhyolitic tephra [39, 40]. Iceland’s volcanic systems exhibit a variety of eruption styles, each broadly dependent on magmatic composition (i.e., basaltic to rhyolitic) and a system’s proximity to, and relationship with, surface waters, groundwaters and ice caps.
Each volcano has distinctive eruption characteristics and products, and particles from different sources could have different toxicological effects. Therefore, a single hazard assessment cannot be made. However, the compositional trends of the products from each volcanic system have remained relatively stable throughout the Holocene, and many of them are geochemically distinct from other systems . Due to the stability of the characteristics, physicochemical analysis of eruptive products from the Holocene can provide insight into the respiratory hazard posed by Iceland’s volcanoes during future eruptions. To consider this breadth of erupted products, 14 tephra samples were sourced from 11 eruptions at 8 central volcanoes for detailed investigation. These include the largest tephra layers produced by each of the relevant volcanic systems as eruptions of similar magnitudes would be the most likely to affect Iceland and the rest of Europe. The details of each sample are outlined in Table Table1,1, and the location of each system is shown in Fig. Fig.11.
The employed IVHHN protocol (Fig. (Fig.2),2), explained in detail previously [8, 15, 16], was designed for rapid assessment and uses the < 1 mm ash fraction rather than a respirable fraction due to the quantity of ash required for analyses and timeframe for separating sufficient fine ash for the range of analyses. While other health-focused studies of volcanic ash use a respirable isolate, particularly in toxicology studies [41–43], use of the < 1 mm fraction for all analyses here is considered appropriate as the parameters of interest for physicochemical characterization generally correspond between the bulk material and respirable fraction . All samples were dried in an oven at 80 °C for 12 h and then sieved (Endecotts woven wire stainless steel sieves) first through a 2 mm and then subsequently a 1 mm sieve. No impact on particle characteristics is expected from this preparation; however, if leachable elements are of concern, a sample split should be taken prior to drying and sieving as outlined elsewhere for best practice [45, 46].
Physicochemical assessment was conducted on all samples except where sample quantities were insufficient or it was believed that the samples were unrepresentative of the original ash deposit. Samples for analysis by transmission electron microscopy (TEM) were chosen based on results of particle size analyses, where samples Hekla-4 and Laki-SnVII contained the highest abundance of < 1 μm material (see section 3.1). Samples selected for surface area analyses are the finest grained (most abundant < 4 μm fraction) that also represent the breadth of magmatic compositions and the range of volcanoes considered. Table Table22 provides a summary of the analyses conducted on each sample. No evidence of alteration was noted during physicochemical characterization of the archived ash samples, but full toxicological testing was not pursued because the samples were, in some cases, several thousand years old and, inevitably, will have experienced surface weathering prior to collection, thereby affecting their toxicity profile .
The chemical composition of ash samples was determined by X-ray fluorescence (XRF) using a PANalytical Axios Advanced XRF spectrometer at the Department of Geology, University of Leicester, UK. Major elements were analyzed on fused glass beads prepared from ignited powders, using 100% Li tetraborate flux with a sample to flux ratio 1:10. Data have been recalculated to include loss on ignition.
Particle size data were collected by laser diffraction using a Malvern Mastersizer 2000 with Hydro MU attachment at the Department of Geography, University of Cambridge, UK. Ultrasonics were used to disaggregate samples and the results are from an average of three runs. Samples were measured with a refractive index appropriate for their chemical composition (after ) and an absorption coefficient of 0.1. Data were interpolated to include the 1–2 mm particles according to weight fractions of the sieved material in order to provide particle size data relative to the ‘ash’ (< 2 mm) fraction.
Imaging of volcanic ash by scanning electron microscopy (SEM) was carried out on a Hitachi SU-70 FEG SEM in the GJ Russell Microscopy Facility, Department of Physics, Durham University, UK. Samples were prepared for imaging by sprinkling ash onto a polycarbonate disc adhered to an aluminum SEM stub using a carbon sticky pad and coated with ~30 nm of carbon.
TEM was used to observe the morphology, chemistry, and structure of the nano-fraction in volcanic ash with a specific emphasis on respirable fibers. Analyses were carried out on a JEOL JEM-2100F FEG TEM at 200 kV in the GJ Russell Microscopy Facility, Department of Physics, Durham University, UK. Bulk ash samples were analyzed on holey carbon copper TEM grids.
Powder X-ray diffraction (XRD) was used to identify crystalline silica phases in the ash. Crystalline silica polymorphs have been singled out for identification (and quantification when present) because they are classed as human carcinogens  and may cause the fibrotic lung disease silicosis . Sub-samples of ash were prepared as a thin smear on a silicon zero diffraction plate and data collected using a Bruker Analytical D8 ADVANCE diffractometer with DAVINCI design in the Department of Chemistry, Durham University, UK.
Specific surface area (SSA) corresponds strongly with particle toxicity as it is a measure of the maximum available surface on which reactions can occur. We used the BET (Brunauer–Emmett-Teller) method of specific surface area analysis using nitrogen adsorption with a Micromeritics TriStar 3000 Surface Area and Porosimetry Analyser in the Department of Chemistry, Durham University, UK. Prior to analysis, samples were degassed under nitrogen at 110 °C for a minimum of 2 h.
The surface reactivity of particles was assessed by their ability to generate free radicals, which are known to be potential inflammatory and carcinogenic factors [51, 52]. Electron Paramagnetic Resonance (EPR) spectroscopy was used to quantify the generation of hydroxyl radicals (HO•) using the spin-trapping technique through replication of the Fenton reaction . Measurements were taken at 30 min using a Miniscope 100 ESR spectrometer, Magnettech at the Università degli Studi di Torino, Italy. The integrated amplitude of the peaks generated is proportional to the number of radicals generated. Data are the average of three runs and are expressed per unit surface area (see section 2.4). Three previously analyzed samples of ash from other volcanoes were included for comparison (see ).
Given that some samples used in this study are ancient, EPR experiments were conducted on samples as they were collected (un-ground) as well as after light grinding. Grinding exposes fresh surfaces, which provides an indication of the reactivity expected for non-weathered samples . Approximately 500 mg of ash was ground in a Retsch MM2 mixer mill at a frequency of 27 Hz for 60 min. Samples were analyzed immediately after grinding. The specific surface area of samples was only determined for the un-ground samples as insufficient material was available to also analyze the ground samples, but previous experience has shown that the change in SSA is minimal as grinding abrades ash surfaces with little fragmentation of particles .
Experiments were conducted to determine the amount of surface iron available for participation in the iron-based reactivity assessed by EPR. Following previously detailed methods , ash was incubated at 37 °C with the Fe2+-specific chelator ferrozine with and without ascorbic acid to measure total Fe and Fe2+, respectively (Fe3+ was calculated by difference). Measurements were taken every 24 h for 7 days in a Uvikon spectrophotometer (562 nm) at the Università degli Studi di Torino, Italy, a time-point previously identified as sufficient to approximate maximum iron removal . Three previously analyzed samples (from other volcanoes, as above) were included for comparison. Results are expressed per unit surface area and are the average of two separate experiments. Only un-ground samples were analyzed due to the limited amount of ash available.
The toxicity of the ash was assessed with the hemolysis (red blood cell lysis) assay. A positive result signifies the ability of a sample to rupture a biological membrane, which is an indicator for the potential to cause cellular damage. For crystalline silica, a direct relationship between hemolysis and disease has been reported , thereby serving as one end point related to inflammation to be tested. Human red blood cells were exposed to a range of ash concentrations in saline from 0.31 to 1 mg ml−1 for 30 mins at the University of Edinburgh, UK following methods previously detailed . DQ12 quartz was used as a positive control and TiO2 was used as a negative control. Data are reported as a percentage of complete cellular lysis as determined with Triton X-100 (0.1%). Samples were not ground prior to analysis. Analyses were carried out on bulk material, which is common practice for volcanic ash [8, 15, 57], as hemolysis on bulk and respirable samples have shown similar results .
The samples selected for this study are from historical and prehistoric eruptions of Icelandic volcanoes, and span the range of magma compositions (from basaltic to rhyolitic) that could be expected from Icelandic volcanism (Fig. (Fig.3).3). All samples were generally coarse grained (Table (Table3),3), with the exception of Laki-SnVII, an ash sample from the 1783–84 Laki eruption, and Hekla-4, erupted c.a. 4.2 ka B.P, which contained abundant respirable material (5.1 and 11.3 vol.% < 4 μm, respectively). Particle sizes observed by SEM imaging qualitatively corroborated laser diffraction data. Samples Snae-1 and Hekla-1158 were not analyzed for particle size since they were too coarse-grained.
Ash particles of all sizes (< 1 mm) are generally angular with fractured surfaces (see Fig. Fig.4),4), as expected for volcanic ash [8, 15–17]. All samples were visually similar except for Laki-SnVII, which was sampled from two ashfall units produced by rootless eruptions that took place as the basaltic lava advanced over wetlands . This sample contained aggregates of fine material and fine particles adhered to larger particles (Fig. (Fig.4g),4g), and also contained diatom frustules (which are not discussed further here but have been identified in deposits from other eruptions ).
Fibers were rare, but present, in both samples investigated by TEM (Fig. (Fig.5).5). Three types of fiber-like particles were identified in Laki-SnVII: completely amorphous (Fig. (Fig.5b),5b), semi-crystalline comprised of sodium and oxygen (Fig. (Fig.5c),5c), and well-crystalline comprised of silicon and oxygen with lesser amounts calcium, iron, magnesium, aluminum, and titanium (Fig. (Fig.5d).5d). Although the actual mineral was not identifiable, the well-crystalline fibers are not related to asbestiform minerals or fibrous zeolites based on database indexing. The three different types of fibers in Laki-SnVII were encountered with equal frequency. In Hekla-4, only amorphous, fiber-like particles were identified (Fig. (Fig.5a5a).
The specific surface areas measured range from 0.4 to 1.6 m2 g−1 (Table (Table3).3). Hekla-4 had the largest surface area of all samples analyzed. These surface area values are in keeping with expected values from previous analyses of ash samples [8, 15–17].
Almost all samples analyzed lacked a detectable crystalline silica component, being predominantly comprised of glass and some feldspar. The exception was Snae-1, which contained detectable amounts of quartz. There was insufficient mass of this sample for quantitative analysis, however. No sample contained cristobalite or tridymite.
All samples were able to generate hydroxyl radicals (Fig. (Fig.6),6), even if the amount of radicals was low when compared with standard ash samples analyzed concurrently (see also Fig. Fig.7).7). Moreover, all samples generated more hydroxyl radicals when ground than when analyzed as collected (Fig. (Fig.6).6). That ‘refreshing’ the sample surfaces resulted in increased radical generation is consistent with previous data , as weathered ash samples are more oxidized and less reactive than freshly collected samples .
The use of previously analyzed andesitic and basaltic samples provides benchmarks for the compositional range of the current samples. As expected from the spectrum of samples analyzed, there is a range in the amount of chelatable iron, with basaltic samples (e.g., Katla-1755 and Laki-SnVII) releasing more iron than dacitic and rhyolitic samples (e.g., Hekla-4, Orae-s1, Askja-59b). However, there is no correlation between the amount of iron mobilized from the surface of un-ground particles and iron-catalyzed hydroxyl radical generation (Fig. (Fig.7).7). Askja-59b, a dacitic sample, generated the most hydroxyl radicals.
None of the samples were found to be hemolytic compared to the negative particle control, and were far less reactive than the positive quartz control (Fig. (Fig.88).
A suite of analyses was conducted in accordance with the IVHHN protocol (Fig. (Fig.2)2) to constrain the potential respiratory health hazard posed in the event of future eruptions of Iceland’s volcanoes in order to inform pre-eruption mitigation policy and preliminary risk assessments whilst syn-eruption data are being collected. The samples selected for this study, from historical and prehistoric eruptions of Icelandic volcanoes, encompass the full range of magma compositions that could be expected from Icelandic volcanism (Fig. (Fig.3).3). Studies on the recent eruptions of Eyjafjallajökull and Grímsvötn  were also conducted following the IVHHN protocol and are considered alongside the present study.
Determining the potential for volcanic ash to be inhaled is of utmost importance when assessing the respiratory hazard. Particle size distributions of ash samples are a function of the eruption intensity (which differs over 3 to 4 orders of magnitude among individual events considered here) as well as size fractionation during transport to the site of deposition. Therefore, exposures are temporally and spatially variable throughout and following an eruption. Only 1 to 3 samples were sourced per eruption in the present study and, by and large, samples were collected at discrete locations relatively close to source; as such, the particle size measurements are considered an indication of potential rather than being representative of the finest tephra produced.
In general, intermediate to silicic eruptions result in finer particle size distributions than basaltic eruptions ; aside from the Laki samples, the data here are in keeping with this trend (Table (Table3).3). However, basaltic eruptions in Iceland have also produced fine-grained ash, such as previous eruptions of Katla, with ash reaching mainland Europe . The notable example in the present study is Laki-SnVII (5.07 vol.% < 4 μm). While these data are not likely representative of the cumulative ashfall of the eruption, as evidenced by the difference in respirable material between Laki-SnVII and Laki-SnV (1.90 vol.% < 4 μm), they highlight the potential for discrete events during an eruption to pose a variable respiratory hazard. This was also observed for the eruption of Eyjafjallajökull, with the abundance of fine material differing amongst the four phases of the eruption [1, 8].
Ash particles were angular and blocky, which is consistent with previous studies, and is also observed for respirable ash . Experimentally, fine-grained ash of this morphology effectively deposits in the alveolar and tracheobronchial regions of the lungs , which should be expected for future exposures. To date, including the current study, the presence and relative abundance of fiber-like particles in ash has been exceptionally rare by number and is sample specific (samples from Hekla and Laki analysed here and also see reference ). We note, however, that fibers were identified by TEM in both samples analyzed here and suggest that such analyses be conducted during future eruptions as the general occurrence of nano-fibers in ash is poorly constrained to date. Even still, no fibrous minerals with established toxicity profiles have been identified, thereby limiting concerns for future exposures.
The experiences of the 2010 Eyjafjallajökull and 2011 Grímsvötn eruptions, the extensive evidence of ashfall reaching UK/Europe from previous eruptions in Iceland (e.g., ), and the quantification of respirable material in samples from the historical eruptions studied herein demonstrate the potential for long-range transport of inhalable ash from eruptions spanning the compositional range of Iceland’s volcanoes. Even ‘weak’ eruptions and low-altitude plumes can transport ash to distances of >1000 km [1, 10]. Existing tephra dispersion models can accurately capture the timing of arrival of an ash cloud , but are unable to reliably predict the abundance of fine ash or ground-level mass concentrations. In the event that dispersion models predict that ash will reach the UK/Europe from an Icelandic source, existing ground-based air quality networks, such as those used to monitor compliance with the EU Ambient Air Quality Directive, and syndromic surveillance systems can be used to monitor exposure and community health during the incident. Particular attention should be paid to areas with existing PM burdens, as small increases in PM concentrations can lead to an increase in exceedance days, and combined exposure to ash and anthropogenic pollution can result in a heightened immune response in vitro .
The minerals of primary concern in volcanic ash are the crystalline silica polymorphs due to their potential to cause fibrotic lung disease and cancer . It is presently unclear whether volcanic crystalline silica can cause disease [41, 63, 64], but volcanic ash has been shown to activate the same biological platform involved in the development of some other particle-induced lung diseases, including silicosis . Until this is further clarified, all rapid health assessments consider the amount of crystalline silica present.
The crystalline silica hazard posed was low for all samples analyzed. This is consistent with previous studies on silicic volcanic products in Iceland, where quartz is exceedingly rare as a phenocryst phase , as well as the results from the previous IVHHN and other studies on Eyjafjallajökull and Grímsvötn ash, which found minor quartz in select Eyjafjallajökull samples (< 3 wt.%) and no detectable crystalline silica in Grímsvötn tephra [8, 18, 67]. The exception in the present study was Snae-1 (glass compositions of 66–69 wt.% SiO2 ); however, the bulk sample was exceptionally coarse grained (91 wt.% > 2 mm material), so was considered non-respirable and was not analyzed further.
Although cristobalite and tridymite were not present in the samples analyzed, these phases are able to form in lava flows and domes from volcanoes with basaltic-andesite to rhyolitic compositions that have undergone post-emplacement mineralization or alteration (see review in ), and can be present in substantial quantities through spherulitic growth in dome lavas in Iceland . Critically, the presence of crystalline silica is not ubiquitous throughout an eruption, as evidenced by the 2008 eruption of Chaitén volcano, where substantial cristobalite was only detected after dome growth (and collapse) began . Therefore, these phases may be present if future eruptions incorporate older material, or in the event of new dome growth during an eruption. Given that no ash was available from historical eruptions involving disruption of a dome, preliminary SEM and XRD analyses were conducted on dome samples from Torfajökull and Krafla. Crystalline silica was present as both cristobalite and tridymite; however, consideration of the resultant abundance of crystalline silica in ash from an eruption of either location would be highly speculative and is not further discussed. Accordingly, we suggest case-by-case consideration of crystalline silica in the ash from future intermediate to silicic eruptions, despite its absence in the present study, as it is considered a hazard that can evolve throughout an eruption.
The inherent variability of volcanic ash across eruptions has prohibited consensus on when (or if) ash will be pathogenic. To date, the IVHHN approach has been to screen samples using the employed tests for free radical production and membrane damage (hemolysis) as the pathways through which volcanic ash can initiate a pro-inflammatory response are largely unconstrained [8, 65]. While other biological tests could be employed, the chosen analyses are low-cost and rapid, making them ideal for a screening approach, and account for the two predominant concerns: crystalline silica and reactive surface iron [54, 71]. Together with physicochemical profiling of ash, this allows us to assess the value of pursuing additional, costlier immune cell-based experiments since these tests are not definitive indicators of toxicity alone , regardless of the inherent variability of volcanic ash. The two endpoints considered were unable to offer predictive insight into the potential variability in toxicity of ash from future eruptions of Iceland’s volcanoes, but, as mentioned, no further toxicology work was conducted as these samples were not collected fresh and, accordingly, results would have limited applicability .
The propensity to generate free radicals serves as one candidate mechanism through which some samples of volcanic ash (including Icelandic ash) can initiate a pro-inflammatory response in vitro [8, 41, 73]. Work on volcanic ash frequently focuses on iron-catalyzed free radical generation [54, 55, 74], which can become prolonged when iron is present in a specific oxidative and coordinative state on the surface of particulate matter . While a dependence on magmatic composition has been observed previously [54, 55], where Fe-rich mafic samples generate more hydroxyl radicals than comparatively Fe-poor silicic samples, a strong trend was not observed in the present study. Mafic samples Katla-1755, Hekla-1980 and Laki-SnVII were only slightly more reactive than silicic samples Orae-s1 and Hekla-4. Askja-59b generated the greatest number of hydroxyl radicals of the test samples despite having a dacitic composition and, therefore, a lower abundance of (surface) iron than basaltic Katla-1755, Hekla-1980 and Laki-SnVII (Figs. (Figs.66 and and7).7). The compositionally aberrant production of radicals by Askja-59b has been observed previously for felsic ash (dacitic Pinatubo sample in reference ), albeit infrequently, emphasizing that high-silica/low-iron compositions do not necessarily display lower reactivity than low-silica/high-iron compositions. This is likely because different phases in ash are variably responsible for radical production , and hydroxyl radical generation is governed by the coordination and redox state of discrete sites on the particle surface . Accordingly, fresh samples should continue to be screened in this manner at the time of an eruption as post-eruptive processing of particles in the eruptive plume, atmosphere and environment, in addition to inherent variability, can affect particle surfaces to variable extents.
Despite the lack of hemolysis observed here and for ash from other volcanoes [8, 15], hemolysis retains value as a screening tool. Recent experimental work has shown that crystalline silica-bearing ash can activate the NLRP3 inflammasome , a mechanism central to the initiation of crystalline silica-induced disease. For reactive surfaces like quartz, the property of being hemolytic carries with it the property of activating the NLRP3 inflammasome , thereby linking hemolytic activity with inflammogenic activity. This discrepancy between negative hemolysis results and the evidence for ash-induced inflammation in vitro has yet to be reconciled, particularly for ash containing appreciable crystalline silica, and is the focus of on-going toxicology work.
Prior to the recent eruptions of Eyjafjallajökull and Grímsvötn, little was known about the toxicity of ash, or the variability thereof, from Iceland’s volcanoes. Studies conducted in Iceland in the aftermath of Eyjafjallajökull, in particular, reported immediate symptoms, both near source and at distances greater than 100 km (Reykjavík), as well as long-term symptoms in communities with chronic exposure to ash. Transient increases in PM were observed in the UK and Europe due to long-range transport of ash from both eruptions, but there was no risk of chronic exposure from resuspended material and no conclusive evidence for a resultant decrease in population health. The events prompted the need to evaluate the hazard posed by future eruptions, however, and a particle-screening approach was adopted for the present study to constrain the range of toxicity-relevant particle characteristics that may result from future eruptions.
The samples analyzed here span the compositional range of Iceland’s volcanoes (basaltic to rhyolitic) and were mostly from eruptions that can be grouped as moderate to large in terms of eruption intensity and erupted volume (0.1 km3 to 10 km3). Specific samples from the various eruptions contained substantial respirable material, and we should expect that future explosive eruptions of Iceland’s volcanoes across the compositional spectrum could produce respirable ash, which may augment ambient PM levels considerably. We expect future Icelandic eruptions to generate ash which has low crystalline silica content, unless an existing dome is disrupted, to have a low surface area and to have insubstantial fiber-like particles. Nevertheless, if inhalable in size, the ash may be reactive in vivo. That ‘refreshing’ the sample surfaces resulted in increased radical generation emphasizes that analysis of fresh ash (whenever possible) is prudent for determining the immediate hazard to public health. The ranges defined for the health-relevant physicochemical properties in this detailed characterization can be used as a qualitative evidence base for future hazard and risk assessment and for scenario-building purposes, but we suggest that eruption-specific monitoring of ash continue to be undertaken as ash characteristics vary as eruptions evolve. Additionally, we emphasize that gas and soluble-species hazards are not addressed in the present study and warrant incorporation into population health assessments during future eruptions.
We thank Chris Rolfe (University of Cambridge, UK) for carrying out particle size analyses, Nick Marsh (University of Leicester, UK) for carrying out XRF analysis, Leon Bowen and Dr. Budhika Mendis at the Durham G.J. Russell Electron Microscopy Facility (Durham University, UK), and Dr. Ken Livi (Johns Hopkins University, USA) for assistance with TEM diffraction indexing and mineral identification. Thanks also to Dr. Peter Baxter for public health advice at planning and report writing stages, Prof Virginia Murray and Dr. Ishani Kar-Purkayastha (Public Health England) for motivating this research, and to Dr. Andrea Foster (USGS) and Dr. Gunnar Guðmundsson for insightful reviews of this manuscript and our approach. This work was carried out under the remit of the International Volcanic Health Hazard Network (IVHHN), the umbrella organization for research and dissemination on the health effects of volcanic emissions. Additional information on the health effects of volcanic ash is available at www.ivhhn.org. Any use of trade, product, or firm names is for descriptive purposes only and does not imply endorsement by the U.S. Government.
This work was funded under the UK Natural Environment Research Council (NERC) Knowledge Exchange (KE) Fellowship NE/J500525/1 granted to R.E. Holdsworth at Durham University. DED was additionally supported by the ERC Advanced Grant no. 247076 awarded to D.B. Dingwell at LMU Munich.
The datasets used and/or analyzed during the current study are available from the corresponding author on reasonable request.
DED carried out the experiments, analyzed and interpreted all data, and drafted the manuscript. CJH conceived the study and helped draft the manuscript. GL and TT sourced archived samples and provided expert knowledge on the eruptions of Icelandic volcanoes. MT provided lab support for the particle surface reactivity experiments. MT, BF and KD provided expertise on particle toxicology. All authors read and approved the final manuscript.
CJH is the director of the International Volcanic Health Hazard Network (IVHHN), DED is a deputy director, and BF and KD are expert members. The authors declare that they have no competing interests.
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David E. Damby, Phone: +1 650 329 4961, Email: vog.sgsu@ybmadd.
Claire J. Horwell, Email: firstname.lastname@example.org.
Gudrun Larsen, Email: si.ih@eralg.
Thorvaldur Thordarson, Email: si.ih@htvrot.
Maura Tomatis, Email: email@example.com.
Bice Fubini, Email: firstname.lastname@example.org.
Ken Donaldson, Email: ku.oc.liamtoh@xotcdk.