Recent decades have seen widespread recovery and analysis of a wide suite of ecofactual remains from archaeological sites, particularly in territories with systematic frameworks and guidance for development-led archaeology. As the cumulative volume of ecofactual data has mounted, however, the analytical tools required for its synthesis across space and time have not always kept pace. While recent attention has been devoted to spatial aspects of meta-analysis, particularly through increasingly sophisticated applications of GIS (see e.g. Livarda and Orengo 2015; McKechnie and Moss 2016), the methodological and statistical challenges of chronological synthesis have been somewhat neglected.
Nowhere is this issue more acute than for urban archaeological sites. A typical combination of complex, well-dated stratigraphy, rich organic remains, and multiple small- to medium-scale excavations often leads to an abundance of small datasets with cross-cutting phasing and varied chronological resolution. Separately, many of these datasets are of limited value; together they can represent the environmental and socio-economic history of a city. The quality of excavation and documentation in this context is often very high, but the resources available for subsequent analysis beyond the level of individual projects are variable. There thus exists a rich and under-utilised archival resource for addressing some of the big questions of urban archaeology, and a need to develop analytical tools enabling optimal use of this resource.
In the medieval period of western Europe, one of those big questions is the extent to which long-range provisioning underpinned urban development and population growth. A key development in this context is the dramatic shift towards marine – and apparently away from freshwater – resources that occurred in England around the start of the 11th century AD, particularly at urban settlements. This ‘Fish Event Horizon’ marks a significant change in the resource bases of medieval towns, and represents the ultimate origin of modern commercial marine fisheries in the North Sea and beyond (Barrett et al. 2004a; 2004b).
This paper discusses two major challenges in urban ecofactual synthesis: chronological uncertainty and variable research intensity. We review recent approaches to chronological synthesis, particularly aoristic analysis and Monte Carlo simulation, before demonstrating a method that allows results to be ‘calibrated’ for the intensity of research on different periods, and hence permits inferences regarding changes in absolute frequency of taxa in the archaeological record. This is applied to a large fish bone dataset from London in order to address two key questions relating to the Fish Event Horizon as manifested in the city: (a) how sudden was the shift towards marine fish; and (b) was it accompanied by an absolute rather than relative decrease in freshwater fish deposition?
Perhaps fittingly, our approach draws inspiration from a concept used in fisheries biology for more than a century (Garstang 1900) and more recently adopted into fisheries history (Poulsen and Holm 2007): catch per unit effort (CPUE). Where data exist for both the amount of fish caught and the distribution of fishing effort, researchers can use these to infer relative abundance of stocks over time. Our approach to the zooarchaeological record is analogous: where fisheries researchers assess changes in the number of fish in the sea, we infer fluctuations in the numbers of fish deposited, replacing fishing effort with archaeological sampling intensity and the yield of live fish with the ‘catch’ of archaeological fish bones.
Having been rare since the onset of the Neolithic (c.4000 cal BC), marine fish taxa suddenly reappear in the English archaeological record in significant numbers from the start of the 11th century AD, often making up more than half of identified fish specimens in sieved assemblages from inland sites (Barrett et al. 2004a; 2004b). In the first instance this was primarily an urban phenomenon, with percentages at rural sites increasing more gradually over the following centuries. This resurgence of marine fish is starkest for cod (Gadus morhua), but related species such as haddock (Melanogrammus aeglefinus), saithe (Pollachius virens), ling (Molva molva), and hake (Merluccius merluccius) all became important by the 13th century. The phenomenon had some precursors at early medieval elite sites (Reynolds 2016) and in the form of herring at proto-urban trading centres, which from the seventh to eighth centuries onwards commonly contributed up to 20% of fish by NISP (fragment count) and occasionally more, for example at Castle Mall, Norwich, England (Locker 2009). Nonetheless, the abundance of herring also increased dramatically around AD 1000, reaching a median of 40–50% of fish NISP between the 11th and 16th centuries at both urban and rural sites.
Synthesis of fish bone data from Flanders, Belgium, reveals a broadly similar phenomenon (Ervynck et al. 2004), albeit with differences in the chronologies for specific taxa – flatfish playing a more important role while gadids remain rare until the 13th century (Van Neer and Ervynck 2016). Meanwhile, stable isotopic analysis of human bones from English sites (Müldner 2016) supports the idea of a substantial increase in marine protein from around the 11th century, albeit with an earlier spike in marine signatures during the Roman period (Müldner 2013 c. AD 43–410) that is not clearly matched by the fishbone record (Locker 2007) and may to some extent represent shellfish consumption.
Various factors have been put forward as possible causes for the Fish Event Horizon. On the supply side, an initial hypothesis that the change was driven partly by long-range trade in dried cod – and perhaps other gadids – from Norway (Barrett et al. 2004a, 624–627) has now been disproven: cod consumed in London and elsewhere appear to have been primarily North Sea catches until at least the mid 13th century, based on stable isotopic composition and anatomical representation (Barrett et al. 2011; Orton et al. 2014; Harland et al. 2016). Climatic conditions can probably thus be ruled out: the same warming that might have been expected to increase cod productivity in northern waters would if anything have depressed it in the southern North Sea, as this area is towards the species’ southern limit (Barrett et al. 2004b, 2419–2420). Yet cod are one of the main species implicated in the Fish Event Horizon in England – although not, interestingly, in Flanders (Van Neer and Ervynck 2016).
On the demand side, population growth, urbanisation, and the development of market economies are likely to have played significant roles (Hoffmann 2001, 144; Barrett 2016, 265; Kowaleski 2016). The medieval period in England, as elsewhere in Europe, saw rapid population growth and development of urban settlements – although the precise scale and timing of these changes are notoriously hard to establish either from historical or archaeological sources (Dyer 2002; Langdon and Masschaele 2006; Astill 2009) – and it is specifically at early urban sites that the Fish Event Horizon first becomes apparent in the 11th century. Towns and cities represent concentrations of net consumers of food; as these concentrations grew the increasing demand must have been met by a combination of intensified production and expansion of hinterlands (Galloway and Murphy 1991; Hoffmann 2001; Barbier 2011). To the extent that transport and land availability placed high costs on expansion in the supply of terrestrial bulk goods, marine resources may have represented an attractive alternative food source (Hoffmann 2002).
Demand for fish will also have been influenced by cultural factors. In particular, Christian fasting practices are likely to have played a role, potentially prohibiting consumption of most meat for much of the year and making fish an attractive alternative for those with access to it (Hoffmann 2001, 141). Aelfric’s letters to Wulfstan (c.AD 1005–1010) noted clergy could fish but not hunt or hawk, although this is not explicitly tied to fasting. The early development and enforcement of fasting rules in England is complex and incompletely understood, however, especially for the secular community (see Barrett et al. 2004a, 629–630; Serjeantson and Woolgar 2006, 104).
Finally, the onset of sea fishing might have been stimulated in part by depletion of freshwater resources due to overfishing and/or habitat destruction (Hoffmann 2001, 144; Barrett et al 2004a, 628; Barrett 2016; Roberts 2007). Apart from significant exploitation of freshwater taxa, the late first and early second millennia also saw several developments likely to have reduced productivity of freshwater ecosystems across much of Europe: widespread construction of mill dams (Lenders et al. 2016), intensification of agriculture, and increased nutrient loads due to growing populations of people and of domestic animals (Hoffmann 1996; Hoffmann 2004, 24; see also Häberle et al. 2016a; 2016b; Van Neer and Ervynck 2010, 2–3). In this scenario the shift to coastal and offshore waters could be seen as a response to diminishing returns from rivers and lakes. Alternatively, demand may simply have outstripped freshwater fisheries’ supply (Hoffmann 2002; Galik et al. 2015; Kowaleski 2016).
In attempting to evaluate the latter hypotheses we encounter a classic limitation of zooarchaeological research, namely that specimen counts are, in normal circumstances, closed datasets: if the percentage frequency of one category increases that of others must necessarily decrease. This can only be circumvented where some external control can be brought to bear, for example the volume of sediment from which specimens were recovered. As such, the relative decrease in freshwater remains observed at the Fish Event Horizon is an inevitable corollary of the increase in marine specimens, and may or may not reflect any absolute decline in their consumption.
In order better to understand the roles of these various processes in the Fish Event Horizon, it is thus necessary to ascertain whether the apparent decline in freshwater fish is real or simply an artefact of increasing marine fish consumption, and to refine the chronology for both apparent trends. If a decline in freshwater fish remains can be shown to start before the increase in marine species, this would support the hypothesis that overfishing and/or pollution of rivers and lakes began in the early medieval period and contributed to the move to marine fishing. Conversely if no such decline can be shown, or if it post-dates the Fish Event Horizon, this would suggest that the development of marine fisheries was driven primarily by increased overall demand for fish and/or changes in culinary tastes.
Given the centrality of chronology to archaeology, there has been surprisingly little debate on how the inevitable uncertainty in the dating of individual archaeological entities – be they sites, stratigraphic units, artefacts, or ecofacts – can be built into meta-analyses and syntheses (Crema 2012, 441; see also Bevan et al. 2013; Baxter and Cool 2016). Research based directly upon radiocarbon databases is somewhat ahead of the wider discipline here: increasingly sophisticated and extensive studies have synthesised 14C results across large numbers of sites, employing Monte Carlo methods (i.e. modelling of complex situations via repeated random sampling) and testing the resulting distributions rigorously against null models (e.g. Shennan et al. 2013; Timpson et al. 2014; Crema et al. 2016, Porčić et al. 2016). In these cases it is the dates themselves that are used as proxies for human activity rather than the archaeological entities that they represent, but the principles underlying such studies have rarely been applied to other forms of archaeological dating – including the combination of artefactual, historical, and dendrochonological information typically employed at medieval urban sites. Crema’s (2012; see also Crema et al. 2010) study of the chronological distribution of Jomon pit houses is a worthy exception, providing the inspiration for the approach adopted here (see also Baxter and Cool 2016; or Edinborough et al. 2015 for a rather different example).
Conventional approaches to grouping variably dated material have often focused on the mid-points of date ranges assigned to individual entities, using these to place entities into chronological categories of – typically – equal length (referred to here as ‘bins’) (Figure 1A). The original Fish Event Horizon study, for example, divided the time period into 200-year blocks and placed assemblages within these based on their mid-ranges, such that an assemblage dated to AD 1150–1260 would be placed into the ‘13th/14th century’ (AD 1200–1300) category, due to its mid-point of 1205 (Barrett et al. 2004b, 2417–2418). While this is a sensible solution in some circumstances, it has two major drawbacks. First the resolution is limited to the chosen bin width; second one must accept that the true date of an entity may fall outside the bin to which it is assigned. Reducing bin width will mitigate the former problem but exacerbate the latter; increasing the width will do the opposite.
Alternatively, one can make a judgemental assessment of ‘natural breaks’ in the available dating to define bins of variable width, potentially even overlapping, so as to optimise the balance between chronological resolution and the number of entities whose date ranges fall cleanly within a single bin – an approach well suited to non-frequency data such as biometrics (Figure 1B; e.g. Thomas et al. 2013). In historical periods these breaks are likely to be defined by a combination of round numbers (particularly ends of centuries), breaks in the pottery chronology, and major historical events. For example, London’s chronology includes a number of major breakpoints such as the Boudiccan destruction horizon (AD 60/61), Hadrianic Fire (AD 122–130) and Great Fire (AD 1666), which can be identified archaeologically. The principal disadvantage of this approach is that some well-dated entities are nonetheless likely to be excluded if they straddle key breakpoints, and that it may exacerbate the inevitable tendency for apparent changes in the material record to gravitate towards major breakpoints in the chronology.
Another option when dealing with frequency data is to define relatively narrow chronological bins of uniform width, and then build up an overall distribution by summing the probability of each individual entity falling within each bin – an approach sometimes known as aoristic analysis (Ratcliffe 2000; Johnson 2004; see Crema 2012, 445–449 for detailed discussion). The principle here is that each entity has a total probability mass of 1, which must be divided over the length of its date range (Figure 1C). For example, using bin widths of 50 years, a fish bone from a stratigraphic unit with a date range of AD 1200 to AD 1350 might contribute a probability mass of 0.33 to each of three bins (1200–1250, 1250–1300, 1300–1350). Better-dated contexts will be spread over fewer bins on the x axis (time) but will contribute more on the y axis (probability density), while area (i.e. probability mass) remains constant. Where the dated entities actually represent multiple items they can simply be weighted accordingly, so (to continue the above example) a context with three fish bones could be given a total probability mass of 3 rather than 1 to be divided between bins. The resulting summed probability distribution – or aoristic sum – is then treated as an estimate of the frequency distribution, i.e. as if it were a true histogram. In theory the bin width could be set to the maximum resolution of the given dating information (to the year, for example), but in practice coarser bins may be used for the sake of computational feasibility. A version of this approach was previously used to compare frequencies of cranial versus postcranial cod bones from London (Orton et al. 2014; 2016).
There is, of course, no strict reason to assume a uniform distribution of probability between given start and end dates. The calculation of summed probability distributions (SPDs) from multiple radiocarbon dates (see e.g. Williams 2012), for example, could be viewed as a form of aoristic analysis in which the individual calibrated date distributions take the place of uniform date ranges. For dates related strictly to artefact typology, a beta distribution model may be appropriate, allowing the analyst to build in estimates for the drop-off in usage of specific types (Baxter and Cool 2016). However, where the sources of dating information are more varied, less formal, uncertainty less well defined, and/or we simply do not know or cannot quantify relative probabilities within the dating limits – a uniform distribution is typically most appropriate, following Laplace’s principle of insufficient reason (Sinn 1980).
This aoristic approach may be an appropriate solution where date ranges are assumed primarily to represent duration, i.e. where the events represented by the dated entity are assumed to be spread over much of the given range (e.g. the gradual silting up of a ditch). It is problematic, however, where the date range largely represents uncertainty – that is, where the events represented by a dated entity are likely to have occurred within a relatively short space of time (e.g. the purposeful filling of a ditch), while the given start and end dates simply represent brackets within which this shorter episode can be safely said to have taken place. In the latter situation – which we would argue to be the norm for ecofactual deposits from most stratigraphic contexts – the meaning of the aoristic sum is not immediately clear. Technically, if scaled to an area of 1, it is the probability distribution of the true date of a single entity picked at random from the dataset: a somewhat obscure function (nb. the same is true for radiocarbon-based SPDs). Treated as an estimated frequency distribution, it describes a scenario that is at best one possibility out of many and at worst – e.g. for smaller datasets – may not even be possible. More pragmatically, while an aoristic sum may give a useful indication of the distribution of archaeological entities across time, it gives no indication of the uncertainty inherent in the dating of the constituent entities, meaning that we cannot assess the reliability of the overall distribution and cannot robustly test it against other variables or against a null model (see Crema 2012, 448–451).
The solution advocated by Crema, and followed here, is to apply Monte Carlo methods, i.e. simulation. As with the aoristic sum, the date range of each archaeological entity is treated as a uniform probability distribution between the stated start and end dates, but instead of summing these distributions across all entities we instead draw one date at random from within each of them – collectively representing one possible combination of true dates that may underlie the observed data – and calculate the number of entities that fall within each chronological bin at the desired resolution. This process is then repeated a large number of times – 5000 in the case study below – allowing medians and confidence intervals to be calculated for the frequency of entities in each chronological bin. On a completely different chronological scale this approach has been applied to uncertainty in zooarchaeological age-at-death analysis (Bréhard et al. 2014), but its use for integrating variably dated archaeological entities aside from 14C samples remains rare.
Since ecofacts of interest (in our case fish remains) derive from specific stratigraphic units, and it is typically these units that are dated rather than the individual specimens, a decision must be made on whether multiple specimens from a single unit should be simulated individually or collectively. Do we assume that they were deposited independently, potentially at different times within the date range, and hence simulate them individually? Or that they were deposited en masse in a single event, and hence simulate them collectively? This again comes down to the extent to which date ranges are assumed to represent duration versus uncertainty. In the below study we take the view that multiple specimens from a single context are likely to have tightly clustered dates of deposition rather than being spread out across the overall date range, and should hence be treated as a single (weighted) unit for simulation purposes. This may not always be true but is the more conservative assumption, inevitably increasing variability between simulation runs and hence broadening confidence intervals.
A key advantage of the simulation approach is that the observed results can be compared to null models by simulating ‘dummy’ sets based upon conservative assumptions (Crema 2012, 454). Most simply, one might set a null model of uniform frequency across a given study period and calculate the confidence interval for frequency distributions under this model, by repeating the simulation process used for the observed data but with the date limits for each entity set to be coterminous with the study period. For example, in our London study the simplest null model might assume a constant frequency of fish bones deposited between AD 1 and AD 2000. The dummy simulation would then show the extent of fluctuation that might be expected purely by chance even if this model were correct, given the observed sample size and weightings. Where the simulated curve for the observed data falls outside the confidence band from the dummy set, fluctuations in frequency may be significant.
This method is loosely analogous to recent studies using 14C dates as a population proxy (e.g. Shennan et al. 2013; Timpson et al. 2014; Crema et al. 2016; Porčić et al. 2016), although in that scenario a dummy set of dates is subsequently run across the radiocarbon calibration curve, to some extent determining the shape of the resulting confidence zone (Armit et al. 2013). Rather than a uniform null model, such studies often use an exponential growth curve fitted as closely as possible to the empirical data, to represent the effect of site loss over time (Surovell and Brantingham 2007; Williams 2012) and/or expected human population increase (Shennan et al. 2013, 3). In the study below we develop a null model based instead on the distribution of sampling effort over time – representing the null hypothesis that deposition of specimens was constant over time and that the observed data are shaped only by variable research intensity (i.e. more intensive sampling of archaeological deposits of certain time periods; see following section). This removes the need for a deposit-loss model – since deposits that have been lost cannot be sampled – although a taphonomic adjustment specifically for bone diagenesis could theoretically be applied.
There are fundamental differences, however, in the nature of dates derived from mixed archaeological sources vis-à-vis those from radiocarbon. In the papers cited above, simulated sets of calendar dates are not sampled from the observed calibrated 14C dates in the same way as advocated here for archaeologically-dated entities. Rather, a single summed probability distribution (SPD) is compiled from the empirical data and compared to a set of hypothetical SPDs derived from populations simulated under the null model (Figure 2A). This is possible because the relationship between calendar dates and radiocarbon dates is readily modelled, being defined by the radiocarbon calibration curve: calendar dates simulated under the null model can be ‘back-calibrated’ (or ‘uncalibrated’) to give a set of hypothetical 14C determinations, which can then be re-calibrated and combined into hypothetical SPDs – thus realistically simulating the process by which the empirical SPD was derived, and providing a null-model-based confidence band against which it can be assessed (see Timpson et al. 2014 for further explanation). The equivalent with a set of archaeologically dated entities, such as our fish bones, would be to calculate the (unique) aoristic sum of the observed entities’ date ranges (which is an SPD if scaled to an area of 1), and compare this with a set of hypothetical aoristic sums based on dates simulated under the null model. But, of course, the relationship between informal archaeological date ranges and true calendar dates cannot readily be modelled, rendering the ‘back-calibration’ step impossible: we cannot probabilisitically generate a set of likely archaeological date ranges based on a set of simulated calendar dates. For this reason, we follow Crema (2012) in using a dual-simulation approach, comparing sets of calendar dates drawn from the empirical data and from the null model respectively (Figure 2B).
In practice, archaeological research questions often relate less to the frequency distribution of an object class per se, and more to the likelihood that an increase or decrease in frequency occurred at a given point in time – the Fish Event Horizon being a good example. With a simulation approach, evaluating such increases or decreases becomes a matter of calculating the rate of change in frequency between adjacent bins for each repeat, and finding the proportion of repeats in which an increase took place (Crema 2012, 454–456). Again, this can be compared with the fluctuations in frequency seen at the same point in time under a null model. Notably, this kind of rate-of-change analysis cannot be achieved using the single-simulation approach typically employed in the 14C literature.
A second key challenge in chronological synthesis is that of variable archaeological research intensity, which hinders any effort to interpret changes in absolute frequency of a given object type. This is especially true for ecofacts (or artefacts) recovered mainly from wet-sieved sediment samples, as the contexts chosen for sampling – and the samples eventually processed – often reflect perceived importance of specific time periods. In English urban settlements, for example, Roman stratigraphic contexts are more likely to be sampled than those from the 19th century.
It is a well-established principle in zooarchaeology that one cannot talk reliably of absolute changes in taxonomic representation, but only of relative shifts (see Lyman 2008, 13–15). This is due to the seldom-noted compositional nature of faunal data: while fragment counts themselves are technically ‘open’, the absence of any meaningful independent reference scale effectively ‘closes’ the dataset when it comes to interpretation: the frequency of any taxon can only be measured relative to a value of which it is itself a component, typically total NISP. It is thus impossible to say whether the frequency of one taxon has increased or that of another decreased. Nor can correlations between taxonomic frequencies be taken at face value – by default taxa should be correlated positively if raw counts are compared or negatively if percentages are used (see Aitchison 1982).
To move beyond relative changes one requires an effectively independent control variable against which frequencies can be calibrated – ‘opening’ the dataset. If the species to be compared are very rare – collectively making up only a few percent of an assemblage, for example – then overall sample size may suffice for this purpose, though not technically independent of the frequencies to be compared and hence not technically correct. Fish remains, for example, might be calibrated against the frequency of other vertebrate classes. Where data on excavated/analysed volumes of sediment are available, however, an alternative is to replace raw frequency counts with measures of the density of bone finds in deposits. In one prehistoric example, applying this technique to a millennium-long Neolithic midden sequence revealed that a sudden apparent decline in representation of one mammalian taxon was in fact an artefact of a dramatic increase in deposition of another (Russell et al. 2013, 216–218). This approach is most readily applicable where discrete samples of wet-sieved sediment have been processed for environmental remains, limiting recovery biases – for example, density in terms of grams of fish-bone per processed litre has been used to track fluctuations over time in the intensity of fishing in Lake Titicaca (Capriles et al. 2014).
Two things must be borne in mind when taking this approach. First, sediment volume is not technically independent of the frequencies of finds, since those finds contribute to the total volume; find-density data are still technically compositional – analogous, perhaps, to trace elements in ceramic or glass compositional analysis. This has troubling implications for multivariate analyses (see Aitchison et al. 2002; Baxter and Freestone 2006), but becomes a problem for comparing find deposition rates only when the finds in question make up a substantial percentage of the sediment matrix. Bone find-density data are thus of limited value for comparing taxonomic frequencies in extremely bone-rich contexts such as fish middens or Roman urban ‘soup kitchen’ deposits.
Second, one must be clear about the chain of proxies involved: finds-per-unit-volume is used as a proxy for deposition rate, which may in turn be used as a proxy for consumption rate. The Neolithic midden trend noted above may thus indicate an increase in meat consumption, but it might alternatively be caused by changes in depositional practices. This is a serious concern for meta-analyses: while the inclusion of sufficiently large numbers of stratigraphic contexts can be expected to mitigate random variation in deposit types represented, the possibility of systematic changes over time in the underlying depositional practices must be kept in mind.
The density approach is related to a more conservative measure of abundance: ubiquity, commonly used in archaeobotany and occasionally in zooarchaeology (Popper 1988; Wright 2010; McKechnie and Moss 2016; see also Lyman 2008, 114–119). Defined as the proportion of samples, stratigraphic entities, or even sites containing a given taxon, ubiquity is particularly useful for finds categories whose distribution tends to be extremely patchy, in the sense that finds often occur in dense concentrations that would cause instability in results using fully quantitative measures.
The chronology of the Fish Event Horizon in London is explored here via a large fish bone dataset provided by MOLA (Museum of London Archaeology), formerly an amalgamation of the Museum of London’s department of urban archaeology and department of Greater London archaeology, and now the city’s largest archaeological contractor. While it would be desirable in future to expand this dataset to include other contractors, we estimate that it already accounts for approximately 40% of the relevant data from London. Crucially, MOLA have consistently operated a single relational database for all excavations since the 1990s, with some earlier projects added retrospectively. Specialist databases, including zooarchaeology, are fully integrated with tables of sites, phasing, contexts, and sediment samples, forming an extremely valuable source for meta-analyses of ecofactual data from the city (see e.g. Livarda and Orengo 2015, Orton et al. 2014; 2016; Thomas et al. 2013).
A snapshot of the MOLA database was taken in October 2013 and includes 320,797 zooarchaeological specimens recovered from 7270 chronologically phased contexts at 142 sites within the urban core of London. Fish contribute 35,187 specimens, of which 32,315 derive from 1163 wet-sieved bulk sediment samples at 84 sites. The number and overrall density of specimens may appear small compared to prehistoric fish middens or to processing deposits at coastal ‘producer’ sites, for example, but is reasonable for an urban ‘consumer’ site, especially since sampling strategies in the city have rarely specifically targeted fish bones. An important aspect of the MOLA dataset is our ability to incorporate available data on processed sediment samples that did not produce fish remains, bringing the total number of chronologically phased samples to 5955, representing 97,471 litres of wet-sieved sediment.
All London archaeological site archives are ultimately deposited with the Museum of London, in the London Archaeological Archive. The data used in this study includes both archived and currently active (post-excavation) archaeological sites, a number of which are yet to see definitive publication with phasing and interpretations still potentially subject to change. Given this fact – and the commercial nature of the data – it is not possible to publish the full dataset here, but for the sake of reproducibility the records and fields used in this study are included in ‘anonymised’ form within the supplementary information, available at https://doi.org/10.5334/oq.29.s1.
We use this dataset to explore deposition rates of marine and freshwater fish bones across the Fish Event Horizon in London, employing the Monte Carlo simulation approach outlined above (see Figure 2B). As is normal in British urban archaeology, dating is derived from a wide range of sources including artefact typologies, coins, dendrochronology, historically-known construction/destruction events and occasionally radiocarbon. Given the infeasibility of modelling dates from this complex range of sources, we apply the principle of insufficient reason (see above) and sample from uniform probability distributions within the stated date ranges.
We control for variable research effort in three ways:
Each metric has technical limitations, but taken together they give a robust picture of changes in fish bone deposition.
Analysis is conducted in R v.3.2.0 (R Core Team 2015) using the archSeries package (v.0.0.0.9003). Developed by DCO with the present study in mind, archSeries consists of a range of functions for creating and plotting chronological distributions using both simple aoristic and simulation methods, which we hope will be of broader utility within archaeology. For the sake of speed when performing simulations based on large datasets, archSeries makes heavy use of the data.table package (Dowle et al. 2015). At present archSeries only supports uniform date distributions within defined limits, but it may be expanded in future to include, for example, the beta distribution and radiocarbon-based dating. The package is accessible at https://github.com/davidcorton/archSeries. A copy is also included in the supplementary information at https://doi.org/10.5334/oq.29.s1, along with specific code for the analysis presented here.
The overall distribution of fish remains from MOLA sites is shown in Figure 3, using the Monte Carlo simulation approach described above. Peaks are seen in the Roman, Saxon, and high medieval periods, followed by a long tail into the late and post-medieval. To some extent the distribution follows fluctuations in settlement activity in London, with gaps between the Roman city (c. AD 47–410) and Saxon Lundenwic (seventh to mid ninth C AD), and again with the transition to the medieval city at the start of the 10th century. Carrying this logic over to the late and post-medieval periods, however, would suggest that activity in London faded away from about the 13th century, when in reality the city continued to grow, becoming one of the largest urban settlements in the world by the post-medieval period. Other variables are clearly influencing these results, potentially including:
While it is not possible to remove all potential biases, the availability of comprehensive environmental sampling information in the MOLA dataset confers an unusual degree of control over excavation, recovery, and research bias (points 6 and 7 above). Figure 4A shows the aoristic sum of wet-sieved sample volumes, revealing peaks of sampling effort during the Roman, mid-Saxon, and high medieval periods. Sampling a dummy set from within this distribution shows that the observed peaks in fish frequency do coincide with the heavily sampled periods, but that sampling intensity cannot account for the relative size of those peaks (Figure 4B). The discrepancy between the sheer volume of processed sediment from the Roman period and the limited numbers of fish remains recovered therein is particularly striking, but the relative heights of the Saxon and high medieval peaks are also at odds with what would be expected based on sampling intensity alone.
The very wide confidence band for certain periods, particularly the mid-Saxon, become clear when individual simulation runs are plotted lines (Figure 4C): a small number of samples with very large fish bone assemblages are loosely dated to the Saxon period, causing instability in this part of the curve. This effect can be removed by ignoring the number of bones and counting each sample with fish remains just once, in effect adopting a presence vs. absence approach (Figure 4D). Plotted this way, with the number (rather than combined volume) of samples used as the sampling distribution for the dummy set, the underrepresentation of fish in Roman London is less dramatic, the Saxon period more-or-less matches expectations – albeit peaking slightly later than predicted – and the 11th- to 12th-century overrepresentation remains apparent. In addition, a new peak emerges during the 16th to 17th centuries.
Figure 5 plots frequency distributions for marine taxa compared to those that could have been caught in freshwater. This distinction is complicated by the presence of catadromous/anadromous and estuarine species, but taxa have been grouped here following the original Fish Event Horizon papers (Barrett et al. 2004a, 2004b): eel, salmon, and other taxa that potentially migrate between fresh and saltwater are included in ‘freshwater/diadromous’, along with flounder and indeterminate right-sided flatfish that might have been caught in estuarine waters. Based upon total numbers of fish remains (Figure 5A, B), the pattern accords quite clearly with the Fish Event Horizon model: the early medieval (seventh-eighth C) peak consists almost exclusively of freshwater/diadromous fish, while the 11th to 12th-century peak also includes a substantial number of remains from definitively marine taxa.
The availability of sampling data makes it possible directly to calibrate the fish bone results for research effort, by estimating ‘catch’ per wet-sieved litre over time (Figure 5C), as discussed above. Chronological bins with limited sampling intensity – hence smaller samples and less reliable results – are highlighted, and it is notable that the widest confidence ranges generally occur within these bins. Taking only the better-represented periods, the lack of Roman-period fish bones is again striking, and continued near-absence of marine specimens in the eighth century contrasts with much higher levels during a broad high medieval window from the 11th to 14th centuries. There is no immediate evidence for an associated decline in deposition of freshwater/diadromous fish – indeed the median count per litre for this category in the early 11th century is higher than that observed in the eighth century, although the latter is subject to considerable uncertainty. A clear decline in deposition of freshwater/diadromous fish remains is, however, apparent over the three centuries after the initial onset of marine fishing. In other words, the data bear out the Fish Event Horizon model, but not the suggestion that it was driven partly by declining availability of freshwater fish. The paucity of 9th- and 10th-century samples severely limits potential for refining the chronology, however.
A sharp decline in the total frequency of fish recovered per litre from the latter half of the 13th century onwards is puzzling, since we know historically that fish continued to be of considerable economic importance in England (Barrett 2016; Locker 2016; Galloway 2007; Kowaleski 2000; Serjeantson and Woolgar 2006) – indeed this decline coincides with archaeological evidence for the onset of large-scale imports of cod to London (Orton et al. 2014). The most likely explanation involves changes in depositional practices and a decline in the relative representation of pits among sampled contexts (Figure 6). The city’s growth and the development of ward-based refuse collection in the 14th century (Rawcliffe 2013, 137), might have resulted in a smaller proportion of animal remains being deposited within discrete, well-dated features within the urban core – the area in which MOLA has traditionally specialised. It is also notable that the 13th- and 16th-century surges in cod vertebrae reported by Orton et al. (2014, 523) were most apparent in data from sources other than MOLA – although this appears partly to reflect identification-level biases for vertebrae that would not affect the broad categories used here.
The possibility of a shift in the depositional practices represented within the dataset is supported by Figure 5D, in which fishbone frequencies are normed against the combined frequency of other vertebrate classes from wet-sieved samples, rather than against sample volumes. The overall picture is reassuringly similar to Figure 5C, showing a freshwater/diadromous-dominated Saxon period followed by a mixed 11th- to 12th-century assemblage. Normed in this way, however, the post-1250 decline in total fish remains is much less apparent. Taken together with Figure 5C, this indicates that the late medieval drop in fishbones per litre has more to do with the overall quantity of bone within the samples – and therefore with depositional practices and context types – than with the specific contribution of fish.
Figure 7 plots simulated rates of change between bins, comparing the observed frequencies of the two fish categories with dummy sets based on sample volumes and on total NISP of other vertebrate taxa. Trends are plotted at three levels of bin resolution: 50, 100, and 200 years. Starting with marine taxa (Figure 7A–C), an increase fitting the Fish Event Horizon model is apparent in all cases but only emerges clearly from the 95% dummy confidence zone at the 200-year resolution, occurring between the 9th/10th and 11th/12th century bins as expected. At the 50-year resolution an increase in frequency is seen between each of the 10th- and 11th-century bins, but none of these is clearly beyond the dummy zone – suggesting either that the Fish Event Horizon in London took the form of a more gradual increase over much of this period, or that the data are simply not fine-grained enough to reveal its timing at this resolution. When the dummy set is based on fluctuations in abundance of other vertebrate classes (Figure 7D–F) a broadly consistent pattern emerges: once marine taxa emerge in appreciable numbers from the 10th or 11th century, they subsequently track the frequency of other vertebrates relatively closely.
Turning to the freshwater/diadromous category (Figure 7G–I), there is no decrease in frequency coincident with the appearance of marine taxa. Rather, there is a sharp increase between the 10th and 11th centuries (visible at all three resolutions) that is at the upper end of what would be expected based on sampling intensity, and almost perfectly meets expectations based on other vertebrate classes. A subsequent sharp decrease may be significant by comparison to sample volumes, but is very much in line with trends in other classes. The data thus provide little support for the suggestion that the Fish Event Horizon coincided with a decrease in availability of freshwater/diadromous taxa.
The frequency-based, fully quantitative metrics applied thus far have two limitations: occasional dense deposits of bones may distort results – as seen above in Saxon London (Figure 5C) – while inter-taxonomic differences in the number of recoverable elements introduce biases (Wheeler and Jones 1989, 152). Figure 8 plots two measures based upon presence, rather than frequency, of remains in samples. First, the overall ubiquity of freshwater/diadromous and of marine fish by time (Figure 8A) shows a rather different pattern than the frequency-based plots. Leaving aside the poorly-represented bins, there is a substantial increase in the ubiquity of both groups between the 8th and 10th centuries, but also between the earlier and later eighth century. Overall, the two categories track each other very closely, with the median estimate for each curve falling within the 95% confidence interval of the other at all times. If one looks at the typical number of species from each category in a sample, however – effectively calculating mean taxonomic richness per sample within each category – the switch from freshwater/diadromous to marine taxa is again apparent (Figure 8B). Comparing these metrics with the frequency data above, the Fish Event Horizon appears to have entailed more widespread deposition of both fish categories in London, but with the typical quantities of marine specimens increasing and those of freshwater/diadromous specimens decreasing. Again, there is no indication that an overall decline in deposition of the latter group coincided with the increase in marine remains.
A detailed analysis of changes at species level is beyond the scope of this paper, but it is worth briefly unpacking the ‘freshwater/diadromous’ category (Figure 9). The majority of specimens here are migratory, with this subcategory accounting for most of the non-marine fish bone from the 11th and 12th centuries in particular. These are primarily catadromous eels (Anguilla anguilla), while anadromous Atlantic salmon (Salmo salar) are present in very small numbers throughout the sequence rather than showing the marked decline recently noted for medieval Belgium, Netherlands, and northern France and attributed to watermill construction (Lenders et al. 2016). Given the unusually large number of vertebrae in the eel skeleton their importance is likely to be exaggerated to some extent (e.g. Enghoff 1986), but is nonetheless clearly substantial. While it is possible that this trend reflects diadromous taxa being caught at sea, it is more likely (along with the estuarine ‘freshwater/marine’ group) to reflect fisheries in the lower reaches of the Thames, particularly using fixed structures (Galloway 2015). A drop in migratory fish numbers – again mainly eel – into the later twelfth century is more dramatic than that observed for other taxa, meanwhile, and merits more detailed study in future.
This paper set out to assess how suddenly the Fish Event Horizon manifested in London, and whether the increase in marine taxa involved a concomitant absolute decrease in deposition of freshwater and diadromous taxa that might potentially be linked to overexploitation or habitat destruction.
The first aim is hindered by limited data from the 9th and 10th centuries, at least within the MOLA dataset: while there is some indication that frequencies of marine fish were already on the rise in the latter half of the 10th century, this is based on limited samples and uncertain dating and should be treated with caution. By the time London re-emerges as a major urban settlement in the 11th century marine taxa are clearly present, contributing probably a little under half of the total fish remains – consistent with the wider national picture. This appears to be an ongoing trend, with the representation of marine taxa increasing markedly into the 12th century in terms of frequency (Figure 5C–D) and average diversity (Figure 8B), though not of ubiquity (Figure 8A). There is also some sign that both ubiquity and average diversity of marine taxa may have already been increasing by the latter half of the eighth century, although this is not clearly apparent in the frequency data.
Turning to the second aim, our analysis strongly suggests that there was no immediate drop-off in deposition of freshwater/diadromous remains coincident with the Fish Event Horizon: whether normed by sample volumes or by abundance of other vertebrate classes, frequency data show no clear change in deposition of this category between the well-sampled 8th and 11th centuries. Ubiquity, meanwhile, shows an increase in representation of non-marine fish between these windows. It is not until the 12th century that deposition of freshwater/diadromous taxa clearly falls behind that of marine fish, and the extent to which this represents a decline in the former rather than an increase in the latter depends on how the data are normed. Find-density data do indicate a rapid absolute decline in freshwater/diadromous fish from an 11th-century peak through to the late medieval period (Figure 5C), while frequency relative to other classes suggests at most a subtle decline (Figure 5D). In either case, any decline appears to postdate the Fish Event Horizon, and hence cannot be invoked as a cause of that phenomenon: we find no evidence to support the notion that the switch to marine fisheries was driven in part by depletion of freshwater resources.
On the other hand, unpacking the ‘freshwater/diadromous’ category reveals a relative shift towards diadromous species (Figure 9), particularly eel. While we consider it unlikely that this mainly represents marine catches of these species, it does suggest developments in the exploitation of the Thames river system – likely including changes in the relative importance of estuarine fisheries – that would benefit from systematic archaeological study in future. Increasing elite control and regulation of inland fisheries may have been important here after AD 1000 (Hoffmann 1996, 653; Barrett et al. 2004a, 628), as might flooding and environmental change in the Thames estuary in the later medieval period (Galloway 2009; 2013).
Regarding other time periods, our analysis supports Locker’s (2007, 157) observation that fish, and especially marine fish, are less common in Roman Britain than sometimes assumed, despite the partially marine human isotopic signatures noted for this period (Müldner 2013).
Methodologically, we set out to demonstrate techniques for integrating data from stratigraphic entities with varying date limits and chronological resolution into overall time series, and calibrating those time series for research intensity. Our solution to the first problem is straightforward but effective, borrowing as it does from proven approaches in other areas of archaeology. By applying Monte Carlo methods, following Crema (2012), we are able not only to integrate zooarchaeological data from across London’s history, but also to visualise our degree of confidence in the trends that emerge.
Our solution to the second problem is likely to be more contentious. Using sampling intensity to calibrate urban environmental archaeological results has considerable potential, as we believe we have demonstrated here, but also significant limitations. It is unreliable for periods in which the degree of sampling effort is low – although in fairness this hinders any approach to the data, and our method at least reveals such periods clearly. More problematic is the fact that it is vulnerable to changes in depositional practices and in spatial organisation of the settlement vis-à-vis excavation patterns. The latter could be explored further through a combined spatio-temporal approach, although the London fish dataset might not be large enough to support such a study.
When working with relatively rare taxonomic groups, such as the fish in our study, this risk of changing deposit type representation may be mitigated by using combined frequency of other taxa as an alternative control variable alongside sampling intensity. In our case, this comparison helped to reveal a discrepancy in late medieval fish abundance trends that we interpret in terms of the changing nature of depositional contexts sampled, but which might otherwise have been taken to represent a rapid decline in deposition. This additional check is only possible, of course, where all the data derive from the same sampling process, and where this process is unlikely to be biased between the taxa under study and those used as the control – in the case of fish it is thus unlikely to be applicable post-hoc to published assemblages (see Barrett et al. 2004b, 628). Nor is it applicable where the taxa in question are relatively abundant within the overall assemblage, in which case sampled volumes remain the only potential external control on frequencies. While potentially powerful, our catch-per-unit-effort approach should thus be applied with some caution.
Any assessment of trends in taxonomic frequencies at a settlement as large, complex, and frequently excavated as London is inevitably fraught with complications. Nonetheless, by integrating zooarchaeological data from across the city with data on sampling intensity, using a range of innovative approaches and metrics, we have been able to make a significant contribution to understanding of a crucial development in medieval economic and environmental history – the Fish Event Horizon – as manifest in London. Most importantly, we have shown that the marked increase in marine fishing around AD 1000 predates any visible drop-off in freshwater fish consumption, and hence cannot have been driven by depletion of inland fisheries. Rather, our results support the argument that changes were driven by rising overall demand and/or increased supply of marine species.
Finally, the freely available R package developed for this project, archSeries, will enable archaeologists in a wide variety of contexts, both within and beyond urban environmental archaeology, to utilise the methods advocated in this study.
The additional files for this article can be found as follows:
A paper of this kind, built on the data from 84 excavations and 97,471 litres of wet-sieved sediment, would not be possible without the excellent work of hundreds of London’s archaeologists, environmental archaeologists and zooarchaeologists past and present. The support of Museum of London Archaeology in allowing the authors access and permission to use the data was instrumental in the success of this paper, in particular Mary Ruddy, Natasha Powers and David Bowsher. We are also grateful to Kevan Edinborough, Clive Orton, Marko Porčić, Geoff Bailey, an internal review panel at York, and two anonymous peer reviewers for discussion of methods and/or comments on drafts. Open Access publication was funded jointly by the Department of Archaeology, University of York and the School of Forensic and Applied Sciences, UCLan.
The authors have no competing interests to declare.
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